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Brief Summary

History in the United States

Tree-of-heaven was first introduced to America by a gardener in Philadelphia, PA, in 1784, and by 1840 was commonly available from nurseries. The species was also brought into California mainly by the Chinese who came to California during the goldrush in the mid-1800s. Today it is frequently found in abandoned mining sites there. The history of ailanthus in China is as old as the written language of the country.

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U.S. National Park Service Weeds Gone Wild website

Source: U.S. National Park Service

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Simaroubaceae -- Quassia family

    James H. Miller

    Ailanthus (Ailanthus altissima), also called  tree-of-heaven, Chinese sumac, paradise-tree, and copal-tree  (fig. 1), is an introduced species that has become widely  naturalized across the continent. Ailanthus has found an  extremely wide variety of places to establish itself, from urban  areas to reclaimed surface-mined lands. Its successful  reproduction on impoverished soils and in harsh environments  results from its ability to sprout from the roots and to seed  prolifically. Ailanthus is found as an upper-canopy component,  with varying frequency, in the eastern hardwood forests,  apparently spreading by sprouting after harvest disturbance.

  • Burns, Russell M., and Barbara H. Honkala, technical coordinators. 1990. Silvics of North America: 1. Conifers; 2. Hardwoods.   Agriculture Handbook 654 (Supersedes Agriculture Handbook 271,Silvics of Forest Trees of the United States, 1965).   U.S. Department of Agriculture, Forest Service, Washington, DC. vol.2, 877 pp.   http://www.na.fs.fed.us/spfo/pubs/silvics_manual/table_of_contents.htm External link.
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James H. Miller

Source: Silvics of North America

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History in the United States

Also called shumac, stinking sumac, Chinese sumac, and ailanthus, it was introduced by a Pennsylvania gardener in 1748 and was made available commercially by 1840. It gained some notoriety as the species featured in the book “A Tree Grows in Brooklyn,” by Betty Smith.

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Tree-of-heaven (Ailanthus altissima), also known ailanthus, Chinese sumac, and stinking shumac, is a deciduous tree in the mostly tropical Simaroubaceae family. Mature trees can reach 80 feet in height. Ailanthus has smooth stems with pale gray bark and twigs which are light chestnut brown, especially in the dormant season. Its large compound leaves are 1-4 feet in length, alternate, and composed of 10-41 smaller leaflets. Each leaflet has one or more glandular teeth along the lower margin. The leaf margins are otherwise entire or lacking teeth. Ailanthus is a dioecious (“two houses”) plant meaning that male and female flowers occur on separate plants. Flowers occur in large terminal clusters and are small and pale yellow to greenish. Flat, twisted, winged fruits each containing a single central seed are produced on female trees in late summer to early fall and may remain on the trees for long periods of time. The wood of ailanthus is soft, weak, coarse-grained, and creamy white to light brown in color. All parts of the tree, especially the leaves and flowers, have a nutty or burned nut odor.

Tree-of-heaven is a fast-growing tree and a prolific seeder that can take over sites, replacing native plants and forming dense thickets. Ailanthus also produces chemicals that prevent the establishment of other plant species nearby. Its root system may be extensive and has been known to cause damage to sewers and foundations.

Tree-of-heaven is a common tree in disturbed urban areas, where it sprouts up just about anywhere, including alleys, sidewalks, parking lots, and streets. For example, the book “A Tree Grows in Brooklyn,” by Betty Smith, is based on the tree-of-heaven. Away from cities, ailanthus is commonly seen in fields, and along roadsides, fencerows, woodland edges and forest openings. It occurs as seedlings that pop up by the hundreds in recently planted fields and as persistent thickets in rocky, untillable areas. In the United States, ailanthus is recognized to be a serious agricultural pest.

NOTE: It is important not to confuse native shrubs and trees with ailanthus. Native sumacs (Rhus) and trees like ash (Fraxinus), hickory (Carya), black walnut, butternut and pecan (Juglans) can be distinguished from tree-of-heaven by having completely serrated (toothed) leaf margins.

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Supplier: Bob Corrigan

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Comprehensive Description

Description

This tree is 40-80' at maturity, forming either single or multiple trunks and a relatively open ovoid crown on each trunk. Trunk bark is mottled light and dark gray; it has weak furrows and ridges that are irregular and fragmented. Branch bark is light gray with abundant lenticels (air pores), while young shoots are yellowish brown to green, relatively stout, and usually glabrous (sometimes temporarily pubescent). Alternate compound leaves about 1-3' long occur along the shoots; they are odd-pinnate (less often even-pinnate) with 11-35 leaflets. Individual leaflets are 3-6" long and 1-2" across; they are lanceolate with smooth margins, except near the base, where 1-2 pairs of blunt dentate teeth usually occur. The upper leaflet surface is dark green and glabrous, while the lower surface is pale to medium green and glabrous (or nearly so). The short petiolules (basal stalklets) of the leaflets are up to ½" in length. The petioles of the compound leaves are 3-6" long; their bases are swollen. Both the rachises and petioles are light green to red and glabrous (or nearly so). The crushed foliage of this tree has an odd scent, resembling a mixture of citrus and skunk-like odors. Tree-of-Heaven is dioecious, producing either all male (staminate) flowers or all female (pistillate) flowers on the same tree. These greenish yellow flowers are produced in panicles about 4-12" long. Male flowers are up to 1/3" across, consisting of a short calyx with 5 lobes, 5 narrow petals, and 10 fertile stamens. Female flowers are up to 1/3" across, consisting of a short calyx with 5 lobes, 5 narrow petals, 10 pseudo-stamens that are sterile, and 5 carpels with united styles. The male flowers, in particular, exude an unpleasant skunk-like odor. The blooming period occurs during mid- to late spring. While the male flowers wither away, the female flowers are replaced by single-seeded samaras that mature during the late summer or fall. Individual samaras are about 1½" long and 1/3" across; they are initially light green, but later become yellowish or reddish green, and finally become tan to brown. Each samara has two elongated membranous wings and a central seed; the wings are often slightly twisted. Individual seeds are about ¼" long, ovoid, and slightly flattened. The samaras are distributed by the wind or water. The root system is wide-spreading and relatively shallow; vegetative offshoots are sometimes produced from long underground runners.
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© John Hilty

Source: Illinois Wildflowers

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Distribution

Range and Habitat in Illinois

The non-native Tree-of-Heaven is native to China. It was introduced into the United States as an easy-to-grow landscape tree. It is occasional to locally common in most areas of Illinois, except the NW section of the state, where it is apparently uncommon (see Distribution Map). This tree is invasive and it is undoubtedly still spreading into new areas. Habitats include woodland edges and openings, thickets, riverbanks, vacant lots, landfills and dumps, gravelly back alleys, areas along roads and railways, fence rows, and urban waste areas. This tree is more common in urban areas than rural or natural areas; it is especially common in impoverished and poorly maintained areas of cities, where it is sometimes cultivated as a yard tree. Tree-of-Heaven is a pioneer species that prefers areas with a history of disturbance.
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© John Hilty

Source: Illinois Wildflowers

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National Distribution

Canada

Origin: Exotic

Regularity: Regularly occurring

Currently: Unknown/Undetermined

Confidence: Confident

United States

Origin: Exotic

Regularity: Regularly occurring

Currently: Unknown/Undetermined

Confidence: Confident

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© NatureServe

Source: NatureServe

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Global Range: Native to central China and widely planted, it now occurs in practically every state of the U.S. and from Canada to Argentina, and is also escaped in Europe. Distribution and abundance in native range not known.

The frequency of Ailanthus occurrences increases as one nears the cities. In neglected urban areas, Ailanthus grows "as trees close to buildings, as hedges, or as bushy aggregates along railroad tracks, highway embankments".

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© NatureServe

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More info for the term: mesic

Tree-of-heaven is native to Taiwan and central China, where it occurs from 22o to 34o N in latitude [304]. It is nonnative in North America, where it is distributed from British Columbia, southern Ontario and Quebec, and Maine south to Florida, Texas, southern California, and Mexico [105,158,208,297,328]. Tree-of-heaven spread in North America apparently followed 3 introductions from China. It was 1st imported to Pennsylvania in 1784 as an ornamental [71,93,139,287,288,312]. A 2nd introduction occurred in New York in 1820, where tree-of-heaven was again planted as an ornamental [62]. Both eastern introductions were from English stock imported from China. Tree-of-heaven was commercially available in eastern nurseries by 1840. The 3rd introduction was in California during the Gold Rush of the mid-1800s. Chinese immigrating to work in the gold fields and in construction of the transcontinental railroad brought tree-of-heaven to California, probably because of the tree's medicinal and cultural importance in their homeland (see Other Uses) [139,288]. Tree-of-heaven was first planted in Hawaii in 1924 [321]. Plants database provides a map of tree-of-heaven's distribution in the United States.

A century after the North American introductions, tree-of-heaven is still most common in its initial centers of distribution: the Northeast and California. In the eastern United States, it is most invasive from New England south to the mid-Atlantic states [93,233]. Tree-of-heaven is frequently found in the upper Midwest. It is weakly invasive in the middle and southern Great Plains [114,258]. It is uncommon south of North Carolina in the Southeast and in the South [82,233,324], but it is spreading in the South. By a 2008 estimate, tree-of-heaven was present in over 214,000 acres (86,600 ha) of southern forests [208]. In the West, tree-of-heaven is common throughout much of California and is locally common in Oregon and Washington [93,137]. In California, it is invasive in the Bay Area, the Central Valley, and in foothill counties with a history of gold mining [139,153]. It grows along waterways in the Pacific Northwest, including banks of the Snake and Columbia rivers [137]. In the Southwest it invades riparian zones and mesic canyons [287].

Tree-of-heaven has established in temperate climates throughout the world. Its earliest introductions may have been in Japan and Korea, where it is probably not native [191]. It was introduced in Europe in the 1700s and has become widespread there [86,163,288]. Using seed from European trees, introductions in Argentina, Australia, and Africa followed [139,140]. Kowarik [172] views human settlements as centers of distribution for tree-of-heaven, with roads providing the migration routes.

  • 105. Godfrey, Robert K. 1988. Trees, shrubs, and woody vines of northern Florida and adjacent Georgia and Alabama. Athens, GA: The University of Georgia Press. 734 p. [10239]
  • 114. Great Plains Flora Association. 1986. Flora of the Great Plains. Lawrence, KS: University Press of Kansas. 1392 p. [1603]
  • 137. Hitchcock, C. Leo; Cronquist, Arthur; Ownbey, Marion; Thompson, J. W. 1961. Vascular plants of the Pacific Northwest. Part 3: Saxifragaceae to Ericaceae. Seattle, WA: University of Washington Press. 614 p. [1167]
  • 139. Hoshovsky, Marc C. 1988. Element stewardship abstract: Ailanthus altissima--Tree-of-heaven, [Online]. In: Managment library--plants. In: The global invasive species team (GIST). Arlington, VA: The Nature Conservancy (Producer). Available: http://tncweeds.ucdavis.edu/esadocs/documnts/ailaalt.html [2010, November 9]. [46265]
  • 140. Hu, Shiu Ying. 1979. Ailanthus. Arnoldia. 39(2): 29-50. [45755]
  • 153. Jepson, Willis Linn. 1925. A manual of the flowering plants of California. Berkeley, CA: University of California Press. 1238 p. [19365]
  • 158. Kartesz, John T. 1999. A synonymized checklist and atlas with biological attributes for the vascular flora of the United States, Canada, and Greenland. 1st ed. In: Kartesz, John T.; Meacham, Christopher A. Synthesis of the North American flora (Windows Version 1.0), [CD-ROM]. Chapel Hill, NC: North Carolina Botanical Garden (Producer). In cooperation with: The Nature Conservancy; U.S. Department of Agriculture, Natural Resources Conservation Service; U.S. Department of the Interior, Fish and Wildlife Service. [36715]
  • 163. Kentucky Exotic Pest Plant Council. 2001. Invasive exotic plant list, [Online]. Southeast Exotic Pest Plant Council (Producer). Available: http://www.se-eppc.org/states/KY/KYlists.html [2005, April 13]. [44948]
  • 172. Kowarik, Ingo. 1983. The acclimatization and phytogeographical behavior of the tree of heaven in the French Mediterranean area. Phytocoenologia. 11(3): 389-406. [46757]
  • 191. Little, Elbert L., Jr. 1979. Checklist of United States trees (native and naturalized). Agric. Handb. 541. Washington, DC: U.S. Department of Agriculture, Forest Service. 375 p. [2952]
  • 208. Meloche, Colette; Murphy, Stephen D. 2006. Managing tree-of-heaven (Ailanthus altissima) in parks and protected areas: a case study of Rondeau Provincial Park (Ontario, Canada). Environmental Management. 37(6): 764-772. [63850]
  • 233. Patterson, David T. 1976. The history and distribution of five exotic weeds in North Carolina. Castanea. 41(2): 177-180. [21454]
  • 258. Root, Thomas W. 1985. Addition to the vascular flora of Rock Island County, Illinois. Transactions, Illinois Academy of Science. 78(3-4): 281-284. [37532]
  • 287. Tellman, Barbara. 1997. Exotic pest plant introduction in the American Southwest. Desert Plants. 13(1): 3-10. [27408]
  • 288. Tellman, Barbara. 1998. Stowaways and invited guests: how some exotic plant species reached the American Southwest. In: Tellman, Barbara; Finch, Deborah M.; Edminster, Carl; Hamre, Robert, eds. The future of arid grasslands: identifying issues, seeking solutions: Proceedings; 1996 October 9-13; Tucson, AZ. Proceedings RMRS-P-3. Fort Collins, CO: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 144-149. [29294]
  • 297. U.S. Department of Agriculture, Agricultural Research Service, National Genetic Resources Program. 2010. GRIN taxonomy for plants, [Online]. In: Germplasm Resources Information Network--(GRIN) database. Beltsville, MD: National Germplasm Resources Laboratory (Producer). Available: http://www.ars-grin.gov/cgi-bin/npgs/html/index.pl?language=en [2010, August 27]. [80267]
  • 304. Udvardy, L. 1998. Spreading and coenological circumstances of the tree of heaven (Ailanthus altissima) in Hungary. Acta Botanica Hungarica. 41(1-4): 299-314. [46454]
  • 312. Voss, Edward G. 1985. Michigan flora. Part II. Dicots (Saururaceae--Cornaceae). Bulletin 59. Bloomfield Hills, MI: Cranbrook Institute of Science; Ann Arbor, MI: University of Michigan Herbarium. 724 p. [11472]
  • 321. Woodcock, Deborah. 2003. To restore the watersheds: early twentieth-century tree planting in Hawaii. Annals of the Association of American Geographers. 93(3): 624-635. [75562]
  • 324. Wunderlin, Richard P. 1998. Guide to the vascular plants of Florida. Gainesville, FL: University Press of Florida. 806 p. [28655]
  • 328. Zasada, John C.; Little, Silas. 2008. Ailanthus altissima (P. Mill.) Swingle: ailanthus. In: Bonner, Franklin T., Karrfalt, Robert P., eds. Woody plant seed manual. Agric. Handbook No. 727. Washington, DC: U.S. Department of Agriculture, Forest Service: 224-226. [46269]
  • 62. Davies, P. A. 1942. The history, distribution, and value of Ailanthus in North America. Transactions, Kentucky Academy of Science. 9: 12-14. [45812]
  • 71. Diggs, George M., Jr.; Lipscomb, Barney L.; O'Kennon, Robert J. 1999. Illustrated flora of north-central Texas. Sida Botanical Miscellany, No. 16. Fort Worth, TX: Botanical Research Institute of Texas. 1626 p. [35698]
  • 82. Duncan, Wilbur H.; Duncan, Marion B. 1988. Trees of the southeastern United States. Athens, GA: The University of Georgia Press. 322 p. [12764]
  • 86. Essl, Franz. 2007. From ornamental to detrimental? The incipient invasion of central Europe by Paulownia tomentosa. Preslia. 79(4): 377-389. [72048]
  • 93. Feret, Peter P. 1985. Ailanthus: variation, cultivation, and frustration. Journal of Arboriculture. 11(12): 361-368. [46741]

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Distribution in the United States

Tree-of-heaven is occurs in many states across the continental U.S. and Hawaii and to date has been reported to be invasive in natural areas in 30 states (see map).

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U.S. National Park Service Weeds Gone Wild website

Source: U.S. National Park Service

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Native Range

Central China
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U.S. National Park Service Weeds Gone Wild website

Source: U.S. National Park Service

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Distribution and Habitat in the United States

Tree of heaven is reported to be invasive in natural areas in 30 states across continental U.S. and Hawaii. It is highly adaptable to disturbance and a huge range of soil types and conditions, grows best in full sun and is tolerant of drought.

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Origin

Northeastern and Central China and Taiwan

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All regions of China except Hainan, Heilongjiang, Jilin, Ningxia, Qinghai [widely cultivated and naturalized elsewhere].
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© Missouri Botanical Garden, 4344 Shaw Boulevard, St. Louis, MO, 63110 USA

Source: Missouri Botanical Garden

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Distribution: Native in China, cultivated in temperate and subtropical regions of the world and often naturalized.
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© Missouri Botanical Garden, 4344 Shaw Boulevard, St. Louis, MO, 63110 USA

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Physical Description

Morphology

Description

More info for the terms: density, perfect, ramet, tree

Botanical description: The following description of tree-of-heaven provides characteristics that may be relevant to fire ecology and is not meant for identification. Keys for identification are available (for example, [71,104,105,135,199,317,324]). Billings and others [28] provide a key for identifying tree-of-heaven and other eastern trees in winter.

Tree-of-heaven is deciduous. It may reach 60 to 70 feet (18-21 m) in height, 80 feet (24 m) in crown width, and 20 feet (6 m) in trunk diameter at maturity [8,71,105,308]. The champion tree as of 2010 was in Virginia; it reached 55 feet (17 m) in height, 48 feet (15 m) in spread, and 20 feet in diameter [8]. Tree-of-heaven may be shrubby when suppressed beneath the canopy or pruned regularly [104]. It has smooth, thin bark and a straight bole. Branches are brittle and self-pruning [71,104,105,308]. There are 2 branch types: long and short shoots. Long shoots are sterile and may extend 18 feet (5 m), while short shoots bear flowers and rarely reach more than 18 inches (46 cm) long [63]. The large, malodorous leaves are pinnately compound, with prominent glands on the back of each leaflet. Leaflets range from 15 to 41 in number, and total leaf length may reach 3 feet (1 m) [71,104,105,308]. Leaf stipules have nectaries that excrete sugars [30].

Most flowers are unisexual, but some trees may have perfect flowers [328]. The inflorescence is a 4- to 7-inch (10-20 cm) long panicle with 6- to 8-mm long flowers. Staminate flowers have a strong odor that is objectionable to humans. Fruits are one-seeded, dry schizocarps with wings. They are 1 to 2 inches (2.5-5 cm) long and propeller-shaped, resembling maple (Acer spp.) fruits [71,104,135,136,147,149,250,317]. The fruits grow in clusters; a fruit cluster may contain hundreds of seeds [163]. Seeds average 0.2 × 1.0 inch (0.6 × 0.25 cm) in area [9] and 27 mg in mass [201].

Roots are shallow and wide-spread [211]. Young trees have a taproot and several large lateral roots [230,248,249], although the taproot may diminish with age [211]. Ramets do not have taproots. In dry, rocky soil or beneath pavement, tree-of-heaven grows long, horizontal roots that do not branch until reaching a more favorable substrate [230,248,249]. Roots near the trunk thicken with age, serving as storage organs. Deep roots send out smaller roots that grow near the soil surface; stem shoots generally sprout from these shallow roots. Most roots occur in the upper 18 inches (46 cm) of soil [211].

Stand structure: Tree-of-heaven typically occurs in clumps, although it may form rows along streams, roads, and fences, and occasionally it grows as widely spaced, single stems. Clumping can result from an even-aged seedling establishment or from clonal expansion through root sprouting [249]. Open-grown colonies may eventually become dense by sprouting. Davis [61] observed a half-acre (0.2 ha) stand in Kentucky that had 32 stems. Stands subject to infrequent control measures may develop into even-aged thickets [77,151]. Untreated stands self-thin, so the stand tends to become even-aged over time. Two years after tree-of-heaven harvest in Pennsylvania, density of tree-of-heaven sprouts averaged 17,860 two-year-old sprouts/acre (mean height=9 feet (3 m)), with 10,019 one-year-old sprouts/acre (mean height=2 feet (0.6 m)). After 3 years many of the sprouts had died, so dead stems were more common than live stems [151]. Sprouts volunteering in closed-canopy understories remain suppressed and few in number. For example, Hunter [148] reported scattered, single-stemmed trees-of-heaven—rather than thickets—in the understory of a mixed-evergreen forest in northern California. On the Jefferson National Forest, Virginia, tree-of-heaven had a clumped distribution on low-leave shelterwood sites and a random distribution on clearcuts and high-leave shelterwood sites [47].

 
  Over- and understory trees-of-heaven. Photo © John M. Randall, The Nature Conservancy.

There are few clues as to tree-of-heaven's original growth habit in China, where it is native. As valued ornamentals, mature trees-of-heaven in China are often pruned to aesthetically pleasing, single-stemmed forms, with sprouts harvested for firewood and medicinal uses [140,249].

Life span: Tree-of-heaven is typically short-lived, with life spans ranging from 30 to 70 years [85,163,211]. Cloning from root sprouts can extend ramet life hundreds of years [148]. Sprouts from the first tree-of-heaven in North America, planted in Philadelphia's Bartram Botanical Garden 1784, still existed at the turn of the 21st century [45].

Physiology: Tree-of-heaven has several physiological adaptations that probably aid in its establishment and spread. It appears to be allelopathic [64,184,190,206,209,217]. Chemical extracts from the leaves, bark, roots, and seeds have inhibited germination and growth of other plant species in the laboratory [129,130,131,184]. Allelopathic chemicals (ailanthone and other compounds identified in these sources: [9,10,64,206]) are concentrated in roots and in young trees, with young ramets producing more toxins than older trees [129,184].

Open-grown trees-of-heaven are highly efficient at photosynthesis [30,33,34,122,194,207] and store large quantities of photosynthate in stems and roots [30,33,34,194,207]. Foliar nectaries excrete photosynthates during growth and flower initiation [31]. A study in a Mediterranean region of Spain found that even after 5 years of once- or twice-yearly cuttings, leaves from new tree-of-heaven sprouts showed higher rates of stomatal conductance in spring than leaves of uncut trees-of-heaven. The authors conjectured that regulating stomatal conductance helps sprouting trees-of-heaven grow quickly [54].

Tree-of-heaven is drought tolerant [87]. In Nava-Constan and others' [54] experiment in Spain, trees-of-heaven showed more positive leaf water potentials than native flowering ashes (Fraxinus ornus). Conflicting information states tree-of-heaven is intolerant [108] or tolerant [18,87] of flooding. Further observations and field studies are needed to resolve this conflict.

Tree-of-heaven is highly tolerant of most industrial pollutants [207,253], although it is sensitive to ozone pollution [111]. In a highly polluted area of Armenia, tree-of-heaven showed the least damage and best growth of 8 urban tree species (Derojan 1958 cited in [93]).

  • 10. Ansari, S. H.; Ali, M. 2003. Two new phytosterols from Ailanthus altissima (Mill) Swingle. In: Bernath, J.; Szoke, E.; Mathe, I.; Blunden, G.; Kery, A., eds. Proceedings, international conference on medicinal and aromatic plants (Part II); 2001 July 8-11; Budapest, Hungary. In: Acta Horticulture. Leuven, Belgium: International Society for Horticultural Science; 597: 91-94. [46145]
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  • 108. Gonzalez, Lisa; Christoffersen, Bradley, eds. 2007. The quiet invasion: a guide to invasive plants of the Galveston Bay area, [Online]. The Woodlands, TX: Houston Advanced Research Center (Producer). In cooperation with: Texas Commission on Environmental Quality, Galveston Bay Estuary Program, Houston, TX; U.S. Environmental Protection Agency, Washington, DC. Available: http://www.galvbayinvasives.org/ [2009, October 16]. [75947]
  • 111. Gravano, Elisabetta; Giulietti, Valentina; Desotgiu, Rosanna; Bussotti, Filippo; Grossoni, Paolo; Gerosa, Giacomo; Tani, Corrado. 2003. Foliar response of an Ailanthus altissima clone in two sites with different levels of ozone-pollution. Environmental Pollution. 121(1): 137-148. [46737]
  • 122. Hammerlynck, E. P. 2001. Chlorophyll fluorescense and photosynthetic gas exchange responses to irradiance of tree of heaven (Ailanthus altissima) in contrasting urban environments. Photosynthetica. 39(1): 25-50. [79905]
  • 129. Heisey, Rod M. 1990. Allelopathic and herbicidal effects of extracts from tree of heaven (Ailanthus altissima). American Journal of Botany. 77(5): 662-670. [45477]
  • 130. Heisey, Rod M. 1990. Evidence for allelopathy by tree-of-heaven. Journal of Chemical Ecology. 16(6): 2039-2055. [45481]
  • 131. Heisey, Rod M. 1996. Identification of an allelopathic compound from Ailanthus altissima (Simaroubaceae) and characterization of its herbicidal activity. American Journal of Botany. 83(2): 192-200. [45475]
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  • 140. Hu, Shiu Ying. 1979. Ailanthus. Arnoldia. 39(2): 29-50. [45755]
  • 147. Hunter, Carl G. 1989. Trees, shrubs, and vines of Arkansas. Little Rock, AR: The Ozark Society Foundation. 207 p. [21266]
  • 148. Hunter, John C. 1995. Ailanthus altissima (Miller) Swingle: its biology and recent history. California Exotic Pest Plant Council News. 3(4): 4-5. [45846]
  • 149. Hunter, John. 2000. Ailanthus altissima (Miller) Swingle. In: Bossard, Carla C.; Randall, John M.; Hoshovsky, Marc C., eds. Invasive plants of California's wildlands. Berkeley, CA: University of California Press: 32-36. [46752]
  • 151. Illick, Joseph S.; Brouse, E. F. 1926. The ailanthus tree in Pennsylvania. Bulletin 38. Harrisburg, PA: Pennsylvania Department of Forests and Waters. 29 p. [46734]
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  • 206. McFarland, Lisa. 1996. Isolation and characterization of seed germination inhibitors from Ailanthus altissima. Orono, ME: University of Maine. 214 p. Thesis. [45752]
  • 207. McTavish, Hugh. 1988. A demonstration of photosynthetic state transitions in nature: Shading by photosynthetic tissue causes conversion to state 1. Photosynthesis Research. 17(3): 247-254. [46141]
  • 209. Mergen, Francois. 1959. A toxic principle in the leaves of ailanthus. Botanical Gazette. 121(1): 32-36. [45478]
  • 211. Miller, James H. 1990. Ailanthus altissima (Mill.) Swingle ailanthus. In: Burns, Russell M.; Honkala, Barbara H., tech. coords. Silvics of North America: Vol. 2. Hardwoods. Agriculture Handbook 654. Washington, DC: U.S. Department of Agriculture, Forest Service: 101-104. [46753]
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  • 230. Pan, Elizabeth; Bassuk, Nina. 1985. Effects of soil type and compaction on the growth of Ailanthus altissima seedlings. Journal of Environmental Horticulture. 3(4): 158-162. [45476]
  • 248. Rabe, Elizabeth P.; Bassuk, Nina. 1984. Adaptation of Ailanthus altissima to the urban environment through analysis of habitat usage and growth response to soil compaction. Hortscience. 19(3): 572. [Abstract]. [45852]
  • 249. Rabe, Elizabeth Pan. 1985. Distribution and growth response of Ailanthus altissima in the urban environment. Ithaca, NY: Cornell University. 87 p. Thesis. [45753]
  • 250. Radford, Albert E.; Ahles, Harry E.; Bell, C. Ritchie. 1968. Manual of the vascular flora of the Carolinas. Chapel Hill, NC: The University of North Carolina Press. 1183 p. [7606]
  • 253. Rank, B. 1997. Oxidative stress response and photosystem 2 efficiency in trees of urban areas. Phytosynthetica. 33(3-4): 467-481. [45848]
  • 28. Billings, W. D.; Cain, S. A.; Drew, W. B. 1937. Winter key to the trees of eastern Tennessee. The Journal of the Southern Appalachian Botanical Club. 2(3): 29-44. [79793]
  • 30. Bory, G.; Clair-Maczulajtys, D. 1980. Production, dissemination, and polymorphism of seeds in Ailanthus altissima (Mill.) Swingle, Simaroubaceae. Revue Gererale de Botanique. 88(1049/1051): 297-311. [45847]
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  • 31. Bory, G.; Clair-Maczulajtys, Danielle. 1986. Composition of nectar and role of extrafloral nectaries in Ailanthus glandulosa. Canadian Journal of Botany. 64(1): 247-253. [46147]
  • 317. Welsh, Stanley L.; Atwood, N. Duane; Goodrich, Sherel; Higgins, Larry C., eds. 1987. A Utah flora. The Great Basin Naturalist Memoir No. 9. Provo, UT: Brigham Young University. 894 p. [2944]
  • 324. Wunderlin, Richard P. 1998. Guide to the vascular plants of Florida. Gainesville, FL: University Press of Florida. 806 p. [28655]
  • 328. Zasada, John C.; Little, Silas. 2008. Ailanthus altissima (P. Mill.) Swingle: ailanthus. In: Bonner, Franklin T., Karrfalt, Robert P., eds. Woody plant seed manual. Agric. Handbook No. 727. Washington, DC: U.S. Department of Agriculture, Forest Service: 224-226. [46269]
  • 33. Bourdeau, Philippe F. 1958. Photosynthetic behavior of sun- and shade-grown leaves in certain tolerant and intolerant tree species. Bulletin of the Ecological Society of America. 39(3): 84. Abstract. [46134]
  • 34. Bourdeau, Philippe F.; Laverick, Miriam L. 1958. Tolerance and photosynthetic adaptability to light intensity in white pine, red pine, hemlock and ailanthus seedlings. Forest Science. 4(3): 196-207. [46152]
  • 45. Call, Lara J. 2002. Analysis of intraspecific and interspecific interactions between the invasive exotic tree-of-heaven (Ailanthus altissima (Miller) Swingle) and the native black locust (Robinia pseudoacacia L.). Blacksburg, VA: Virginia Polytechnic Institute. 80 p. Thesis. [45299]
  • 47. Call, Lara J.; Nilsen, Erik T. 2005. Analysis of interactions between the invasive tree-of-heaven (Ailanthus altissima) and the native black locust (Robinia pseudoacacia). Plant Ecology. 176: 275-285. [54325]
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Description

Tree-of-heaven, also known ailanthus, Chinese sumac, and stinking shumac, is a deciduous tree in the mostly tropical quassia family. Mature trees can reach 80 feet in height. Ailanthus has smooth stems with pale gray bark and twigs which are light chestnut brown, especially in the dormant season. Its large compound leaves are 1-4 feet in length, alternate, and composed of 10-41 smaller leaflets. Each leaflet has one or more glandular teeth along the lower margin. The leaf margins are otherwise entire or lacking teeth. Ailanthus is a dioecious (“two houses”) plant meaning that male and female flowers occur on separate plants. Flowers occur in large terminal clusters and are small and pale yellow to greenish. Flat, twisted, winged fruits each containing a single central seed are produced on female trees in late summer to early fall and may remain on the trees for long periods of time. The wood of ailanthus is soft, weak, coarse-grained, and creamy white to light brown in color. All parts of the tree, especially the leaves and flowers, have a nutty or burned nut odor.

Look-alikes: It is important not to confuse native shrubs and trees with ailanthus. Native sumacs (Rhus) and trees like ash (Fraxinus), hickory (Carya), black walnut, butternut and pecan (Juglans) can be distinguished from tree-of-heaven by having completely serrated (toothed) leaf margins.

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U.S. National Park Service Weeds Gone Wild website

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Description and Biology

  • Plant: deciduous tree that can reach 70 ft. in height; twigs with smooth, pale gray bark, and twigs that are light chestnut brown, especially in the dormant season; dioecious meaning plants are either male or female; wood soft, weak, coarse-grained and creamy white to light brown in color; leaves, stems and some flowers have a strong, unpleasant to offensive odor likened to cat urine or rotting peanuts or cashews.
  • Leaves: alternate, large (1-4 ft. long), compound, with 11-25 smaller leaflets, each with one to several glandular teeth near the base.
  • Flowers, fruits and seeds: large showy clusters of small yellowish-green flowers produced during June; in summer, flat, twisted, single-seeded winged fruits or samaras are produced on female trees and may remain on trees for long periods of time; individual trees may produce an estimated 325,000 seeds per year.
  • Spreads: reproduces by seed and by vigorous re-sprouting, especially in response to injury such as breakage or cutting.
  • Look-alikes: compound-leaved shrubs and trees like staghorn sumac (Rhus typhina), ash (Fraxinus sp.), black walnut (Juglans nigra), and hickory (Carya sp.). Sumac has fuzzy, reddish-brown stems and leaves; ash species have opposite leaves; ash, black walnut, hickory and sumac leaf margins are completely to mostly toothed; black walnuts have large green fruits.

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Description

Trees, deciduous, up to 20 m tall; bark smooth and straightly grained. Branches with pith, yellow or yellow-brown pubescent when young, then glabrescent. Leaves odd-pinnate, 40-60 cm; petiole 7-13 cm; leaflets 13-27, opposite or nearly so; blades ovate-lanceolate, abaxially dark green, adaxially gray-green, smelly when rubbed. Panicles 10-30 cm. Flowers light green; pedicel 1-2.5 mm. Sepals 5, imbricate, 0.5-1 mm. Petals 5, 2-2.5 mm, base hispid. Stamens 10; filaments densely hispid basally, longer than petals in males, shorter than petals in females; anthers oblong, ca. 1 mm. Carpels 5; styles connate; stigmas 5-lobed. Samarium oblong, 3-4.5 × 1-1.2 cm. Seed in middle of wing, flat-globose. Fl. Apr-May, fr. Aug-Oct.
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© Missouri Botanical Garden, 4344 Shaw Boulevard, St. Louis, MO, 63110 USA

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Description

A large polygamous tree, upto 30 m high or more. Leaves large, 30-40 cm or more long. Leaflets upto 12 cm long, 2.5-4 cm broad, alternate, ovate-lanceolate, usually cordate at base, glabrous except the veins and midrib near the base, with 2-4 coarse teeth, each with a large gland beneath, margin almost entire. Petiolules 2-10 mm long; midrib prominent. Inflorescence panicle, 10-30 cm long. Bracts minute. Flowers c. 7.0 mm across. Calyx 5-lobed, unequal, sepals much smaller than petals, c. 1 mm long and 0.5 mm broad, valvate, joined at the base, margin serrulate, glabrous, ovate, acuminate. Petals spreading, c.3 x 1.5 mm, glabrous, hairy at the base. Staminate flower with 10 stamens, filaments c. 3 mm long, arising from the base of small 10- lobed disc; anthers 2-celled, dehiscing longitudinally. Pistillate flower: ovary deeply divided, ovule solitary in each cell. Fruit samara, 3.5-5 cm long, twisted at the top, light reddish brown.
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Ecology

Habitat

Range and Habitat in Illinois

The non-native Tree-of-Heaven is native to China. It was introduced into the United States as an easy-to-grow landscape tree. It is occasional to locally common in most areas of Illinois, except the NW section of the state, where it is apparently uncommon (see Distribution Map). This tree is invasive and it is undoubtedly still spreading into new areas. Habitats include woodland edges and openings, thickets, riverbanks, vacant lots, landfills and dumps, gravelly back alleys, areas along roads and railways, fence rows, and urban waste areas. This tree is more common in urban areas than rural or natural areas; it is especially common in impoverished and poorly maintained areas of cities, where it is sometimes cultivated as a yard tree. Tree-of-Heaven is a pioneer species that prefers areas with a history of disturbance.
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Comments: Ailanthus is native to central China, where its history is as old as the written language of the country (Hu 1979). Little information is available on its ecology in China, although Hu (1979) reviews its cultural importance and value for wood products and medicine.

The species was apparently introduced into America by two different routes. The first route began with Pierre d'Incarville mistaking it for the lacquer tree in China and sending seeds to England around 1751 (Feret and Bryant 1974, Hu 1979). It was then introduced to America by a Philadelphia gardener in 1784 (Hu 1979). Because of its rapid growth and ability to grow in unfavorable conditions with little care, it became a common stock in eastern nurseries by 1840. The second route was through Chinese miners. During the days of the California gold rush, many Chinese miners brought ailanthus seeds with them as they settled in California, probably because of its medicinal and cultural importance to them.

Escaping from cultivation and quickly becoming established on both coasts, ailanthus has expanded its range considerably since its initial introductions. Specimens from the Harvard University Herbarium indicate that it "runs wild from Massachusetts...to Oregon ... and from Toronto, Canada ... to Argentina ..." (Hu 1979). In some localities ailanthus is so well established that it appears to be a part of the native flora (Little 1974).

In the eastern United States, the frequency of ailanthus occurrences increases as one nears the cities. In neglected urban areas, ailanthus grows "as trees close to buildings, as hedges, or as bushy aggregates along railroad tracks, highway embankments, walls at the ends of bridges and overpasses, or in cracks of sidewalks and along fences" (Hu 1979). Although it is usually found in disturbed areas, it occasionally spreads to undisturbed areas. Kowarik (1983) views human settlements as centers of its distribution and roads as migration routes.

In California ailanthus is widely naturalized in cismontane areas, especially around old dwellings and mining settlements (Munz and Keck 1973). It has become established in Pleasants Valley, Solano and Marin counties, Berkeley, Vacaville, Petaluma, San Andreas, Angel's Camp, Columbia, and in various places in the Sacramento Valley (Robbins et al. 1951).

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Habitat characteristics

More info for the terms: alliance, cover, density, frequency, importance value, presence, reclamation, relative density, tree

Tree-of-heaven occurs on a variety of sites in North America, ranging from very poor to very productive. In Ithaca, New York, it was positively correlated with urban sites where rooting space was limited and other species could not establish (P=0.05) [230,248]. In contrast, soils in the Central Valley of California, where tree-of-heaven is also common, are nutrient-rich and productive [128]. Little information is available on tree-of-heaven's original habitats in China; it is common there as a cultivated tree [139,140,249].

Tree-of-heaven has been characterized as "the most adaptable and pollution tolerant tree available" for urban plantings [74]. Highly tolerant of industrial gases, dust, and smoke, it is common on disturbed urban sites, especially alleyways, roadsides, and fence rows [71,105,114,214,324]. It is generally more common in urban, suburban, and rural than wild environments [57,181]. In wildlands, tree-of-heaven occurs on floodplains and other disturbed sites, riparian areas, open woodlands and forests, and rock outcrops [41,114,137,164,280,312]. After Hurricane Camille, tree-of-heaven was positively associated with debris avalanche chutes in Virginia [145]. It was most frequent on roadsides in an oak-hickory forest in West Virginia [141]:

Tree-of-heaven frequency on different sites within a West Virginian oak-hickory forest [141]
Habitat Frequency (%)
roadsides 26
streams 19
mature forest 13
open forest 7
railroad rights-of-way 6
residential 6
trails 3
old fields 0
other 20

Tree-of-heaven has invaded rare sugar maple-sweet birch (Betula lenta) rock outcrop communities in High Mountain Park Preserve, New Jersey [76]. In the Southwest, it invades canyons, arroyos, and riparian zones, including the banks of the Rio Grande [6,203].

Soils and topography: Tree-of-heaven tolerates a wide range of soil moisture conditions [82,211]. In oak-hickory woodland of Sussex County, New Jersey, it grows in permanently swampy, ridgebottom soils of an abandoned Boy Scout camp [18]. At the other extreme, tree-of-heaven tolerates dry, rocky soils and extended drought, aided by its large, water-storing roots. Even seedlings show drought tolerance, often volunteering in pavement cracks and other dry sites [113,293]. In Kansas, mature trees-of-heaven and eastern redcedars showed better survivorship during the "Dust Bowl" drought of 1934 than associated tree species [278].

Tree-of-heaven also tolerates a wide range of soil nutrient levels and other soil conditions. Best growth occurs on nutrient-rich, loamy soils, but tree-of-heaven establishes in nutrient-poor soils [93,163,211,328]. Tree-of-heaven tolerates all soil textures [216]. It often establishes on disturbed sites lacking topsoil [164]. In the Appalachians and the Northeast, the tree-of-heaven alliance occurs on limestone clifftops and on calcareous soils [223,237]. On reclamation sites, trees-of-heaven tolerated acid mine spoils better than calcareous spoils and grew on low-phosphorus soils [211]. Tree-of-heaven can grow on soils as low as 4.1 pH, in soluble salt concentrations of 0.25 mmhos/cm, and in soils with phosphorus levels as low as 1.8 ppm [245]. In a mixed-deciduous forest on Staten Island, New York, tree-of-heaven had the highest importance value and relative density of all tree species on neutral soils but was absent on acidic soils (pH ≤5.1) [186]. It tolerates compacted soils [230].

Topography on tree-of-heaven sites may be flat, rolling, or very steep, with tree-of-heaven potentially occurring on all aspects. Tree-of-heaven's spreading root system permits establishment and growth on steep inclines and cliff faces [7]. In Massachusetts, tree-of-heaven is reported on upland, interior wetland, and coastal areas [200]. On the floodplain of the Raitan River, New Jersey, tree-of-heaven was not important on low floodplains (<11 feet (3.3 m) above sea level), but it ranked in the top one-third of species' importance values on upper floodplains [101]. In a slippery elm-white ash woodlot in Ohio, tree-of-heaven presence on forest-roadside edges was similar on north- and south-facing exposures [85]. In Inwood Hill Park, a mixed-hardwood wildland site in Manhattan, tree-of-heaven was most common on west-facing ridges [98]:

Density of tree-of-heaven seedlings and saplings in a wildland park in New York City [98]
  Seedlings (<2 cm DBH) Saplings (2-10 cm DBH)
Valley forest 55 9
East ridge 113 38
Ridgetops 0 50
West ridge 363 211

Climate: Tree-of-heaven is most common in temperate climates, in both North America and its native China. It tolerates minimum temperatures of -38 °F (-39 °C) and maximum temperatures of 110 °F (45 °C). Mean annual precipitation ranges from 0.55 to 158 inches (14-4,010 mm) across tree-of-heaven's North American and Chinese distributions. Tree-of-heaven tolerates drought of several month's duration [3].

Climate within tree-of-heaven's North American distribution ranges from subtropical and wet in Florida; arid in the Great Plains and western United States; to cold and wet in the Northeast. It occurs in USDA hardiness zones 4 to 8 [144]. Annual mean maximum and minimum temperatures within its North American range are 15o F and 97 oF (-9 oC and 36 oC). It tolerates as much as 90 inches (2,290 mm) of mean annual precipitation in the Appalachian Mountains as little as 14 inches (360 mm) of annual precipitation and 8 months of drought in the western United States. Large, water-storing roots confer drought tolerance [140], although tree-of-heaven may not reach maximum growth on dry sites. On an "extremely dry" site on the George Washington National Forest, Pomp [247] observed that trees-of-heaven in an oak-pine forest only reached the canopy in riparian areas and on logged sites. Because seedlings are not cold resistant, extreme cold and prolonged snow cover restrict its occurrence to lower slopes in mountainous regions. Tree-of-heaven may be able to colonize in cold regions that experience several successive years of mild climate [211]. It is the only species in its genus that tolerates cold climates [140].

Elevation: Tree-of-heaven is reported from the following elevations in the western United States:

Elevational range of tree-of-heaven in 3 western states
State Elevation
California <6,600 feet [135,149]
New Mexico 4,500-7,000 feet [199]
Utah 790-5,900 feet [317]

It grows from 4,900 to 5,900 feet (1,500-1,800 m) elevation in China [304].

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  • 223. NatureServe. 2004. International Ecological Classification Standard: terrestrial ecological classifications--National Forests of Arkansas (Ouchita, Ozark, St. Francis) final report, [Online]. Subset of NatureServe central databases. 196 p. In: Publications--library. Arlington, VA: NatureServe (Producer). Available: http://www.natureserve.org/library/arNF.pdf [2010, October 19]. [79606]
  • 230. Pan, Elizabeth; Bassuk, Nina. 1985. Effects of soil type and compaction on the growth of Ailanthus altissima seedlings. Journal of Environmental Horticulture. 3(4): 158-162. [45476]
  • 237. Patterson, Karen D. 2008. Vegetation classification and mapping at Petersburg National Battlefield, Virginia. Technical Report NPS/NER/NRTR--2008/127. Philadelphia, PA: U.S. Department of the Interior, National Park Service, Northeast Region. 235 p. [79673]
  • 245. Plass, William T. 1975. An evaluation of trees and shrubs for planting surface-mine spoils. Res. Pap. NE-317. Upper Darby, PA: U.S. Department of Agriculture, Forest Service, Northeastern Forest Experiment Station. 8 p. [46129]
  • 247. Pomp, Jonathan A. 2008. Disturbances, prescribed fire, and invasion by exotic plants in a xeric mixed-oak and oak-pine dominated area of the ridge and valley in eastern West Virginia. Morgantown, WV: West Virginia University. 173 p. Thesis. [79748]
  • 248. Rabe, Elizabeth P.; Bassuk, Nina. 1984. Adaptation of Ailanthus altissima to the urban environment through analysis of habitat usage and growth response to soil compaction. Hortscience. 19(3): 572. [Abstract]. [45852]
  • 249. Rabe, Elizabeth Pan. 1985. Distribution and growth response of Ailanthus altissima in the urban environment. Ithaca, NY: Cornell University. 87 p. Thesis. [45753]
  • 278. Stiles, Elsa Horn; Melchers, Leo E. 1935. The drought of 1934 and its effect on trees in Kansas. Part I: Meteorological conditions, 1934. Kansas Academy of Sciences. 38: 107-127. [46732]
  • 280. Strausbaugh, P. D.; Core, Earl L. 1977. Flora of West Virginia. 2nd ed. Morgantown, WV: Seneca Books. 1079 p. [23213]
  • 293. Trifilo, P.; Raimondo, F.; Nardini, A.; Lo Gullo, M. A.; Salleo, S. 2004. Drought resistance of Ailanthus altissima: root hydraulics and water relations. Tree Physiology. 24: 107-114. [46736]
  • 3. Albright, Thomas P.; Chen, Hao; Chen, Lijun; Guo, Qinfeng. 2010. The ecological niche and reciprocal prediction of the disjunct distribution of an invasive species: the example of Ailanthus altissima. Biological Invasions. 12(8): 2413-2427. [80211]
  • 304. Udvardy, L. 1998. Spreading and coenological circumstances of the tree of heaven (Ailanthus altissima) in Hungary. Acta Botanica Hungarica. 41(1-4): 299-314. [46454]
  • 312. Voss, Edward G. 1985. Michigan flora. Part II. Dicots (Saururaceae--Cornaceae). Bulletin 59. Bloomfield Hills, MI: Cranbrook Institute of Science; Ann Arbor, MI: University of Michigan Herbarium. 724 p. [11472]
  • 317. Welsh, Stanley L.; Atwood, N. Duane; Goodrich, Sherel; Higgins, Larry C., eds. 1987. A Utah flora. The Great Basin Naturalist Memoir No. 9. Provo, UT: Brigham Young University. 894 p. [2944]
  • 324. Wunderlin, Richard P. 1998. Guide to the vascular plants of Florida. Gainesville, FL: University Press of Florida. 806 p. [28655]
  • 328. Zasada, John C.; Little, Silas. 2008. Ailanthus altissima (P. Mill.) Swingle: ailanthus. In: Bonner, Franklin T., Karrfalt, Robert P., eds. Woody plant seed manual. Agric. Handbook No. 727. Washington, DC: U.S. Department of Agriculture, Forest Service: 224-226. [46269]
  • 41. Bush, Eleanor M. 1976. Vascular flora along the Tygart Valley River near Arden, West Virginia. Castanea. 41(4): 283-308. [73983]
  • 57. Cranfill, Raymond. 1991. Flora of Hardin County, Kentucky. Castanea. 56(4): 228-267. [73952]
  • 6. Allen, Craig Daniel. 1989. Changes in the landscape of the Jemez Mountains, New Mexico. Berkeley, CA: University of California. 346 p. Dissertation. [42116]
  • 7. Almeida, M. T.; Mouga, T.; Barracosa, P. 1994. The weathering ability of higher plants. The case of Ailanthus altissima (Miller) Swingle. International Biodeterioration and Biodegradation. 33(4): 333-343. [45754]
  • 71. Diggs, George M., Jr.; Lipscomb, Barney L.; O'Kennon, Robert J. 1999. Illustrated flora of north-central Texas. Sida Botanical Miscellany, No. 16. Fort Worth, TX: Botanical Research Institute of Texas. 1626 p. [35698]
  • 74. Dirr, Michael A. 1990. Manual of woody landscape plants: their identification, ornamental characteristics, culture, propagation and uses. Champagne, IL: Stipes Publishing Company. 1007 p. [46754]
  • 76. Dodge, Sheridan L. 1997. Successional trends in a mixed oak forest on High Mountain, New Jersey. Journal of the Torrey Botanical Society. 124(4): 312-317. [79792]
  • 82. Duncan, Wilbur H.; Duncan, Marion B. 1988. Trees of the southeastern United States. Athens, GA: The University of Georgia Press. 322 p. [12764]
  • 85. Espenschied-Reilly, Amanada L.; Runkle, James R. 2008. Distribution and changes in abundance of Ailanthus altissima (Miller) Swingle in a southwest Ohio woodlot. Ohio Journal of Science. 108(2): 16-22. [79745]
  • 93. Feret, Peter P. 1985. Ailanthus: variation, cultivation, and frustration. Journal of Arboriculture. 11(12): 361-368. [46741]
  • 98. Fitzgerald, Judith M.; Loeb, Robert E. 2008. Historical ecology of Inwood Hill Park, Manhattan, New York. The Journal of the Torrey Botanical Society. 135(2): 281-293. [72480]

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Key Plant Community Associations

More info for the terms: alliance, codominant, frequency

Tree-of-heaven is most common in urban areas [141]. It varies from a minor to important component of wildland vegetation in its North American range. Because of its scattered and disjunct distribution in North America, tree-of-heaven occurrence is not well documented for all plant communities where
it may occur [211]. The following descriptions are not restrictive, but they include plant communities where tree-of-heaven is a known invader.

In wildlands of the East and Midwest, tree-of-heaven is a common component in oak-hickory (Quercus-Carya spp.) and maple-birch-beech (Acer-Betula-Fagus spp.) forests [286]. It has infested hundreds of acres of oak-hickory forest in Shenandoah National Park, Virginia [195,303]. In eastern oak-hickory forests, tree-of-heaven is frequently associated with native black locust (Robinia pseudoacacia), an early-successional species, and nonnative Norway maple (Acer platanoides) and princesstree (Paulownia tomentosa) [45,46,117,227,249,314]. Other early-seral associates are black cherry (Prunus serotina), gray birch (Betula populifolia), sweetgum (Liquidambar styraciflua), and eastern redcedar (Juniperus virginiana) [117]. In oak-hickory woodlands of Gettysburg National Military Park, Pennsylvania, tree-of-heaven is associated with overstory with black oak (Q. velutina), red oak (Q. rubra), scarlet oak (Q. coccinea), mockernut hickory (C. tomentosa), and bitternut hickory (C. cordiformis). Nonnative invasives other than tree-of-heaven include the understory species Japanese barberry (Berberis thunbergii) and multiflora rose (Rosa multiflora). Late-successional native understory species include white ash (Fraxinus americana), black cherry, sassafras (Sassafras albidum), and boxelder (Acer negundo) [91]. In silver maple (Acer saccharinum)-white oak-red oak forests of Ohio, tree-of-heaven occurs with American elm (Ulmus americana), hickory, black locust, black walnut (Juglans nigra), and black cherry [67]. Tree-of-heaven stands have been observed in estuaries and freshwater marshes on the Atlantic seaboard. Tree-of-heaven dominated the overstory of the estuary at Jug Bay Wetlands Sanctuary, Maryland [164].
On the Georgia piedmont, tree-of-heaven is an important species in early-successional loblolly pine (Pinus taeda)-black oak-white oak forests. Native flowering dogwood (Cornus florida) and yellow-poplar (Liriodendron tulipifera) and nonnative Chinese privet (Ligustrum sinense) and winged elm
(U. alata) are common associated species [55].
Tree-of-heaven is most common in riparian, valley, and foothill communities of California. In riparian areas of southern California, tree-of-heaven frequently associates with Fremont cottonwood (Populus fremontii), California sycamore (Platanus racemosa), mule-fat (Baccharis
salicifolia), and poison-oak (Toxicodendron diversilobum). A 1990 to 1992 survey in Chino Hills State Park showed 15% frequency for tree-of-heaven, with
its geographic range and "vigor" increasing over the study period [162].
Tree-of-heaven is invasive in riparian zones of the Southwest [135,266,273,281]. In the middle Rio Grande Basin of New Mexico, it occurs in Fremont cottonwood-Rio Grande cottonwood-sandbar willow (P. deltoides var. wislizenii-Salix exigua) bosques along with nonnative, invasive Siberian elm (U. pumila) and white mulberry (Morus alba) [97]. Tree-of-heaven has invaded arroyos of the Sandia National Laboratory, New Mexico; nonnative Siberian elm and saltcedar (Tamarix ramosissima) and native Apache plume (Fallugia paradoxa) and fourwing saltbush (Atriplex canescens) are common associated species. On upland sites it occurs in Colorado pinyon-oneseed juniper (Pinus edulis-Juniperus monosperma) stands with Gambel oak (Quercus gambelii) and Siberian elm [203].
The following vegetation classifications describe plant communities in which tree-of-heaven is a dominant or indicator species:
Appalachians and Northeast

  • tree-of-heaven forest alliance.
    Occurs in the Appalachians, the Piedmont, the Interior Low Plateau, eastern Kentucky, the Ozark and Ouachita mountains, and probably other areas in the northeastern
    United States. Common in disturbed areas, along roadsides, urban abandoned lands, and on limestone clifftops [223].
California

  • locally dominant in riparian woodlands [204]
North Carolina

  • dominant and indicator species in edge communities developing on logged sites near oak-loblolly pine forest [205]
Pennsylvania

  • eastern white pine (Pinus strobiformis)-gray birch-tree-of-heaven shale scree slopes in the Delaware Water Gap National Recreation Area [241]

  • occasional codominant in the black cherry-yellow-poplar-red maple (Acer rubrum)-white ash forest alliance of
    Valley Forge National Historical Park [246]

  • modified successional forest at Allegheny Portage Railroad National Historic Site; this forest is dominated by "weedy, early successional
    species" [243]
Tennessee

  • tree-of-heaven forest alliance in Great Smoky Mountains National Park [290]
Virginia

  • successional mixed shrublands on the Petersburg National Battlefield [237] and in Richmond National Battlefield Park; sweetgum may codominate [238]

  • locally dominant on disturbed calcareous forest on the Petersburg National Battlefield [237]

  • successional tree-of-heaven forest in Colonial National Historical Park [236] and Appomattox Court House National Historical Park [234]
  • 117. Greller, Andrew M. 1977. A classification of mature forests on Long Island, New York. Bulletin of the Torrey Botanical Club. 104(4): 376-382. [22020]
  • 135. Hickman, James C., ed. 1993. The Jepson manual: Higher plants of California. Berkeley, CA: University of California Press. 1400 p. [21992]
  • 141. Huebner, Cynthia D. 2003. Vulnerability of oak-dominated forests in West Virginia to invasive exotic plants: temporal and spatial patterns of nine exotic species using herbarium records and land classification data. Castanea. 68(1): 1-14. [46144]
  • 162. Keller, Terry. 1993. Riparian zone plant ecology and hydrology in Aliso Creek, Chino Hills State Park, southern California. In: Keeley, Jon E., ed. Interface between ecology and land development in California: Proceedings of the symposium; 1992 May 1-2; Los Angeles, CA. Los Angeles, CA: The Southern California Academy of Sciences: 137-141. [21702]
  • 164. Kiviat, Eric. 2004. Occurrence of Ailanthus altissima in a Maryland freshwater tidal estuary. Castanea. 69: 139-142. [61224]
  • 195. Marler, Marilyn. 2000. A survey of exotic plants in federal wilderness areas. In: Cole, David N.; McCool, Stephen F.; Borrie, William T.; O'Loughlin, Jennifer, comps. Wilderness science in a time of change conference--Volume 5: wilderness ecosystems, threats, and management; 1999 May 23-27; Missoula, MT. Proceedings RMRS-P-15-VOL-5. Ogden, UT: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 318-327. [40580]
  • 203. McAllister, C.; Beckert, H.; Abrams, C.; Bilyard, G.; Cadwell, K.; Friant, S.; Glantz, C.; Mazaika, R.; Miller, K. 1996. Survey of ecological resources at selected U.S. Department of Energy sites, [Online]. Oak Ridge, TN: U.S. Department of Energy (Producer). Available: http://homer.ornl.gov/oepa/guidance/risk/ecores.pdf [2004, January 21]. On file with: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory, Missoula, MT; FEIS files. [46457]
  • 204. McBride, Joe R. 1994. SRM 203: Riparian woodland. In: Shiflet, Thomas N., ed. Rangeland cover types of the United States. Denver, CO: Society for Range Management: 13-14. [66662]
  • 205. McDonald, Robert I.; Urban, Dean L. 2006. Edge effects on species composition and exotic species abundance in the North Carolina Piedmont. Biological Invasions. 8: 1049-1060. [68821]
  • 211. Miller, James H. 1990. Ailanthus altissima (Mill.) Swingle ailanthus. In: Burns, Russell M.; Honkala, Barbara H., tech. coords. Silvics of North America: Vol. 2. Hardwoods. Agriculture Handbook 654. Washington, DC: U.S. Department of Agriculture, Forest Service: 101-104. [46753]
  • 223. NatureServe. 2004. International Ecological Classification Standard: terrestrial ecological classifications--National Forests of Arkansas (Ouchita, Ozark, St. Francis) final report, [Online]. Subset of NatureServe central databases. 196 p. In: Publications--library. Arlington, VA: NatureServe (Producer). Available: http://www.natureserve.org/library/arNF.pdf [2010, October 19]. [79606]
  • 227. Orians, G. H.. 1986. Site characteristics favoring invasions. In: Mooney, Harold A.; Drake, James A., eds. Ecology of biological invasions of North America and Hawaii. Ecological Studies 58. New York: Springer-Verlag: 133-148. [17513]
  • 234. Patterson, Karen D. 2008. Vegetation classification and mapping at Appomattox Court House National Historical Park, Virginia. Technical Report NPS/NER/NRTR--2008/125. Philadelphia, PA: U.S. Department of the Interior, National Park Service, Northeast Region. 261 p. [78026]
  • 236. Patterson, Karen D. 2008. Vegetation classification and mapping at Colonial National Historical Park, Virginia. Technical Report NPS/NER/NRTR--2008/129. Philadelphia, PA: U.S. Department of the Interior, National Park Service, Northeast Region. 369 p. [79670]
  • 237. Patterson, Karen D. 2008. Vegetation classification and mapping at Petersburg National Battlefield, Virginia. Technical Report NPS/NER/NRTR--2008/127. Philadelphia, PA: U.S. Department of the Interior, National Park Service, Northeast Region. 235 p. [79673]
  • 238. Patterson, Karen D. 2008. Vegetation classification and mapping at Richmond National Battlefield Park, Virginia. Technical Report NPS/NER/NRTR--2008/128. Philadelphia, PA: U.S. Department of the Interior, National Park Service, Northeast Region. 244 p. [79674]
  • 241. Perles, Stephanie J.; Podniesinski, Gregory S.; Eastman, E.; Sneddon, Lesley A.; Gawler, Sue C. 2007. Classification and mapping of vegetation and fire fuel models at Delaware Water Gap National Recreation Area: Volume 1 of 2, [Online]. Technical Report NPS/NER/NRTR2007/076. Philadelphia, PA: U.S. Department of the Interior, National Park Service, Northeast Region, Natural Resource Stewardship and Science. 187 p. Available: http://www.nps.gov/nero/science/FINAL/DEWA_veg_map/DEWA_veg_map.htm [2010, March 3]. [78999]
  • 243. Perles, Stephanie J.; Podniesinski, Gregory S.; Zimmerman, Ephraim A.; Eastman, Elizabeth; Sneddon, Lesley A. 2007. Vegetation classification and mapping at Allegheny Portage Railroad National Historic Site. Technical Report NPS/NER/NRTR--2007/079. Philadelphia, PA: U.S. Department of the Interior, National Park Service, Northeast Region. 156 p. Available online: http://www.nps.gov/nero/science/FINAL/ALPO_finals.htm. [79633]
  • 246. Podniesinski, Gregory S.; Sneddon, Lesley A.; Lundgren, Julie; Devine, Hugh; Slocumb, Bill; Koch, Frank. 2005. Vegetation classification and mapping of Valley Forge National Historical Park. Technical Report NPS/NER/NRTR--2005/028. Philadelphia, PA: U.S. Department of the Interior, National Park Service, Northeast Region. 115 p. Available online: http://biology.usgs.gov/npsveg/vafo/vaforpt.pdf. [79639]
  • 249. Rabe, Elizabeth Pan. 1985. Distribution and growth response of Ailanthus altissima in the urban environment. Ithaca, NY: Cornell University. 87 p. Thesis. [45753]
  • 266. Schwartz, Mark W.; Porter, Daniel J.; Randall, John M.; Lyons, Kelly E. 1996. Impact of nonindigenous plants. In: Status of the Sierra Nevada. Sierra Nevada Ecosystem Project: Final report to Congress. Volume II: Assessments and scientific basis for management options. Wildland Resources Center Report No. 37. Davis, CA: University of California, Centers for Water and Wildland Resources: 1203-1218. [28977]
  • 273. Smith, D. Max; Finch, Deborah M.; Gunning, Christian; Jemison, Roy; Kelly, Jeffrey F. 2009. Post-wildfire recovery of riparian vegetation during a period of water scarcity in the southwestern USA. Fire Ecology--Special Issue. 5(1): 38-55. [79160]
  • 281. Stromberg, Juliet C.; Chew, Matt K. 2002. Foreign visitors in riparian corridors of the American Southwest: Is xenophytophobia justified? In: Tellman, Barbara, ed. Invasive exotic species in the Sonoran region. Arizona-Sonora Desert Museum Studies in Natural History. Tucson, AZ: The University of Arizona Press; The Arizona-Sonora Desert Museum: 195-219. [48665]
  • 286. Tajchman, Stanislaw J.; Fu, Hailiang; Kochenderfer, James N.; Chunshen, Pan. 1995. Spatial characteristics of topography, energy exchange, and forest cover in a central Appalachian watershed. In: Gottschalk, Kurt W.; Fosbroke, Sandra L., eds. Proceedings, 10th central hardwood forest conference; 1995 March 5-8; Morgantown, WV. Gen. Tech. Rep. NE-197. Radnor, PA: U.S. Department of Agriculture, Forest Service, Northeastern Forest Experiment Station: 297-314. [25870]
  • 290. The Nature Conservancy. 1999. Vegetation classification of Great Smoky Mountains National Park (Cades Cove and Mount Le Conte quadrangles). Final report. National Vegetation Classification--Southeastern United States. Arlington, VA: The Nature Conservancy. 195 p. [79665]
  • 303. U.S. Department of the Interior, National Park Service, Shenandoah National Park. 2006. Non-native species, [Online]. In: Nature and science: Environmental factors--nonnative species. Luray, VA: U.S. Department of the Interior, National Park Service, Shenandoah National Park (Producer). Available: http://www.nps.gov/shen/naturescience/nonnativespecies.htm [2010, November 15]. [46456]
  • 314. Wardle, David. A.; Nilsson, Marie-Charlotte; Gallet, Christiane; Zackrisson, Olle. 1998. An ecosystem-level perspective of allelopathy. Biological Reviews of the Cambridge Philosophical Society. 73: 305-319. [80212]
  • 45. Call, Lara J. 2002. Analysis of intraspecific and interspecific interactions between the invasive exotic tree-of-heaven (Ailanthus altissima (Miller) Swingle) and the native black locust (Robinia pseudoacacia L.). Blacksburg, VA: Virginia Polytechnic Institute. 80 p. Thesis. [45299]
  • 46. Call, Lara J.; Nilsen, Erik T. 2003. Analysis of spatial patterns and spatial association between the invasive tree-of-heaven (Ailanthus altissima) and the native black locust (Robinia pseudoacacia). The American Midland Naturalist. 150(1): 1-14. [45002]
  • 55. Cowell, C. Mark. 1993. Environmental gradients in secondary forests of the Georgia Piedmont, U.S.A. Journal of Biogeography. 20: 199-207. [24132]
  • 67. DeMars, Brent G.; Runkle, James R. 1992. Groundlayer vegetation ordination and site-factor analysis of the Wright State University Woods (Greene County, Ohio). Ohio Journal of Science. 92(4): 98-106. [19823]
  • 91. Fairweather, Stephen E.; Cavanaugh, Cecile M. 1990. Identification, restoration, and maintenance of historic woodlots at Gettysburg National Military Park. Tech. Rep. NPS/MAR/NRTR - 90/049. Philadelphia, PA: U.S. Department of the Interior, National Park Service, Mid-Atlantic Region. 123 p. [17985]
  • 97. Finch, Deborah M.; Wolters, Gale L.; Yong, Wang; Mund, Mary J. 1995. Plants, arthropods, and birds of the Rio Grande. In: Finch, Deborah M.; Tainter, Joseph A., eds. Ecology, diversity, and sustainability of the Middle Rio Grande Basin. Gen. Tech. Rep. RM-GTR-268. Fort Collins, CO: U.S. Department of Agriculture, Forest Service, Rocky Mountain Forest and Range Experiment Station: 133-164. [26190]

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Habitat in the United States

Tree-of-heaven is a common tree in disturbed urban areas, where it sprouts up just about anywhere, including alleys, sidewalks, parking lots, and streets. For example, the book “A Tree Grows in Brooklyn,” by Betty Smith, is based on the tree-of-heaven. Away from cities, ailanthus is commonly seen in fields, and along roadsides, fencerows, woodland edges and forest openings. It occurs as seedlings that pop up by the hundreds in recently planted fields and as persistent thickets in rocky, untillable areas. Nationally, ailanthus is recognized to be a serious agricultural pest.

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U.S. National Park Service Weeds Gone Wild website

Source: U.S. National Park Service

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Soils and Topography

Ailanthus grows best in loamy, moist soils but tolerates a wide  range of textures, stoniness, and pH. On the dry end of the  moisture spectrum it is drought hardy, and on the wet end it  cannot tolerate flooding. The species is widely recognized by the  urban populace since it frequently occupies and covers untended  areas in cities. The species' tolerance of harsh sites led to  testing for strip mine reclamation; a study in eastern Kentucky  found ailanthus better adapted to acid spoil than to calcareous  spoil and capable of growing on spoils with low to moderate  phosphorus (17). Soils on which ailanthus is most  commonly found are within the orders Ultisols, Inceptisols, and  Entisols.

  • Burns, Russell M., and Barbara H. Honkala, technical coordinators. 1990. Silvics of North America: 1. Conifers; 2. Hardwoods.   Agriculture Handbook 654 (Supersedes Agriculture Handbook 271,Silvics of Forest Trees of the United States, 1965).   U.S. Department of Agriculture, Forest Service, Washington, DC. vol.2, 877 pp.   http://www.na.fs.fed.us/spfo/pubs/silvics_manual/table_of_contents.htm External link.
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James H. Miller

Source: Silvics of North America

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Climate

Because of its wide distribution, ailanthus grows under a variety  of climatic conditions. Within the naturalized range of the  species, the climate can be temperate to subtropical and humid to  arid. In arid regions bordering the Great Plains, low  precipitation, from 360 to 610 mm (14 to 24 in) annually with 8  dry months, can be tolerated (7), whereas in humid localities in  the southern Appalachians rainfall can exceed 2290 mm (90 in)  annually (15). Annual maximum and minimum temperatures  are -9° and 36° C (15° and 97° F). Extreme  cold and prolonged snow cover restricts the elevational range to  the lower slopes of the Rocky Mountains and prolonged cold  temperatures have reportedly caused dieback, but resprouting  occurs (1,7).

  • Burns, Russell M., and Barbara H. Honkala, technical coordinators. 1990. Silvics of North America: 1. Conifers; 2. Hardwoods.   Agriculture Handbook 654 (Supersedes Agriculture Handbook 271,Silvics of Forest Trees of the United States, 1965).   U.S. Department of Agriculture, Forest Service, Washington, DC. vol.2, 877 pp.   http://www.na.fs.fed.us/spfo/pubs/silvics_manual/table_of_contents.htm External link.
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James H. Miller

Source: Silvics of North America

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● Found in many habitats; 100-2500 m.
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© Missouri Botanical Garden, 4344 Shaw Boulevard, St. Louis, MO, 63110 USA

Source: Missouri Botanical Garden

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Associations

Flower-Visiting Insects of Tree-of-Heaven in Illinois

Ailanthus altissima (Tree-of-Heaven) introduced
(information is very limited; this observation is from Krombein et al.)

Bees (short-tongued)
Andrenidae (Panurginae): Calliopsis andreniformis sn (Kr)

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Faunal Associations

The flowers are cross-pollinated by such insects as honeybees, other bees, beetles, and flies. Aside from seeking nectar and pollen from the flowers, very few insects feed on Tree-of-Heaven (at least in North America). The caterpillars of two moths, Atteva punctella (Ailanthus Webworm) and Samia cynthia (Ailanthus Silkworm), feed on the foliage of this tree. Some birds, like the Pine Grosbeak and White-Winged Crossbill, eat the seeds. There are scattered reports of limited browsing by deer on the foliage, and cattle sometimes browse on seedlings.
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© John Hilty

Source: Illinois Wildflowers

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Foodplant / spot causer
amphigenous colony of Mycocentrospora anamorph of Mycocentrospora acerina causes spots on live leaf of Ailanthus altissima

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Associated Forest Cover

Because of ailanthus' scattered and disjunct occurrence over a  wide geographical range, a listing of associated species would  have little significance. Forest stands around cities are common  areas of invasion and establishment, but it may be an occasional  or minor component of forests following disturbance anywhere  within its naturalized range.

  • Burns, Russell M., and Barbara H. Honkala, technical coordinators. 1990. Silvics of North America: 1. Conifers; 2. Hardwoods.   Agriculture Handbook 654 (Supersedes Agriculture Handbook 271,Silvics of Forest Trees of the United States, 1965).   U.S. Department of Agriculture, Forest Service, Washington, DC. vol.2, 877 pp.   http://www.na.fs.fed.us/spfo/pubs/silvics_manual/table_of_contents.htm External link.
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James H. Miller

Source: Silvics of North America

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Common Hungarian name - mixup with 'vinegar tree'


The common Hungarian name for the "Tree of Heaven" is "Bálványfa".

Unfortunately, most people, even gardeners, call it "ecetfa" that can be translated word by word as "vinegar tree"
which is actually a different specimen: 'Rhus typhina'.

It would be interesting to know if there was a similar confusion in other languages/regions other than hungary.

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Supplier: Zoltan Kocsis

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Diseases and Parasites

Damaging Agents

The species is relatively resistant to  insect predation (7). Three insect species are known to  feed on ailanthus foliage, however (2). Most noted of the  foliage feeders in the eastern range, especially in the South, is  the ailanthus web-worm (Atteva punctella). Larvae from  this insect feed on leaves enclosed in a frail, silken web.  Another larval feeder, imported from Asia, is the cynthia moth  (Samia cynthia). Ailanthus is the preferred host for this  insect, but wild cherry and plum can also become infested. The  Asiatic garden beetle (Maladera castanea) feeds on  numerous plants during night flights, including ailanthus.

    Although many fungi have been reported on the leaves and twigs of  ailanthus, the tree suffers little from disease, and its  pathology need rarely be a consideration in its culture (9). If  ailanthus can be said to be subject to a major disease it would  be Verticillium wilt (Verticillium albo-atrum). Many  trees were killed by this soil-borne wilt in Philadelphia in  1936. Shoestring root rot (Armillaria mellea) has been  reported in trees in New York (16).

    While this tree is rated moderately susceptible to Phymatotrichum  root rot (Phymatotrichum omnivorum) in Texas, it is  considered most satisfactory for planting in the southern parts  of Texas root rot belt (20,23).

    In Texas, seeds are eaten by a number of birds, including the pine  grosbeak and the crossbill (21). Occasional browsing by  deer has also been reported.

    Wind, snow, and hard freezes are damaging to tops of seedlings,  while mature trees are resistant to ice breakage (3). Resprouting  usually occurs, although repeated damage leads to a reduction in  seedling survival.

  • Burns, Russell M., and Barbara H. Honkala, technical coordinators. 1990. Silvics of North America: 1. Conifers; 2. Hardwoods.   Agriculture Handbook 654 (Supersedes Agriculture Handbook 271,Silvics of Forest Trees of the United States, 1965).   U.S. Department of Agriculture, Forest Service, Washington, DC. vol.2, 877 pp.   http://www.na.fs.fed.us/spfo/pubs/silvics_manual/table_of_contents.htm External link.
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James H. Miller

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General Ecology

Although ailanthus is sensitive to frost damage during its early years (Adamik and Brauns 1957), 6-year-old trees have survived winters of -33 centigrades accompanied by high winds (Zelenin 1976). Although Koffer (1895) suggested that ailanthus was unable to withstand the prolonged dry seasons of the Midwest, Dubroca and Bory (1981) commented on the "drought resistance" of the species. Dry soils are probably more suitable for its growth than wet soils (Adamik and Brauns 1957).

Ailanthus does well on very poor soils. Adamik and Brauns (1957) cultivated the species on rather thin topsoil and it "thrives even on stony ground." The tree has been used in revegetating acid mine spoils, tolerating a pH of less than 4.1, soluble salt concentrations up to 0.25 mmhos/cm and phosphorus levels as low as 1.8 ppm (Plass 1975). The tolerance of ailanthus to soil salinity is a disputed point in the literature. Opinions range from "salty soils not suitable for growth" (Adamik and Brauns 1957) to ailanthus "growing well on very saline shell sands (Lavrinenko and Volkov 1973). Intermediate views are expressed by Brogowski et al. (1977), Semoradova and Materna (1982) and Zelenin (1976).

Ailanthus has been planted widely in urban areas because of its ability to tolerate atmospheric pollution. Its ability to adapt to "the dirt and smoke, the dust and drought of cities" was recognized nearly 100 years ago (Sargent 1888). More recently ailanthus has been observed to survive cement dust near cement and lime works (Klincsek 1976); it is moderately resistant to fumes produced by the coke and coal-tar industry (Kozyukina and Obraztsova 1971); its leaves absorb significant amounts of sulfur in areas of high traffic flow (Kim 1975); it can accumulate high levels of mercury in its tissues (Smith 1972); and it is somewhat resistant to ozone exposure (Davis et al. 1978).

Although ailanthus may suffer from root competition by other trees already established in an area (Cozzo 1972), usually it competes successfully with other plants (Cozzo 1972, Hu 1979) and is considered a "dangerous weed" in forest plantations (Magic 1974). A high degree of shade tolerance gives ailanthus a competitive edge over other plant species (Grime 1965). The production of toxic chemicals by ailanthus may also explain the success of this plant. An aqueous extract of ailanthus leaves has been shown to be toxic to 35 species of gymnosperms and 10 species of angiosperms (Mergen 1959). This may be important in limiting natural succession in ailanthus stands. The toxicity levels are highest in the leaves during the early part of the growing season and are maintained at high levels at least until October (Voigt and Mergen 1962).

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Fire Management Considerations

More info for the terms: density, fire suppression, restoration

Due to its ability to sprout from the roots, fire is not recommended for tree-of-heaven control [147,163,275]. Limited fire studies [11,20,39,150,196,247] and anecdotal information [185] suggest that fire may increase tree-of-heaven density. Tree-of-heaven is capable of rapid growth even under adverse conditions, and it grows best with increased nutrient and open canopy conditions [14,34,124,163,166,173,228], which fire can create. Pomp [247] recommends removing tree-of-heaven from the understory prior to prescribed burning or logging.

Whenever there is a nearby tree-of-heaven seed source, disturbed sites require monitoring and follow-up treatments to prevent tree-of-heaven invasion and spread. Roadways, skid trails, and other disturbed grounds are corridors for tree-of-heaven invasion [40,46]. By disturbing soil, fire suppression efforts may lead to postfire establishment if there are trees-of-heaven nearby. Fire-fighting machinery can also disperse tree-of-heaven seed. Washing equipment before it enters fire suppression zones can help prevent tree-of-heaven invasion on burned sites. Postfire monitoring and treatment of skid trails is also advised [232].

Preventing invasive plants from establishing in weed-free burned areas is the most effective and least costly management method. This may be accomplished through early detection and eradication, careful monitoring and follow-up, and limiting dispersal of invasive plant propagules into burned areas. General recommendations for preventing postfire establishment and spread of invasive plants include:
  • Incorporate cost of weed prevention and management into fire rehabilitation plans
  • Acquire restoration funding
  • Include weed prevention education in fire training
  • Minimize soil disturbance and vegetation removal during fire suppression and rehabilitation activities
  • Minimize the use of retardants that may alter soil nutrient availability, such as those containing nitrogen and phosphorus
  • Avoid areas dominated by high priority invasive plants when locating firelines, monitoring camps, staging areas, and helibases
  • Clean equipment and vehicles prior to entering burned areas
  • Regulate or prevent human and livestock entry into burned areas until desirable site vegetation has recovered sufficiently to resist invasion by undesirable vegetation
  • Monitor burned areas and areas of significant disturbance or traffic from management activity
  • Detect weeds early and eradicate before vegetative spread and/or seed dispersal
  • Eradicate small patches and contain or control large infestations within or adjacent to the burned area
  • Reestablish vegetation on bare ground as soon as possible
  • Avoid use of fertilizers in postfire rehabilitation and restoration
  • Use only certified weed-free seed mixes when revegetation is necessary
For more detailed information on these topics, see the following publications: [13,37,109,301].
  • 109. Goodwin, Kim; Sheley, Roger; Clark, Janet. 2002. Integrated noxious weed management after wildfires. EB-160. Bozeman, MT: Montana State University, Extension Service. 46 p. Available online: http://www.montana.edu/wwwpb/pubs/eb160.html [2003, October 1]. [45303]
  • 11. Apsley, David K.; McCarthy, Brian C. 2004. White-tailed deer herbivory on forest regeneration following fire and thinning treatments in southern Ohio mixed oak forests. In: Yaussy, Daniel; Hix, David M.; Goebel, P. Charles; Long, Robert P., eds. Proceedings, 14th central hardwood forest conference; 2004 March 16-19; Wooster, OH. Gen. Tech. Rep. NE-316. Newton Square, PA: U.S. Department of Agriculture, Forest Service, Northeastern Research Station: 461-471. [CD]. [49755]
  • 124. Hanover, James W.; Wood, Bruce W.; Hart, John W.; Brissette, John C.; Dickmann, Donald I.; Stadt, Thomas J.; Lemmien, Walter A.; Kowalewski, Greg. 1978. Accelerated growth of hardwood seedlings. In: Central hardwood forest conference: Proceedings; 1978 November 14-16; West Lafayette, IN. West Lafayette, IN: Purdue University, Department of Forestry and Natural Resources: 370-388. [46133]
  • 13. Asher, Jerry; Dewey, Steven; Olivarez, Jim; Johnson, Curt. 1998. Minimizing weed spread following wildland fires. Proceedings, Western Society of Weed Science. 51: 49. Abstract. [40409]
  • 14. Ashraf, Mohammad, Rehman, Sham-ur. 2001. A short note on the vegetative propagation of Ailanthus and Prosopis. The Pakistan Journal of Forestry. 51(1): 85. [46216]
  • 147. Hunter, Carl G. 1989. Trees, shrubs, and vines of Arkansas. Little Rock, AR: The Ozark Society Foundation. 207 p. [21266]
  • 150. Hutchinson, Todd; Rebbeck, Joanne; Long, Robert. 2004. Abundant establishment of Ailanthus altissima (tree-of-heaven) after restoration treatments in an upland oak forest. In: Yaussy, Daniel; Hix, David M.; Goebel, P. Charles; Long, Robert P., eds. Proceedings, 14th central hardwood forest conference; 2004 March 16-19; Wooster, OH. Gen. Tech. Rep. NE-316. Newton Square, PA: U.S. Department of Agriculture, Forest Service, Northeastern Research Station: 514. [CD]. [49766]
  • 163. Kentucky Exotic Pest Plant Council. 2001. Invasive exotic plant list, [Online]. Southeast Exotic Pest Plant Council (Producer). Available: http://www.se-eppc.org/states/KY/KYlists.html [2005, April 13]. [44948]
  • 166. Knapp, Liza B.; Canham, Charles D. 2000. Invasion of an old-growth forest in New York by Ailanthus altissima: sapling growth and recruitment in canopy gaps. Journal of the Torrey Botanical Society. 127(4): 307-315. [46142]
  • 173. Kowarik, Ingo. 1995. Clonal growth in Ailanthus altissima on a natural site in West Virginia. Journal of Vegetation Science. 6: 853-856. [45195]
  • 185. Lepart, J.; Debussche, M. 1991. Invasion processes as related to succession and disturbance. In: Groves, R. H.; Di Castri, F., eds. Biogeography of Mediterranean invasions. Cambridge: Cambridge University Press: 159-177. [46742]
  • 196. Marsh, Michael A. 2005. Floristic dynamics of Appalachian pine-oak forests over a prescribed fire chronosequence. Morgantown, WV: West Virginia University. 278 p. Thesis. [79749]
  • 20. Beck, John T.; Van Horn, Gene S. 2007. The vascular flora of Prentice Cooper State Forest and Wildlife Management Area, Tennessee. Castanea. 72(1): 15-44. [72483]
  • 228. Orwig, David A.; Foster, David R. 1998. Forest response to the introduced hemlock woolly adelgid in southern New England, USA. Journal of the Torrey Botanical Club. 125(1): 60-73. [44642]
  • 232. Parsons, W. T.; Cuthbertson, E. G. 1992. Noxious weeds of Australia. Melbourne: Inkata Press. 692 p. [74553]
  • 247. Pomp, Jonathan A. 2008. Disturbances, prescribed fire, and invasion by exotic plants in a xeric mixed-oak and oak-pine dominated area of the ridge and valley in eastern West Virginia. Morgantown, WV: West Virginia University. 173 p. Thesis. [79748]
  • 275. Southeast Exotic Pest Plant Council, Tennessee Chapter. 2001. Invasive exotic pest plants in Tennessee, [Online]. Athens, GA: University of Georgia; Southeast Exotic Pest Plant Council (Producer). Available: http://www.se-eppc.org/states/TN/TNIList.html [2004, February 12]. [46747]
  • 301. U.S. Department of Agriculture, Forest Service. 2001. Guide to noxious weed prevention practices. Washington, DC: U.S. Department of Agriculture, Forest Service. 25 p. Available online: http://www.fs.fed.us/invasivespecies/documents/FS_WeedBMP_2001.pdf [2009, November 19]. [37889]
  • 34. Bourdeau, Philippe F.; Laverick, Miriam L. 1958. Tolerance and photosynthetic adaptability to light intensity in white pine, red pine, hemlock and ailanthus seedlings. Forest Science. 4(3): 196-207. [46152]
  • 37. Brooks, Matthew L. 2008. Effects of fire suppression and postfire management activities on plant invasions. In: Zouhar, Kristin; Smith, Jane Kapler; Sutherland, Steve; Brooks, Matthew L., eds. Wildland fire in ecosystems: Fire and nonnative invasive plants. Gen. Tech. Rep. RMRS-GTR-42-vol. 6. Ogden, UT: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 269-280. [70909]
  • 39. Bryant, William S.; Held, Michael E. 2004. Forest vegetation in Hamilton County, Ohio: a cluster analysis and ordination study. In: Yaussy, Daniel; Hix, David M.; Goebel, P. Charles; Long, Robert P., eds. Proceedings, 14th central hardwood forest conference; 2004 March 16-19; Wooster, OH. Gen. Tech. Rep. NE-316. Newton Square, PA: U.S. Department of Agriculture, Forest Service, Northeastern Research Station: 312-322. [CD]. [49744]
  • 40. Burch, Patrick L.; Zedaker, Shepard M. 2003. Removing the invasive tree Ailanthus altissima and restoring natural cover. Journal of Arboriculture. 29(1): 18-24. [45788]
  • 46. Call, Lara J.; Nilsen, Erik T. 2003. Analysis of spatial patterns and spatial association between the invasive tree-of-heaven (Ailanthus altissima) and the native black locust (Robinia pseudoacacia). The American Midland Naturalist. 150(1): 1-14. [45002]

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Fire Regimes

More info for the terms: fire exclusion, fire regime, succession

The fire ecology of tree-of-heaven in its native China was not available in English-language literature as of this writing (2010). Tree-of-heaven is common in long-settled, densely populated regions of China. Although its pharmacological use is mentioned in early Chinese writings, Hu [140] reported that Chinese-language references to its historical ecology were lacking as of 1979. Tree-of-heaven's ability to sprout from photosynthate-storing roots and establish from off-site, wind-dispersed seed; its extraordinarily rapid growth rate; early age of seed production; and its appearance in early successional plant communities in North America (see Botanical and Ecological Characteristics) all suggest that tree-of-heaven has been subject to evolutionary pressures of frequent, stand-replacement disturbances. Whatever FIRE REGIMES tree-of-heaven's native ecosystems were subject to in the past, tree-of-heaven's ability to establish on disturbed sites and persist into late succession suggests that it is well-adapted to survive under a wide range of FIRE REGIMES. See the Fire Regime Table for information on FIRE REGIMES of North American plant communities in which tree-of-heaven may occur.

In North America, tree-of-heaven has invaded ecosystems where, for the most part, historic FIRE REGIMES are no longer functional (for example, see [12,239,313,322]). Dodge [76] speculates that fire exclusion in rare sugar maple-sweet birch communities of High Mountain Park Preserve, New Jersey, may have fostered establishment of tree-of-heaven. However, only a few fire studies have been conducted on tree-of-heaven to date (2010), so it is impossible to assess how—or whether—tree-of-heaven has altered historic FIRE REGIMES in North America.

  • 12. Arno, Stephen F. 2000. Fire in western forest ecosystems. In: Brown, James K.; Smith, Jane Kapler, eds. Wildland fire in ecosystems: Effects of fire on flora. Gen. Tech. Rep. RMRS-GTR-42-vol. 2. Ogden, UT: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 97-120. [36984]
  • 140. Hu, Shiu Ying. 1979. Ailanthus. Arnoldia. 39(2): 29-50. [45755]
  • 239. Paysen, Timothy E.; Ansley, R. James; Brown, James K.; Gottfried, Gerald J.; Haase, Sally M.; Harrington, Michael G.; Narog, Marcia G.; Sackett, Stephen S.; Wilson, Ruth C. 2000. Fire in western shrubland, woodland, and grassland ecosystems. In: Brown, James K.; Smith, Jane Kapler, eds. Wildland fire in ecosystems: Effects of fire on flora. Gen. Tech. Rep. RMRS-GTR-42-vol. 2. Ogden, UT: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 121-159. [36978]
  • 313. Wade, Dale D.; Brock, Brent L.; Brose, Patrick H.; Grace, James B.; Hoch, Greg A.; Patterson, William A., III. 2000. Fire in eastern ecosystems. In: Brown, James K.; Smith, Jane Kapler, eds. Wildland fire in ecosystems: Effects of fire on flora. Gen. Tech. Rep. RMRS-GTR-42-vol. 2. Ogden, UT: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 53-96. [36983]
  • 322. Wright, Henry A.; Bailey, Arthur W. 1982. Fire ecology: United States and southern Canada. New York: John Wiley & Sons. 501 p. [2620]
  • 76. Dodge, Sheridan L. 1997. Successional trends in a mixed oak forest on High Mountain, New Jersey. Journal of the Torrey Botanical Society. 124(4): 312-317. [79792]

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Fuels

More info for the terms: fuel, invasive species, litter, total heat release, tree

Few quantitative measurements of tree-of-heaven litter, aboveground biomass, or leaf area indices were available as of 2010, so the ability of tree-of-heaven to alter fuel loads of native ecosystems is unclear. Fuel studies are needed on tree-of-heaven.

Although tree-of-heaven has large, finely divided leaves [71,104,105,250,308], its leaves may not contribute more to total leaf litter load than the leaves of many associated tree species in deciduous forests. In Connecticut, mean depth of tree-of-heaven litter alone was similar to litter depth averages under most associated tree species in the mixed-deciduous forest (about 0.8 inch (2 cm)). Oaks contributed most biomass to the litter layer, which was sampled in July and August [167]. Tree-of-heaven litter may decay more rapidly than litter of many associated deciduous trees. In Spain, tree-of-heaven litter decayed faster than native English elm (Ulmus minor) (P=0.01) [50]. A study in Maryland found that in first-order streams, litter of native trees contained more lignin and decayed more than twice as slowly as tree-of-heaven litter (P<0.0001) [284].

Tree-of-heaven may contribute important amounts of woody debris to fuel loads in invaded areas. It frequently sheds broken branches in all size classes. The brittle branches break easily even when green, and branch die-back from drought or frost is common [148,151]. In riparian areas by the Middle Rio Grande in New Mexico, tree-of-heaven and other nonnative, invasive woody species were implicated as the main source of heavy fuel loads, with altered hydrologic regimes likely partially responsible for nonnative invasions. The author states "excess woody materials consisting of exotic species and dead and downed fuels of all species are the primary fuels of catastrophic fires" in riparian bosques on the Middle Rio Grande. The community was a Rio Grande cottonwood bosque before nonnative invasions. Contributions to total fuel load were not broken down by species, but saltcedar and Russian-olive (Elaeagnus angustifolia) apparently contributed more woody fuels than tree-of-heaven [152].

Flammability of tree-of-heaven was not reported in the literature as of 2010. Its growth habit and stand structure suggest that once ignited, tree-of-heaven stands probably burn easily. The large, finely divided leaves provide a surface-to-volume ratio favorable for ignition and burning. Dibble and others [69] conducted laboratory tests comparing fuel characteristics of nonnative invasive species with those of cooccurring native species. They found no significant difference between tree-of-heaven and quaking aspen in either total heat release or effective heat of combustion of leaves and twigs [69].

  • 104. Gleason, Henry A.; Cronquist, Arthur. 1991. Manual of vascular plants of northeastern United States and adjacent Canada. 2nd ed. New York: New York Botanical Garden. 910 p. [20329]
  • 105. Godfrey, Robert K. 1988. Trees, shrubs, and woody vines of northern Florida and adjacent Georgia and Alabama. Athens, GA: The University of Georgia Press. 734 p. [10239]
  • 148. Hunter, John C. 1995. Ailanthus altissima (Miller) Swingle: its biology and recent history. California Exotic Pest Plant Council News. 3(4): 4-5. [45846]
  • 151. Illick, Joseph S.; Brouse, E. F. 1926. The ailanthus tree in Pennsylvania. Bulletin 38. Harrisburg, PA: Pennsylvania Department of Forests and Waters. 29 p. [46734]
  • 152. Jemison, Roy. 2004. Relationships between hydrology, exotic plants, and fuel loads in the Middle Rio Grande. In: Hydrology and water resources in Arizona and the Southwest: Proceedings of the 2003 meetings of the hydrology section--Arizona-Nevada Academy of Science; 2003 April 12; Flagstaff, AZ. Volume 33. Glendale, AZ: Arizona Nevada Academy of Science: 85-92. [52856]
  • 167. Kostel-Hughes, Faith; Young, Truman P.; Carreiro, Margaret M. 1998. Forest leaf litter quantity and seedling occurrence along an urban-rural gradient. Urban Ecosystems. 2: 263-278. [51962]
  • 250. Radford, Albert E.; Ahles, Harry E.; Bell, C. Ritchie. 1968. Manual of the vascular flora of the Carolinas. Chapel Hill, NC: The University of North Carolina Press. 1183 p. [7606]
  • 284. Swan, Christopher M.; Healey, Benjamin; Richardson, David C. 2008. The role of native riparian tree species in decomposition of invasive tree of heaven (Ailanthus altissima) leaf litter in an urban stream. Ecoscience. 15(1): 27-35. [79746]
  • 308. Vines, Robert A. 1960. Trees, shrubs, and woody vines of the Southwest. Austin, TX: University of Texas Press. 1104 p. [7707]
  • 50. Castro-Diez, P.; Gonzalez-Munoz, N.; Alonso, A.; Gallardo, A.; Poorter, L. 2009. Effects of exotic invasive trees on nitrogen cycling: a case study in Central Spain. Biological Invasions. 11(8): 1973-1986. [79728]
  • 69. Dibble, Alison C.; White, Robert H.; Lebow, Patricia K. 2007. Combustion characteristics of north-eastern USA vegetation tested in the cone calorimeter: invasive versus non-invasive plants. International Journal of Wildland Fire. 16(4): 426-443. [68947]
  • 71. Diggs, George M., Jr.; Lipscomb, Barney L.; O'Kennon, Robert J. 1999. Illustrated flora of north-central Texas. Sida Botanical Miscellany, No. 16. Fort Worth, TX: Botanical Research Institute of Texas. 1626 p. [35698]

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Fire adaptations and plant response to fire

More info for the terms: basal area, density, ferns, fire management, fire severity, forbs, fuel, importance value, marsh, root crown, root sprout, severity, shrub, shrubs, top-kill, tree

Tree-of-heaven sprouts after top-kill by fire [103,274,299]. It sprouts from the roots, root crown, and/or bole after other aboveground damage (see Vegetative regeneration); so any of these sprouting strategies may occur after top-kill by fire, with root sprouting most likely. Anecdotal accounts suggest that tree-of-heaven is "able to sprout vigorously when...burnt" [185] and persists in some areas "despite...burning" [309]. The fire studies below provide other evidence of tree-of-heaven's ability to survive fire. It is likely—given its large, extended root system [211,230,248,249] and its ability to root sprout and show increased growth rates under fertilization [124]—that tree-of-heaven can flourish in postfire environments. As one of the fastest-growing trees in North America [166,244,259], tree-of-heaven may outcompete native woody species for the open spaces and flush of nutrients that often occur after fire. Further studies on the fire ecology of tree-of-heaven are needed.

Tree-of-heaven can also establish from seed after fire. Although this was documented in only 1 study as of 2010 [196], the potential for postfire tree-of-heaven seedling establishment seems high. Its seed disperses easily by wind [82,163,275], and tree-of-heaven is known to establish from seed in early-successional, disturbed environments other than burns [34,163,166,228] (see Successional Status).

Fire studies: Tree-of-heaven sprouted after the Chavez and Rio Grande Complex wildfires in Rio Grande cottonwood (Populus deltoides subsp. wislizeni) communities along the Middle Rio Grande, New Mexico [299]. It also sprouted after top-kill following 2 separate automobile-ignited fires at the same location in San Diego County, California. It was the only green vegetation in the burned area in postfire year 1 [103]. In mixed oak-pine forests of the Cooper State Forest and Wildlife Management Area, Tennessee, tree-of-heaven grew on sites burned under prescription [20].

Studies on the George Washington National Forest, West Virginia [196,247], and Tar Hollow State Forest, Ohio [11,39,150] show that prescribed burning or thinning and burning may increase tree-of-heaven abundance over prefire or pretreatment levels.

One year after late March prescribed fires on the George Washington National Forest, tree-of-heaven increased on 2 of 3 study sites compared to prefire abundance; these increases were not considered significant except on the upper portion of 1 site, where tree-of-heaven increased exponentially. All postfire tree-of-heaven regeneration was from seedling establishment. The community was a Table Mountain pine-pitch pine-chestnut oak-scarlet oak/mountain-laurel (Pinus pungens-P. rigida-Quercus prinus-Q. coccinea/Kalmia latifolia) forest [196] where fire had been excluded for 81 years. Elevation ranged from 1,880 to 2,782 feet (573-848 m) [247]. Plots on the 3 study sites (Heavener Mountain, Dunkle Knob, and Brushy Knob) were distinguished by aspect and elevation (above or below 2,400 feet (732 m)) [196]. Fire management objectives were to reduce fuel loads, reduce understory shrubs and trees, and increase wildlife forage in groundlayer vegetation. Fire conditions were [196]:

Fire weather conditions for prescribed March fires in a pine-oak forest on the George Washington National Forest [196]
  Heavener Mountain Dunkle Knob
Date 25 March 2009 29 March 2009
Air temperature 18-27 °C 11-21 °C
Relative humidity 32-50% 29-76%
Wind direction mostly SW; SE in late afternoon NW and SE
Windspeed 1.6-9 km/h 2-10 km/h

Tree-of-heaven was not present on Brushy Knob sites either before fire or in postfire year 1. It increased significantly in density (P=0.032) and importance value (P=0.007) on the upper-northeast section of Heavener Mountain compared to adjacent unburned areas. In postfire year 1, tree-of-heaven seedlings also established on unburned portions of Heavener Mountain and on burned, southwest aspects of Heavener Mountain and on Dunkle Knob. Seedling establishment in the upper-northeast section of Dunkle Knob was about 4.5 times greater than that of the other sites combined [196].

Tree-of-heaven abundance before and after the prescribed March fires [196]
Site Density (stems/ha) Importance value* Basal area (m²/ha)
prefire postfire year 1 prefire postfire year 1 prefire postfire year 1
Heavener Mountain, lower-northeast section, seedlings 0.00 0.00 0.00 0.00    
Heavener Mountain, upper-northeast section, seedlings 0.00 277.78 0.00 0.93    
Dunkle Knob, lower-southwest section, seedlings 0.00 277.78 0.00 0.56    
Dunkle Knob, upper-southwest section, seedlings 0.00 833.33 0.00 2.04    
Dunkle Knob, upper-southwest section, overstory 2.22 2.22 0.56 0.56 0.09 0.09
Dunkle Knob, upper-northeast section, seedlings 277.78 6,388.89** 0.23 14.78**    
*Importance value=(relative density + relative basal area)/2
**Significant difference between years (P<0.05). Cells are blank where information is not available.

Since tree-of-heaven seedlings occurred on both burned and unburned areas of Heavener Mountain, Marsh [196] suggested that tree-of-heaven increases on burned sites were not due to fire alone. Increases were not correlated with aspect or elevation, so those factors apparently did not affect tree-of-heaven establishment. Tree-of-heaven was the only nonnative tree species on the site. Overall, the prescribed fires did not significantly increase abundance of nonnative invasive shrubs or herbs. Fuel loads were significantly less in postfire year 1 compared to prefire loads (P=0.0052). Shrub density was reduced 19% to 21%. Forbs and ferns were more abundant after than before fire on sites where fire behavior was "most severe" [196].

In a follow-up study on Dunkle Knob, Pomp [247] found that on most sites, tree-of heaven had returned to prefire levels by postfire year 3. Tree-of-heaven seedlings were producing root sprouts, suggesting that tree-of-heaven density would soon increase beyond prefire levels. Dunkle Knob is an "extremely dry" site. Tree-of-heaven abundance was positively correlated with either moist areas where fire severity was low, areas with a history of logging, or with an open canopy. Outside of riparian zones, tree-of-heaven abundance in postfire year 3 was not significantly associated with fire severity. In contrast to Marsh's [196] earlier findings, Pomp [247] found tree-of-heaven abundance was positively correlated with increasing elevation (R²=0.37).

In a mixed-oak forest in Tar Hollow State Forest, thin-and-burn treatments apparently promoted tree-of-heaven compared to thin-only and burn-only treatments, although the results could be due to pretreatment vegetation composition. Plots were thinned in fall and winter to a density of 19.5 m²/ha; burning was conducted the following March and April [39]. All plots were in white-tailed deer exclosures [11,39]. The following summer, tree-of-heaven was the 4th most common species among 26 woody plants in thin-and-burn treatments [11]. It did not occur on thin-only or burn-only plots [39]. By postfire year 3, tree-of-heaven was "widely distributed" on thin-and-burn plots, with mean density of 17.1 stems/100 m² compared to 5.8 stems/100 m² in thin-only plots and 0.6 stem/100 m² in burn-only plots. Seedling establishment was the assumed method of postfire establishment due to the scarcity of trees-of-heaven before fire [150]. Hutchinson and others [150] concluded that tree-of-heaven's high posttreatment occurrence on thin-and-burn plots was due to its higher pretreatment density on thin-and-burn units (18 trees/100 m²) compared to thin-only (8 trees/100 m²) and burn-only (1 tree/100 m²) units.

  • 103. Gibson, Carly; Sproul, Fred; Rudy, Susan; Davis, Linh. 2003. Vegetation resource assessment: Cedar and Paradise Fires. Ramona, CA: Cleveland National Forest, Palomar Ranger District. 18 p. Unpublished report on file at: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory, Missoula, MT. [60552]
  • 11. Apsley, David K.; McCarthy, Brian C. 2004. White-tailed deer herbivory on forest regeneration following fire and thinning treatments in southern Ohio mixed oak forests. In: Yaussy, Daniel; Hix, David M.; Goebel, P. Charles; Long, Robert P., eds. Proceedings, 14th central hardwood forest conference; 2004 March 16-19; Wooster, OH. Gen. Tech. Rep. NE-316. Newton Square, PA: U.S. Department of Agriculture, Forest Service, Northeastern Research Station: 461-471. [CD]. [49755]
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  • 150. Hutchinson, Todd; Rebbeck, Joanne; Long, Robert. 2004. Abundant establishment of Ailanthus altissima (tree-of-heaven) after restoration treatments in an upland oak forest. In: Yaussy, Daniel; Hix, David M.; Goebel, P. Charles; Long, Robert P., eds. Proceedings, 14th central hardwood forest conference; 2004 March 16-19; Wooster, OH. Gen. Tech. Rep. NE-316. Newton Square, PA: U.S. Department of Agriculture, Forest Service, Northeastern Research Station: 514. [CD]. [49766]
  • 163. Kentucky Exotic Pest Plant Council. 2001. Invasive exotic plant list, [Online]. Southeast Exotic Pest Plant Council (Producer). Available: http://www.se-eppc.org/states/KY/KYlists.html [2005, April 13]. [44948]
  • 166. Knapp, Liza B.; Canham, Charles D. 2000. Invasion of an old-growth forest in New York by Ailanthus altissima: sapling growth and recruitment in canopy gaps. Journal of the Torrey Botanical Society. 127(4): 307-315. [46142]
  • 185. Lepart, J.; Debussche, M. 1991. Invasion processes as related to succession and disturbance. In: Groves, R. H.; Di Castri, F., eds. Biogeography of Mediterranean invasions. Cambridge: Cambridge University Press: 159-177. [46742]
  • 196. Marsh, Michael A. 2005. Floristic dynamics of Appalachian pine-oak forests over a prescribed fire chronosequence. Morgantown, WV: West Virginia University. 278 p. Thesis. [79749]
  • 20. Beck, John T.; Van Horn, Gene S. 2007. The vascular flora of Prentice Cooper State Forest and Wildlife Management Area, Tennessee. Castanea. 72(1): 15-44. [72483]
  • 211. Miller, James H. 1990. Ailanthus altissima (Mill.) Swingle ailanthus. In: Burns, Russell M.; Honkala, Barbara H., tech. coords. Silvics of North America: Vol. 2. Hardwoods. Agriculture Handbook 654. Washington, DC: U.S. Department of Agriculture, Forest Service: 101-104. [46753]
  • 228. Orwig, David A.; Foster, David R. 1998. Forest response to the introduced hemlock woolly adelgid in southern New England, USA. Journal of the Torrey Botanical Club. 125(1): 60-73. [44642]
  • 230. Pan, Elizabeth; Bassuk, Nina. 1985. Effects of soil type and compaction on the growth of Ailanthus altissima seedlings. Journal of Environmental Horticulture. 3(4): 158-162. [45476]
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  • 247. Pomp, Jonathan A. 2008. Disturbances, prescribed fire, and invasion by exotic plants in a xeric mixed-oak and oak-pine dominated area of the ridge and valley in eastern West Virginia. Morgantown, WV: West Virginia University. 173 p. Thesis. [79748]
  • 248. Rabe, Elizabeth P.; Bassuk, Nina. 1984. Adaptation of Ailanthus altissima to the urban environment through analysis of habitat usage and growth response to soil compaction. Hortscience. 19(3): 572. [Abstract]. [45852]
  • 249. Rabe, Elizabeth Pan. 1985. Distribution and growth response of Ailanthus altissima in the urban environment. Ithaca, NY: Cornell University. 87 p. Thesis. [45753]
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  • 274. Smith, D. Max; Kelly, Jeff F.; Finch, Deborah M. 2006. Wildfire, exotic vegetation, and breeding bird habitat in the Rio Grande bosque. In: Aguirre-Bravo, C.; Pellicane, Patrick J.; Burns, Denver P.; Draggan, Sidney, eds. Monitoring science and technology symposium proceedings: unifying knowledge for sustainability in the western hemisphere; 2004 September 20-24; Denver, CO. RMRS-P-42CD. Fort Collins, CO: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 230-237. [67910]
  • 275. Southeast Exotic Pest Plant Council, Tennessee Chapter. 2001. Invasive exotic pest plants in Tennessee, [Online]. Athens, GA: University of Georgia; Southeast Exotic Pest Plant Council (Producer). Available: http://www.se-eppc.org/states/TN/TNIList.html [2004, February 12]. [46747]
  • 299. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station. 2004. Avian, arthropod, and plant communities on unburned and wildfire sites along the Middle Rio Grande. Annual report to Middle Rio Grande Conservancy District [and] Bosque del Apache National Wildlife Refuge. Albuquerque, NM: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station. 32 p. [61054]
  • 309. Virginia Department of Conservation and Recreation, Division of Natural Heritage. 2003. Fact sheet: Tree-of-heaven (Ailanthus altissima (Miller) Swingle), [Online]. In: Invasive alien plant species of Virginia. In: Invasive specis--invasive plants. Richmond, VA: Virginia Division of Natural Heritage (Producer). Available: http://www.dcr.virginia.gov/natural_heritage/documents/fsaial.pdf [2010, November 10]. [45525]
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  • 39. Bryant, William S.; Held, Michael E. 2004. Forest vegetation in Hamilton County, Ohio: a cluster analysis and ordination study. In: Yaussy, Daniel; Hix, David M.; Goebel, P. Charles; Long, Robert P., eds. Proceedings, 14th central hardwood forest conference; 2004 March 16-19; Wooster, OH. Gen. Tech. Rep. NE-316. Newton Square, PA: U.S. Department of Agriculture, Forest Service, Northeastern Research Station: 312-322. [CD]. [49744]
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Post-fire Regeneration

More info for the terms: adventitious, geophyte, initial off-site colonizer, root crown, secondary colonizer, tree

POSTFIRE REGENERATION STRATEGY
[277]:
Tree with root suckers, a sprouting root crown, and adventitious buds
Geophyte, growing points deep in soil
Initial off-site colonizer (off site, initial community)
Secondary colonizer (on- or off-site seed sources)
  • 277. Stickney, Peter F. 1989. Seral origin of species comprising secondary plant succession in Northern Rocky Mountain forests. FEIS workshop: Postfire regeneration. Unpublished draft on file at: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory, Missoula, MT. 10 p. [20090]

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Immediate Effect of Fire

Fire top-kills tree-of-heaven [185,274,299]. Because tree-of-heaven has thin bark [71,104,105,308], live tissues beneath the bark probably scorch easily.
  • 104. Gleason, Henry A.; Cronquist, Arthur. 1991. Manual of vascular plants of northeastern United States and adjacent Canada. 2nd ed. New York: New York Botanical Garden. 910 p. [20329]
  • 105. Godfrey, Robert K. 1988. Trees, shrubs, and woody vines of northern Florida and adjacent Georgia and Alabama. Athens, GA: The University of Georgia Press. 734 p. [10239]
  • 185. Lepart, J.; Debussche, M. 1991. Invasion processes as related to succession and disturbance. In: Groves, R. H.; Di Castri, F., eds. Biogeography of Mediterranean invasions. Cambridge: Cambridge University Press: 159-177. [46742]
  • 274. Smith, D. Max; Kelly, Jeff F.; Finch, Deborah M. 2006. Wildfire, exotic vegetation, and breeding bird habitat in the Rio Grande bosque. In: Aguirre-Bravo, C.; Pellicane, Patrick J.; Burns, Denver P.; Draggan, Sidney, eds. Monitoring science and technology symposium proceedings: unifying knowledge for sustainability in the western hemisphere; 2004 September 20-24; Denver, CO. RMRS-P-42CD. Fort Collins, CO: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 230-237. [67910]
  • 299. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station. 2004. Avian, arthropod, and plant communities on unburned and wildfire sites along the Middle Rio Grande. Annual report to Middle Rio Grande Conservancy District [and] Bosque del Apache National Wildlife Refuge. Albuquerque, NM: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station. 32 p. [61054]
  • 308. Vines, Robert A. 1960. Trees, shrubs, and woody vines of the Southwest. Austin, TX: University of Texas Press. 1104 p. [7707]
  • 71. Diggs, George M., Jr.; Lipscomb, Barney L.; O'Kennon, Robert J. 1999. Illustrated flora of north-central Texas. Sida Botanical Miscellany, No. 16. Fort Worth, TX: Botanical Research Institute of Texas. 1626 p. [35698]

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Successional Status

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More info for the terms: association, density, hardwood, importance value, relative density, succession, tree

Tree-of-heaven is mostly an early-successional species in forest ecosystems [257], and it is most common on disturbed sites throughout its North American range. Starting with a few stems along roadsides or woodland edges, tree-of-heaven may encroach into meadows, woodlands, and open forests [163,250,275]. In invades open eastern hardwood forests, sometimes sharing the canopy with native hardwoods into late succession [280]. In 1986, tree-of-heaven and princesstree were classified as the 2 most successful nonnative trees invading hardwood forests in the Northeast [227], where they often established after tree harvest or other disturbances [211,257]. Huebner [141] found tree-of-heaven was positively associated with either highly disturbed or urban counties in West Virginia (P<0.05). In mixed oak-pine forests on the Cumberland Plateau of Tennessee, tree-of-heaven occurred on early-seral sites disturbed by tornados or construction, on prescribed burns, and along roads, pipelines, and ditches [20]. It is an early-seral, subcanopy or canopy species characteristic of the black cherry-yellow-poplar-red maple-white ash forest association in the Delaware Water Gap National Recreation Area, Pennsylvania [242]. It sometimes codominates in successional black cherry-yellow-poplar-red maple-American ash forests in Valley Forge National Historical Park, North Carolina [246]. Tree-of-heaven is associated with eastern white pine/rhododendron (Rhododendron spp.) second growth on the Carl Sandberg Home National Historic Site, North Carolina [318].

Tree-of-heaven often establishes after logging [247]. It was most common on logged sites in oak-hickory forests on the Jefferson National Forest, especially on skid trails [47]. In another study in oak-hickory on the Jefferson National Forest, tree-of-heaven was most common on clearcut plots; less common on low-leave shelterwood plots; and least common on high-leave shelterwood plots, respectively [46]. On the George Washington National Forest, 71% of the sites where tree-of-heaven was found had previously been logged; the other sites were along roads [247]. Tree-of-heaven density was much greater in recently logged mixed-hardwood stands than mature forest stands in south-central Virginia; only yellow-poplar was more abundant on logged sites [49].

Tree-of-heaven density (stems/ha) in mixed-hardwood in Virginia [49]
  Recently logged stands Mature stands
Seedlings 10,138 (6,692)* 320 (147)
Saplings 318 (112)* 244 (212)
*Significant difference between logged and mature stands (P≤0.05)).
Seedlings are

Tree-of-heaven may also establish in early-seral shrubfields [238] and old fields. In Rock Creek, Washington, DC, tree-of-heaven is a common component in an Allegheny blackberry-multiflora rose (Rubus allegheniensis-Rose multiflora) shrubland [289]. In Maryland, it grew with black locust and princesstree on a farm abandoned 14 years previously [21]. A review of studies conducted in the Hutcheson Memorial Forest Center, New Jersey—which has the largest set of old-field permanent plots established for the longest time in the United States—determined that tree-of-heaven typically established 2 to 4 years after field abandonment [221]. Tree-of-heaven may also occur in middle old-field succession. It was not reported in initial old-field succession in Pennsylvania, but was found in old fields that were abandoned approximately 20 years before. In year 20, hardwoods were forming a 23- to 39-foot (7-12 m) canopy over the herbs. Tree-of-heaven was common in these young hardwood stands [161].

Capacity for rapid growth, mycorrhizal associations [143], and—in eastern hardwood forests with dense white-tailed deer populations—relative unpalatability compared to associated hardwood species [99,166] may confer advantages to tree-of-heaven during early succession. A West Virginia study found mycorrhizal colonization of tree-of-heaven seedling roots was significantly greater on a steep, barren slope (62%) compared to a forest site adjacent to a stream (38%) (P<0.002). The authors suggested that tree-of-heaven established more successfully on open sites due to this trend [143].

Tree-of-heaven is moderately shade tolerant [16,47,108,196] and may persist into late forest succession, typically at low levels in the subcanopy until a canopy gap allows further invasion or expansion [47,166,173,328]. In urban oak-hickory woodlots of central Massachusetts, tree-of-heaven was present only on disturbed sites and did not invade intact woodlands [25]. Gaps created by storms [145,325], hemlock woolly adelgid [228] or gypsy moth defoliation, windstorms [145], or possibly fire [20] may facilitate tree-of-heaven invasion. In Nelson County, Virginia, tree-of-heaven occurred in 2 of 4 avalanche debris chutes surveyed 10 years after Hurricane Camille, but it did not occur in adjacent, undisturbed hardwood forest [145]. Xi and others [325] found tree-of-heaven was invasive following hurricanes in mixed oak-sweetgum piedmont forests of Duke Forest, North Carolina.

Once established in a gap, tree-of-heaven may grow into the forest canopy [166]. It occurs in mature upland hardwood forests of northern New Jersey (review by [60]). It also occurs in upland, mature mixed oak-pignut hickory (Carya glabra) forest in the Black Rock Forest of New York. However, it is most common on disturbed sites, especially near reservoirs [17]. On the Cumberland Plateau of Tennessee, tree-of-heaven was a minor species in gaps within a sugar maple-red maple-yellow-poplar forest. Tree-of-heaven density averaged 4.7 saplings/ha, which represented <0.1 % relative density of tree species in forest gaps [127]. In Ohio, tree-of-heaven apparently invaded canopy gaps in an old-growth slippery elm-white ash woodlot from adjacent secondary stands. Its density was similar in secondary and old-growth stands, although density decreased with distance from roads. In a 2002 survey, tree-of-heaven had increased in all size classes compared to a 1980 survey. Density of trees-of-heaven in the canopy had increased threefold, but subcanopy and smaller trees had the largest increases. Survivorship of sprouts from 2001 to 2002 averaged 42% [85].

Tree-of-heaven does not regenerate from seed under its own canopy [17,85,173]. The seedlings are intolerant of deep shade [34,99,118,119,173], and tree-of-heaven does not photosynthesize efficiently in shade [33,34] at any age. A West Virginia survey found 100% mortality of seedlings in the understory of an oak (Quercus spp.)-sugar maple forest [170]. Seed plantings in New Jersey showed best tree-of-heaven establishment in an open-grown herbaceous community, intermediate establishment in an eastern redcedar/little bluestem (Schizachyrium scoparium) woodland, and least establishment in a closed-canopy oak-hickory forest. Mortality rate was over 90% for tree-of-heaven seed planted under a closed-canopy oak-hickory forest [99]. In the Black Rock Forest of New York, tree-of-heaven likely established from seed after a blowdown and subsequent logging and herbicide spraying in the 1960s. By the early 2000s, an oak-hickory forest had redeveloped; tree-of-heaven was present but not reproducing under the canopy [17].

Tree-of-heaven is generally uncommon in closed-canopy, late-successional hardwood forests lacking gaps [25,34,328]. However, trees-of-heaven on forest edges may spread into the surrounding understory by root sprouts, which may grow slowly but persist with shade [132,148,173]. Without canopy-opening disturbance, under-canopy sprouts remain suppressed and grow slowly [118,148,173]. Tree-of-heaven was scarce in a midsuccessional, mixed oak-hickory forest in southern Illinois, with 2.5 stems/ha, relative dominance of 0.1%, and a low importance value of 0.4% [188].

Little information was available on successional patterns of tree-of-heaven where it is native. A study on coal mine spoils in Shanxi, China, found tree-of-heaven dominated late stages of spoil recovery, after the grassland and shrubland stages had succeeded to a tree-of-heaven woodland [189].
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  • 318. White, Rickie D., Jr. 2003. Vascular plant inventory and plant community classification for Carl Sandberg Home National Historic Site. NatureServe Technical Report: Prepared for the National Park Service under Cooperative Agreement H 5028 01 0435. Durham, NC: NatureServe. 152 p. [79627]
  • 325. Xi, Weimin; Peet, Robert K. 2008. Hurricane effects on the Piedmont forests: patterns and implications. Ecological Restoration. 26(4): 295-298. [73812]
  • 328. Zasada, John C.; Little, Silas. 2008. Ailanthus altissima (P. Mill.) Swingle: ailanthus. In: Bonner, Franklin T., Karrfalt, Robert P., eds. Woody plant seed manual. Agric. Handbook No. 727. Washington, DC: U.S. Department of Agriculture, Forest Service: 224-226. [46269]
  • 33. Bourdeau, Philippe F. 1958. Photosynthetic behavior of sun- and shade-grown leaves in certain tolerant and intolerant tree species. Bulletin of the Ecological Society of America. 39(3): 84. Abstract. [46134]
  • 34. Bourdeau, Philippe F.; Laverick, Miriam L. 1958. Tolerance and photosynthetic adaptability to light intensity in white pine, red pine, hemlock and ailanthus seedlings. Forest Science. 4(3): 196-207. [46152]
  • 46. Call, Lara J.; Nilsen, Erik T. 2003. Analysis of spatial patterns and spatial association between the invasive tree-of-heaven (Ailanthus altissima) and the native black locust (Robinia pseudoacacia). The American Midland Naturalist. 150(1): 1-14. [45002]
  • 47. Call, Lara J.; Nilsen, Erik T. 2005. Analysis of interactions between the invasive tree-of-heaven (Ailanthus altissima) and the native black locust (Robinia pseudoacacia). Plant Ecology. 176: 275-285. [54325]
  • 49. Carter, William K.; Fredericksen, Todd S. 2007. Tree seedling and sapling density and deer browsing incidence on recently logged and mature non-industrial private forestlands in Virginia, USA. Forest Ecology and Management. 242(2-3): 671-677. [66560]
  • 60. Davidson, Donald W. 1973. Vascular plants of the mature upland forests of northern New Jersey. Bulletin of the Torrey Botanical Club. 100(1): 44-55. [62587]
  • 85. Espenschied-Reilly, Amanada L.; Runkle, James R. 2008. Distribution and changes in abundance of Ailanthus altissima (Miller) Swingle in a southwest Ohio woodlot. Ohio Journal of Science. 108(2): 16-22. [79745]
  • 99. Forgione, Helen M. 1993. Limits to the establishment and growth of tree-of-heaven explored. Restoration & Management Notes. 11(1): 70-71. [22459]

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Germination and seedling establishment

More info for the terms: hardwood, interference, litter, presence, schizocarp, succession, tree

Tree-of-heaven does not have exacting germination requirements, although germination may proceed slowly. Tree-of-heaven embryos are dormant, and stratification improves germination rates [19,112,148,211]. Seeds dispersed in the field likely overwinter before germinating. Hunter [148] reported a 30% germination rate for seeds that overwintered on parent trees and dispersed in spring. A study in Spain found tree-of-heaven schizocarp size was not correlated with rates of either germination or seedling establishment [66].

Substrate is seemingly not important for successful tree-of-heaven germination. Seed can germinate and establish in highly compacted soil [249] and in pavement cracks [291]. The seed is salt tolerant. Studies of several eastern hardwood species found roadside salt did not appreciably affect tree-of-heaven germination; native oak and birch seeds were far more adversely affected by road salt [27].

Immersion, light intensity, and presence of litter affect tree-of-heaven germination rates. Short immersion in water may enhance tree-of-heaven germination. A German study showed 87% mean germination for tree-of-heaven seed lots soaked for 3 days, 53% germination for unsoaked seed lots, and 32% germination for seed lots soaked for 20 days [174]. Tree-of-heaven may germinate in low light, but resulting emergents are unlikely to establish [85]. Litter has both negative and positive effects on germination. In eastern deciduous forests, oak (Quercus spp.) leaf litter delayed tree-of-heaven germination and increased seedling mortality, but it did not affect subsequent biomass of surviving tree-of-heaven seedlings [89]. Litter may have positive effects on tree-of-heaven germination and establishment by reducing interference from herbaceous species [90].

Although seed production is prolific, tree-of-heaven seedling establishment is infrequent on many sites [148,198,232]. Despite tree-of-heaven's large seed output in a Connecticut site (see Seed production) [198], seedling establishment was low. The authors concluded that tree-of-heaven required canopy gaps to establish in otherwise closed-canopy forests [198]. Dry climate may limit tree-of-heaven recruitment in the Great Plains and the western United States [93,232]. Even so, tree-of-heaven has successfully expanded its range through seed spread and seedling establishment [166,245,257,262], and establishment from seed appears more common than generally indicated in the literature [163,275]. In a root excavation study in New York, Knapp and Canham [166] found initial tree-of-heaven recruitment in gaps in an eastern hemlock (Tsuga canadensis) forest was from off-site seed, not root sprouts. In the Black Rock Forest of New York, tree-of-heaven likely established from seed after a blowdown and subsequent logging and herbicide spraying in the 1960s. By the early 2000s, an oak-hickory forest had redeveloped; tree-of-heaven was present but not reproducing under the canopy [17]. Tree-of-heaven also established from seed on harvested oak forests on the Jefferson National Forest, Virginia [47].

Kostel-Hughes and others [169] surmised that tree-of-heaven is best adapted to establishment in early succession, when litter layers are lacking or shallow. In the greenhouse, tree-of-heaven seeds showed no significant differences in germination rate when placed on top of the litter, buried shallowly (0.4-0.8 inch (1-2 cm)), or buried deeply (2 inches (5 cm)). However, seedling height (P<0.001), aboveground biomass (P<0.03), and root:shoot ratio (P<0.001) decreased with increasing burial depth of seeds. The authors noted that some oak seedlings lifted up and hence reduced litter as they emerged, and some tree-of-heaven seedlings emerged from those reduced-litter microsites. Based on studies by Facelli and Pickett [90], they conjectured that a portion of tree-of-heaven's invasive success may be due to its ability to allocate more biomass to shoots than roots when emerging in deep litter. Although less root biomass means less ability to absorb water and nutrients, tree-of-heaven may compensate by allocating more resources to roots later in the growing season [169].

Two studies show tree-of-heaven germinated more slowly but had greater total emergence than native tree species. In the greenhouse, tree-of-heaven germinated later than native sweetgum, American sycamore, and nonnative princesstree [215,216]. In West Virginia field experiments in mixed-hardwood communities, stratified tree-of-heaven seeds showed better emergence across several sites compared to yellow-poplar seeds (P<0.0001). Tree-of-heaven showed no preference for north- vs. south-facing slopes, while yellow-poplar establishment was better on north slopes. Comparing tree-of-heaven germination across sites, there was no significant difference in emergence on clearcut and selective-cut sites (~80%), but tree-of-heaven emergence was significantly lower in intact forest (<20%) compared to logged sites (P=0.001) [171].

In Seoul, South Korea, tree-of-heaven seedlings established south of parent plants due to seed dispersal by prevailing northwest winds. The tree is nonnative there and is considered an urban weed because of its prolific seedling establishment and spread [53].

  • 112. Graves, William R. 1990. Stratification not required for tree-of-heaven seed germination. Tree Planters' Notes. 41(2): 10-12. [46149]
  • 148. Hunter, John C. 1995. Ailanthus altissima (Miller) Swingle: its biology and recent history. California Exotic Pest Plant Council News. 3(4): 4-5. [45846]
  • 163. Kentucky Exotic Pest Plant Council. 2001. Invasive exotic plant list, [Online]. Southeast Exotic Pest Plant Council (Producer). Available: http://www.se-eppc.org/states/KY/KYlists.html [2005, April 13]. [44948]
  • 166. Knapp, Liza B.; Canham, Charles D. 2000. Invasion of an old-growth forest in New York by Ailanthus altissima: sapling growth and recruitment in canopy gaps. Journal of the Torrey Botanical Society. 127(4): 307-315. [46142]
  • 169. Kostel-Hughes, Faith; Young, Truman P.; Wehr, John D. 2005. Effects of leaf litter depth on the emergence and seedling growth of deciduous forest tree species in relation to seed size. Journal of the Torrey Botanical Society. 132(1): 50-61. [62403]
  • 17. Barringer, Kerry; Clemants, Steven E. 2003. The vascular flora of Black Rock Forest, Cornwall, New York. Journal of the Torrey Botanical Society. 130(4): 292-308. [69529]
  • 171. Kota, Nathan L.; Landenberger, Rick E.; McGraw, James B. 2007. Germination and early growth of Ailanthus and tulip poplar in three levels of forest disturbance. Biological Invasions. 9: 197-211. [71253]
  • 174. Kowarik, Ingo; Saumel, Ina. 2008. Water dispersal as an additional pathway to invasions by the primarily wind-dispersed tree Ailanthus altissima. Plant Ecology. 198: 241-252. [71495]
  • 19. Baskin, Carol C.; Baskin, Jerry M. 2001. Seeds: ecology, biogeography, and evolution of dormancy and germination. San Diego, CA: Academic Press. 666 p. [60775]
  • 198. Martin, Patrick H.; Canham, Charles D. 2010. Dispersal and recruitment limitation in native versus exotic tree species: life-history strategies and Janzen-Connell effects. Oikos. 119(5): 807-824. [79723]
  • 211. Miller, James H. 1990. Ailanthus altissima (Mill.) Swingle ailanthus. In: Burns, Russell M.; Honkala, Barbara H., tech. coords. Silvics of North America: Vol. 2. Hardwoods. Agriculture Handbook 654. Washington, DC: U.S. Department of Agriculture, Forest Service: 101-104. [46753]
  • 215. Moore, James E. 2006. Effects of soil type and soil moisture on the germination and establishment of exotic and native trees of the North Carolina Piedmont. Greensboro, NC: The University of North Carolina. 48 p. Thesis. [72014]
  • 216. Moore, James E.; Lacey, Elizabeth P. 2009. A comparison of germination and early growth of four early successional tree species of the southeastern United States in different soil and water regimes. The American Midland Naturalist. 162(2): 388-394. [79718]
  • 232. Parsons, W. T.; Cuthbertson, E. G. 1992. Noxious weeds of Australia. Melbourne: Inkata Press. 692 p. [74553]
  • 245. Plass, William T. 1975. An evaluation of trees and shrubs for planting surface-mine spoils. Res. Pap. NE-317. Upper Darby, PA: U.S. Department of Agriculture, Forest Service, Northeastern Forest Experiment Station. 8 p. [46129]
  • 249. Rabe, Elizabeth Pan. 1985. Distribution and growth response of Ailanthus altissima in the urban environment. Ithaca, NY: Cornell University. 87 p. Thesis. [45753]
  • 257. Robinson, George R.; Handel, Steven N. 1993. Forest restoration on a closed landfill: rapid addition of new species by bird dispersal. Conservation Biology. 7(2): 271-278. [22062]
  • 262. Santamour, Frank S., Jr. 1983. Woody-plant succession in the urban forest: filling cracks and crevices. Journal of Arboriculture. 9(10): 267-270. [45849]
  • 27. Bicknell, Susan H.; Smith, William H. 1975. Influence of soil salt, at levels characteristic of some roadside environments, on the germination of certain tree seeds. Plant and Soil. 43(3): 719-722. [46740]
  • 275. Southeast Exotic Pest Plant Council, Tennessee Chapter. 2001. Invasive exotic pest plants in Tennessee, [Online]. Athens, GA: University of Georgia; Southeast Exotic Pest Plant Council (Producer). Available: http://www.se-eppc.org/states/TN/TNIList.html [2004, February 12]. [46747]
  • 291. Thomson, James D.; Neal, Paul R. 1989. How-to-do-it: Wind dispersal of tree seeds & fruits. The American Biology Teacher. 51(8): 482-486. [79794]
  • 47. Call, Lara J.; Nilsen, Erik T. 2005. Analysis of interactions between the invasive tree-of-heaven (Ailanthus altissima) and the native black locust (Robinia pseudoacacia). Plant Ecology. 176: 275-285. [54325]
  • 53. Cho, Chi-Woung; Lee, Kyong-Jae. 2002. Seed dispersion and seedling spatial distribution of the tree of heaven in urban environments. Korean Journal of Environment and Ecology. 16(1): 87-93. [50249]
  • 66. Delgado, J. A.; Jimenez, M. D.; Gomez, A. 2009. Samara size versus dispersal and seedling establishment in Ailanthus altissima (Miller) Swingle. Journal of Environmental Ecology. 30(2): 183-186. [79741]
  • 85. Espenschied-Reilly, Amanada L.; Runkle, James R. 2008. Distribution and changes in abundance of Ailanthus altissima (Miller) Swingle in a southwest Ohio woodlot. Ohio Journal of Science. 108(2): 16-22. [79745]
  • 89. Facelli, Jose M. 1994. Multiple indirect effects of plant litter affect the establishment of woody seedlings in old fields. Ecology. 75(6): 1727-1735. [23541]
  • 90. Facelli, Jose M.; Pickett, S. T. A. 1991. Indirect effects of litter on woody seedlings subject to herb competition. Oikos. 62(2): 129-138. [46146]
  • 93. Feret, Peter P. 1985. Ailanthus: variation, cultivation, and frustration. Journal of Arboriculture. 11(12): 361-368. [46741]

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Seed banking

Seeds retain dormancy for less than a year, so tree-of-heaven does not build up a persistent seed bank [87,149,176]. Tree-of-heaven establishes transient soil seed banks from on- and off-site parent sources [328]. Dobberpuhl [75] found viable tree-of-heaven seed in a soil seed bank in Tennessee, although there were no trees-of-heaven in the mixed-oak overstory [75]. A West Virginia field study showed tree-of-heaven's seed bank averaged 48.5 seeds/m² in soils of rural woodlands and grasslands [180]. In soils from a New York City park, tree-of-heaven establishment in the greenhouse averaged 27.7 emergents/m² in soils collected at 0- to 2-inch (5 cm) depths and 14.3 emergents/m² in soils collected at 2- to 4-inch (5-10 cm) depths [168].
  • 149. Hunter, John. 2000. Ailanthus altissima (Miller) Swingle. In: Bossard, Carla C.; Randall, John M.; Hoshovsky, Marc C., eds. Invasive plants of California's wildlands. Berkeley, CA: University of California Press: 32-36. [46752]
  • 168. Kostel-Hughes, Faith; Young, Truman P.; McDonnell, Mark J. 1998. The soil seed bank and its relationship to the aboveground vegetation in deciduous forests in New York City. Urban Ecosystems. 2: 43-59. [51882]
  • 176. Krussmann, Gerd; Wennemuth, Georg; Thon, Heinz Edgar. 1981. Die baumschule. 5th ed. Berlin: Parey. 565 p. [46761]
  • 180. Landenberger, Rick E.; Kota, Nathan L.; McGraw, James B. 2007. Seed dispersal of the non-native invasive tree Ailanthus altissima into contrasting environments. Plant Ecology. 192(1): 55-70. [69766]
  • 328. Zasada, John C.; Little, Silas. 2008. Ailanthus altissima (P. Mill.) Swingle: ailanthus. In: Bonner, Franklin T., Karrfalt, Robert P., eds. Woody plant seed manual. Agric. Handbook No. 727. Washington, DC: U.S. Department of Agriculture, Forest Service: 224-226. [46269]
  • 75. Dobberpuhl, J. 1980. Seed banks of forest soils in east Tennessee. Knoxville, TN: University of Tennessee. 219 p. Thesis. [46755]
  • 87. Evans, C. W.; Moorhead, D. J.; Bargeron, C. T.; Douce, G. K. 2006. Invasive plant responses to silvicultural practices in the South. Bugwood Network BW-2006-03. Tifton, GA: The University of Georgia Bugwood Network. 52 p. Available online: http://www.invasive.org/silvicsforinvasives.pdf. [72425]

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Seed dispersal

More info for the terms: marsh, restoration, schizocarp, tree

The winged schizocarps are easily and widely dispersed by wind [53,82,163,170,180,181,261]. Entire schizocarp clusters may break off and disperse as a unit. In Ithaca, New York, tree-of-heaven schizocarp clusters often fell and dispersed in clumps in fall, resulting in patches of closely related seedlings. Over the winter, seeds dispersed individually as the fruit clusters disintegrated [230]. A New Jersey study found large, heavy tree-of-heaven seeds traveled as far as light tree-of-heaven seeds [181]. In Seoul, South Korea, tree-of-heaven seed traveled a maximum of 7.5 times the width of the parent crown [53]. On Staten Island, New York, tree-of-heaven seedlings volunteered on a restored landfill site planted to native woody species. A year after restoration plantings, tree-of-heaven count on fifty 10 × 30 meter plots totaled 65 seedlings, the 6th highest among 32 taxa that regenerated on the site. Distance to the nearest seed-bearing tree-of-heaven was 299 feet (70 m) [257]. In West Virginia, seeds from trees on steep slopes dispersed farther downhill than seeds on gentle or flat sites (P157]. Matlack [201] reported the following dispersal patterns for tree-of-heaven schizocarps collected in Delaware:

Dispersal characteristics for tree-of-heaven schizocarps in the laboratory. Data are means (SD) [201].
Rate of descent Lateral movement in still air Lateral distance in a 10 km/hr breeze (estimated)
0.56 m/sec (0.09) 0.87 m (0.10) 111.6 m

Distance traveled was significantly greater than that of fruits or seeds of 37 other wind-dispersed species (P<0.05) [201].

Water [174,232,261] and machinery [232] also disperse tree-of-heaven schizocarp clusters and seeds. A study in Germany found that for cities with rivers, the rivers were a secondary dispersal agent that moved wind-dispersed tree-of-heaven seed that landed in rivers from urban to distant rural areas [261]. Tree-of-heaven seeds dispersed in and along the Monogahela River of West Virginia showed germination rates similar to those of seeds on land (94% germination, P=0.006). Seeds from trees growing near water were most likely to land in and be transported directly by water; water-borne seeds stayed buoyant about 1.5 days [157]. In a pine-oak community in West Virginia, Marsh [196] observed that tree-of-heaven established near roads and on tree harvest sites; machinery may have helped disperse seeds onto these sites.

  • 157. Kaproth, Matthew A.; McGraw, James B. 2008. Seed viability and dispersal of the wind-dispersed invasive Ailanthus altissima in aqueous environments. Forest Science. 54(5): 490-496. [79730]
  • 163. Kentucky Exotic Pest Plant Council. 2001. Invasive exotic plant list, [Online]. Southeast Exotic Pest Plant Council (Producer). Available: http://www.se-eppc.org/states/KY/KYlists.html [2005, April 13]. [44948]
  • 170. Kota, Nathan L. 2005. Comparitive seed dispersal, seedling establishment and growth of exotic invasive Ailanthus altissima (Mill.) Swingle and native Lirodendron tulipera (L.). Morgantown, WV: West Virginia University. 108 p. Thesis. [79906]
  • 174. Kowarik, Ingo; Saumel, Ina. 2008. Water dispersal as an additional pathway to invasions by the primarily wind-dispersed tree Ailanthus altissima. Plant Ecology. 198: 241-252. [71495]
  • 180. Landenberger, Rick E.; Kota, Nathan L.; McGraw, James B. 2007. Seed dispersal of the non-native invasive tree Ailanthus altissima into contrasting environments. Plant Ecology. 192(1): 55-70. [69766]
  • 181. Landenberger, Rick E.; Warner, Timothy A.; McGraw, James B. 2009. Spatial patterns of female Ailanthus altissima across an urban-to-rural land use gradient. Urban Ecosystems. 12(4): 437-448. [79727]
  • 196. Marsh, Michael A. 2005. Floristic dynamics of Appalachian pine-oak forests over a prescribed fire chronosequence. Morgantown, WV: West Virginia University. 278 p. Thesis. [79749]
  • 201. Matlack, Glenn R. 1987. Diaspore size, shape, and fall behavior in wind-dispersed plant species. American Journal of Botany. 74(8): 1150-1160. [28]
  • 230. Pan, Elizabeth; Bassuk, Nina. 1985. Effects of soil type and compaction on the growth of Ailanthus altissima seedlings. Journal of Environmental Horticulture. 3(4): 158-162. [45476]
  • 232. Parsons, W. T.; Cuthbertson, E. G. 1992. Noxious weeds of Australia. Melbourne: Inkata Press. 692 p. [74553]
  • 257. Robinson, George R.; Handel, Steven N. 1993. Forest restoration on a closed landfill: rapid addition of new species by bird dispersal. Conservation Biology. 7(2): 271-278. [22062]
  • 261. Samuel, Ina; Kowarik, Ingo. 2010. Urban rivers as dispersal corridors for primarily wind-dispersed invasive tree species. Landscape and Urban Planning. 94(3-4): 244-249. [79737]
  • 53. Cho, Chi-Woung; Lee, Kyong-Jae. 2002. Seed dispersion and seedling spatial distribution of the tree of heaven in urban environments. Korean Journal of Environment and Ecology. 16(1): 87-93. [50249]
  • 82. Duncan, Wilbur H.; Duncan, Marion B. 1988. Trees of the southeastern United States. Athens, GA: The University of Georgia Press. 322 p. [12764]

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Seed production

More info for the terms: top-kill, tree

Tree-of-heaven produces many small, light seeds [77,92]. In a mixed-hardwood forest in Connecticut, tree-of-heaven averaged 4.84 inches (12.3 cm) DBH in size at first seed production. It had greatest average seed production of 10 overstory trees across 2 years; its seed production was 40 times that of the next highest-producing species. For parent trees of 12 inches (30 cm) DBH, tree-of-heaven produced means of 400,000 seeds in 1994 and 2 million seeds in 1995. Tree-of-heaven and white ash had the longest seed dispersal distances of the 10 trees, but most tree-of-heaven seeds fell within 20 feet (5 m) of the parent trunk. Tree-of-heaven seed rain spiked at 2,500 seeds/m²/12-inch DBH parent tree, showing greatest seed output of all 10 tree species. The authors concluded that tree-of-heaven is "exceptionally fecund even in competitive, closed-canopy forest stands" [198].

Flower, fruit, and seed production begins early in development. Six-week-old seedlings have flowered in the greenhouse [92], and 1-year-old seedlings and 2-year-old root sprouts have been observed in the field with fruit [148,163,275]. Trees in California produce viable seed by 10 years of age [148]. Heaviest seed production is from 12 to 20 years of age [211]. In France, which has a climate similar to California, 1.6- to 3.3-foot long (0.5-1 m) root sprouts produced seeds [30].

Mature female trees may produce several hundred flower clusters in a year. Hunter [148] reports that over 5 years, production of a female tree in Martinez, California, averaged 150, 183, 219, 439, and 56 clusters/year. An individual flower contains hundreds of seeds, so individual trees may produce >325,000 seeds/year [30,148]. Illick and Brouse [151] estimated that a small, 12-inch-diameter (30 cm) tree in Pennsylvania produced over a million seeds in 1 year. Most seeds are viable, even those that overwinter on the tree and disperse in spring [148,328]. Repeated top-kill reduces seed production [211].

  • 148. Hunter, John C. 1995. Ailanthus altissima (Miller) Swingle: its biology and recent history. California Exotic Pest Plant Council News. 3(4): 4-5. [45846]
  • 151. Illick, Joseph S.; Brouse, E. F. 1926. The ailanthus tree in Pennsylvania. Bulletin 38. Harrisburg, PA: Pennsylvania Department of Forests and Waters. 29 p. [46734]
  • 163. Kentucky Exotic Pest Plant Council. 2001. Invasive exotic plant list, [Online]. Southeast Exotic Pest Plant Council (Producer). Available: http://www.se-eppc.org/states/KY/KYlists.html [2005, April 13]. [44948]
  • 198. Martin, Patrick H.; Canham, Charles D. 2010. Dispersal and recruitment limitation in native versus exotic tree species: life-history strategies and Janzen-Connell effects. Oikos. 119(5): 807-824. [79723]
  • 211. Miller, James H. 1990. Ailanthus altissima (Mill.) Swingle ailanthus. In: Burns, Russell M.; Honkala, Barbara H., tech. coords. Silvics of North America: Vol. 2. Hardwoods. Agriculture Handbook 654. Washington, DC: U.S. Department of Agriculture, Forest Service: 101-104. [46753]
  • 275. Southeast Exotic Pest Plant Council, Tennessee Chapter. 2001. Invasive exotic pest plants in Tennessee, [Online]. Athens, GA: University of Georgia; Southeast Exotic Pest Plant Council (Producer). Available: http://www.se-eppc.org/states/TN/TNIList.html [2004, February 12]. [46747]
  • 30. Bory, G.; Clair-Maczulajtys, D. 1980. Production, dissemination, and polymorphism of seeds in Ailanthus altissima (Mill.) Swingle, Simaroubaceae. Revue Gererale de Botanique. 88(1049/1051): 297-311. [45847]
  • 328. Zasada, John C.; Little, Silas. 2008. Ailanthus altissima (P. Mill.) Swingle: ailanthus. In: Bonner, Franklin T., Karrfalt, Robert P., eds. Woody plant seed manual. Agric. Handbook No. 727. Washington, DC: U.S. Department of Agriculture, Forest Service: 224-226. [46269]
  • 77. Dow Agro Sciences. 2006. Top 10 invasive plants. Arbor age. 26(8): 12-14. [77657]
  • 92. Feret, Peter P. 1973. Early flowering in Ailanthus. Forest Science. 19(3): 237-239. [45855]

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Pollination

A variety of nectar- and pollen-feeding insects pollinate tree-of-heaven [5,227]. Although disagreeable to humans, the strong odor of the flowers attracts honey bees, flies, beetles, and other insects [5,211]. A study in suburban Chicago found large bee species were the primary pollinators; the bees visited both male and female trees. Flies, especially those attracted to fetid-smelling flowers, visited female trees-of-heaven often but were probably less efficient pollinators than the bees [5].
  • 211. Miller, James H. 1990. Ailanthus altissima (Mill.) Swingle ailanthus. In: Burns, Russell M.; Honkala, Barbara H., tech. coords. Silvics of North America: Vol. 2. Hardwoods. Agriculture Handbook 654. Washington, DC: U.S. Department of Agriculture, Forest Service: 101-104. [46753]
  • 227. Orians, G. H.. 1986. Site characteristics favoring invasions. In: Mooney, Harold A.; Drake, James A., eds. Ecology of biological invasions of North America and Hawaii. Ecological Studies 58. New York: Springer-Verlag: 133-148. [17513]
  • 5. Aldrich, Preston R.; Brusa, Anthony; Heinz, Cheryl A.; Greer, Gary K.; Huebner, Cynthia. 2008. Floral visitation of the invasive stinking ash in western suburban Chicago. Transactions of the Illinois State Academy of Science. 101(1-2): 1-12. [79787]

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Breeding system

More info for the terms: bisexual, dioecious

Tree-of-heaven is mostly dioecious. Rarely, either bisexual trees or trees with both bisexual and unisexual flowers are found [71,104,148,211,328].

As with most species with wind-dispersed seed, tree-of-heaven appears to have a relatively uniform genetic system, with most diversity occurring among rather than within populations [94,249]. Because most North American tree-of-heaven populations originated from 3 introductions [71,139,288,312] (see General Distribution), they may be less genetically diverse than native Asian populations. A comparison of tree-of-heaven seedlings germinated from seed collections from 5 locations across the United States and 5 locations across China showed significant differences in height growth (P=0.01), root:shoot ratios (P=0.05), and leaf area (P=0.05) among seedlings from the United States and Chinese seedlings. Populations from the United States were taller, allocated relatively less biomass to roots than stems, and had greater leaf areas than Chinese populations [94]. In a common garden study comparing seedlings of populations within the United States, Feret and others [95] found California populations were significantly taller than eastern populations (P=0.01). Seed width and biomass were correlated with latitude (t=0.96), with northern populations having the widest, heaviest seeds. Feret [93] found some tree-of-heaven seed and seedling growth characteristics of provenances from the eastern United States and California appeared random, and they were not correlated (nor appeared best adapted) to site or geographic location. He reported significant differences between North American and Chinese tree-of-heaven provenances for seed and seedling characteristics. Contrary to expectations, there was no evidence of inbreeding depression in North American provenances compared to native Chinese provenances [93].

  • 104. Gleason, Henry A.; Cronquist, Arthur. 1991. Manual of vascular plants of northeastern United States and adjacent Canada. 2nd ed. New York: New York Botanical Garden. 910 p. [20329]
  • 139. Hoshovsky, Marc C. 1988. Element stewardship abstract: Ailanthus altissima--Tree-of-heaven, [Online]. In: Managment library--plants. In: The global invasive species team (GIST). Arlington, VA: The Nature Conservancy (Producer). Available: http://tncweeds.ucdavis.edu/esadocs/documnts/ailaalt.html [2010, November 9]. [46265]
  • 148. Hunter, John C. 1995. Ailanthus altissima (Miller) Swingle: its biology and recent history. California Exotic Pest Plant Council News. 3(4): 4-5. [45846]
  • 211. Miller, James H. 1990. Ailanthus altissima (Mill.) Swingle ailanthus. In: Burns, Russell M.; Honkala, Barbara H., tech. coords. Silvics of North America: Vol. 2. Hardwoods. Agriculture Handbook 654. Washington, DC: U.S. Department of Agriculture, Forest Service: 101-104. [46753]
  • 249. Rabe, Elizabeth Pan. 1985. Distribution and growth response of Ailanthus altissima in the urban environment. Ithaca, NY: Cornell University. 87 p. Thesis. [45753]
  • 288. Tellman, Barbara. 1998. Stowaways and invited guests: how some exotic plant species reached the American Southwest. In: Tellman, Barbara; Finch, Deborah M.; Edminster, Carl; Hamre, Robert, eds. The future of arid grasslands: identifying issues, seeking solutions: Proceedings; 1996 October 9-13; Tucson, AZ. Proceedings RMRS-P-3. Fort Collins, CO: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 144-149. [29294]
  • 312. Voss, Edward G. 1985. Michigan flora. Part II. Dicots (Saururaceae--Cornaceae). Bulletin 59. Bloomfield Hills, MI: Cranbrook Institute of Science; Ann Arbor, MI: University of Michigan Herbarium. 724 p. [11472]
  • 328. Zasada, John C.; Little, Silas. 2008. Ailanthus altissima (P. Mill.) Swingle: ailanthus. In: Bonner, Franklin T., Karrfalt, Robert P., eds. Woody plant seed manual. Agric. Handbook No. 727. Washington, DC: U.S. Department of Agriculture, Forest Service: 224-226. [46269]
  • 71. Diggs, George M., Jr.; Lipscomb, Barney L.; O'Kennon, Robert J. 1999. Illustrated flora of north-central Texas. Sida Botanical Miscellany, No. 16. Fort Worth, TX: Botanical Research Institute of Texas. 1626 p. [35698]
  • 93. Feret, Peter P. 1985. Ailanthus: variation, cultivation, and frustration. Journal of Arboriculture. 11(12): 361-368. [46741]
  • 94. Feret, Peter P.; Bryant, Richard L. 1974. Genetic differences between American and Chinese ailanthus seedlings. Silvae Genetica. 23(5): 144-148. [45518]
  • 95. Feret, Peter P.; Bryant, Richard L.; Ramsey, James A. 1974. Genetic variation among American seed sources of Ailanthus altissima (Mill.) Swingle. Scientia Horticulturae. 2(4): 405-411. [46124]

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Vegetative regeneration

More info for the terms: root crown, root sprout, top-kill

Tree-of-heaven sprouts from the roots, root crown, and bole [93,145,163,185,211,275]. Although reproduction from seed is not rare, sprouting is its most common method of regeneration [163]. In Ithaca, New York, 58% of 1-year-old, excavated tree-of-heaven stems were root sprouts and 42% were seedlings [230]. Young trees that are cut to the root crown before bark becomes thick and corky often sprout from both the root crown and roots [163,275]. Bole damage promotes root, root crown, and bole sprouting [148,163]. Death or injury of the main stem usually results in prolific root sprouting [211]. Top-growth damage is not necessary for root sprouting to occur, however. Even as seedlings, trees-of-heaven produce horizontal roots capable of sprouting [45]. Except in the rose (Rosacea) [96,269] and willow (Salicaceae) (review by [327]) families, root sprouting without top damage is uncommon in woody species (reviews by [65,120]), but it is a powerful regeneration strategy for species employing it. Roots have more nutrient- and photosynthate-storing capacity than rhizomes, conferring better protection from aboveground disturbances such as fire [159,160] and show a stronger sprouting response after top-kill [65,120]. Tree-of-heaven sprouts are more likely to persist in low-light conditions, such as within a subcanopy, than are seedlings [85].

With tree-of-heaven's spreading root system, root sprouts may appear as far as 50 to 90 feet (15-27 m) from the parent stem [151,163,275]. During drought, tree-of-heaven translocates stem water into roots and begins stem die-back. Die-back may be extensive during extended droughts, but tree-of-heaven typically survives drought by sprouting from the roots when there is sufficient water to support new growth. Sprouting after frost die-back is common in tree-of-heaven's northern limits [93].

On the Himalayan foothills of India, trees-of-heaven with root crown girths between 12 and 16 inches (30 and 40 cm) showed greatest root sprout production following road construction. Trees in the largest-diameter class did not produce sprouts [179].

  • 120. Groff, Paul A.; Kaplan, Donald R. 1988. The relation of root systems to shoot systems in vascular plants. The Botanical Review. 54(4): 387-422. [80428]
  • 145. Hull, James C.; Scott, Ralph C. 1982. Plant succession on debris avalanches of Nelson County, Virginia. Castanea. 47(2): 158-176. [41715]
  • 148. Hunter, John C. 1995. Ailanthus altissima (Miller) Swingle: its biology and recent history. California Exotic Pest Plant Council News. 3(4): 4-5. [45846]
  • 151. Illick, Joseph S.; Brouse, E. F. 1926. The ailanthus tree in Pennsylvania. Bulletin 38. Harrisburg, PA: Pennsylvania Department of Forests and Waters. 29 p. [46734]
  • 159. Keeley, Jon E. 1981. Reproductive cycles and FIRE REGIMES. In: Mooney, H. A.; Bonnicksen, T. M.; Christensen, N. L.; Lotan, J. E.; Reiners, W. A., tech. coords. FIRE REGIMES and ecosystem properties: Proceedings of the conference; 1978 December 11-15; Honolulu, HI. Gen. Tech. Rep. WO-26. Washington, DC: U.S. Department of Agriculture, Forest Service: 231-277. [4395]
  • 160. Keeley, Jon E. 1986. Resilience of Mediterranean shrub communities to fires. In: Dell, B.; Hopkins, A. J. N.; Lamont B. B., eds. Resilience in Mediterranean-type ecosystems. Dordrecht, The Netherlands: Dr. W. Junk Publishers: 95-112. [9826]
  • 163. Kentucky Exotic Pest Plant Council. 2001. Invasive exotic plant list, [Online]. Southeast Exotic Pest Plant Council (Producer). Available: http://www.se-eppc.org/states/KY/KYlists.html [2005, April 13]. [44948]
  • 179. Lalhal, J. S.; Singh, Ombir. 1992. Sucker development in Ailanthus glandulosa Desf. Van Vigyan. Dehra Dun, India: Society of Indian Foresters. 30(3&4): 179-180. [46155]
  • 185. Lepart, J.; Debussche, M. 1991. Invasion processes as related to succession and disturbance. In: Groves, R. H.; Di Castri, F., eds. Biogeography of Mediterranean invasions. Cambridge: Cambridge University Press: 159-177. [46742]
  • 211. Miller, James H. 1990. Ailanthus altissima (Mill.) Swingle ailanthus. In: Burns, Russell M.; Honkala, Barbara H., tech. coords. Silvics of North America: Vol. 2. Hardwoods. Agriculture Handbook 654. Washington, DC: U.S. Department of Agriculture, Forest Service: 101-104. [46753]
  • 230. Pan, Elizabeth; Bassuk, Nina. 1985. Effects of soil type and compaction on the growth of Ailanthus altissima seedlings. Journal of Environmental Horticulture. 3(4): 158-162. [45476]
  • 269. Shaw, Nancy L.; Monsen, Stephen B.; Stevens, Richard. 2004. Rosaceous shrubs. In: Monsen, Stephen B.; Stevens, Richard; Shaw, Nancy L., comps. Restoring western ranges and wildlands. Gen. Tech. Rep. RMRS-GTR-136-vol-2. Fort Collins, CO: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 539-596. [52845]
  • 275. Southeast Exotic Pest Plant Council, Tennessee Chapter. 2001. Invasive exotic pest plants in Tennessee, [Online]. Athens, GA: University of Georgia; Southeast Exotic Pest Plant Council (Producer). Available: http://www.se-eppc.org/states/TN/TNIList.html [2004, February 12]. [46747]
  • 327. Zasada, John C.; Daouglas, D. A.; Buechler, W. 2008. Salix L.: willow. In: Bonner, Franklin T., Karrfalt, Robert P., eds. Woody plant seed manual. Agric. Handbook No. 727. Washington, DC: U.S. Department of Agriculture, Forest Service: 1000-1009. [79502]
  • 45. Call, Lara J. 2002. Analysis of intraspecific and interspecific interactions between the invasive exotic tree-of-heaven (Ailanthus altissima (Miller) Swingle) and the native black locust (Robinia pseudoacacia L.). Blacksburg, VA: Virginia Polytechnic Institute. 80 p. Thesis. [45299]
  • 65. Del Tredici, Peter. 2001. Sprouting in temperate trees: A morphological and ecological review. Botanical Review. 67(2): 121-140. [80429]
  • 85. Espenschied-Reilly, Amanada L.; Runkle, James R. 2008. Distribution and changes in abundance of Ailanthus altissima (Miller) Swingle in a southwest Ohio woodlot. Ohio Journal of Science. 108(2): 16-22. [79745]
  • 93. Feret, Peter P. 1985. Ailanthus: variation, cultivation, and frustration. Journal of Arboriculture. 11(12): 361-368. [46741]
  • 96. Ferguson, Robert B. 1983. Use of rosaceous shrubs for wildland plantings in the Intermountain West. In: Monsen, Stephen B.; Shaw, Nancy, comps. Managing Intermountain rangelands--improvement of range and wildlife habitats; Proceedings of symposia; 1981 September 15-17; Twin Falls, ID; 1982 June 22-24; Elko, NV. Gen. Tech. Rep. INT-157. Ogden, UT: U.S. Department of Agriculture, Forest Service, Intermountain Forest and Range Experiment Station: 136-149. [915]

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Regeneration Processes

More info for the term: breeding system

Tree-of-heaven reproduces by sprouting and from seed [71,135,312]. Both methods are important to tree-of-heaven's reproductive success and invasiveness [87,249].
  • 135. Hickman, James C., ed. 1993. The Jepson manual: Higher plants of California. Berkeley, CA: University of California Press. 1400 p. [21992]
  • 249. Rabe, Elizabeth Pan. 1985. Distribution and growth response of Ailanthus altissima in the urban environment. Ithaca, NY: Cornell University. 87 p. Thesis. [45753]
  • 312. Voss, Edward G. 1985. Michigan flora. Part II. Dicots (Saururaceae--Cornaceae). Bulletin 59. Bloomfield Hills, MI: Cranbrook Institute of Science; Ann Arbor, MI: University of Michigan Herbarium. 724 p. [11472]
  • 71. Diggs, George M., Jr.; Lipscomb, Barney L.; O'Kennon, Robert J. 1999. Illustrated flora of north-central Texas. Sida Botanical Miscellany, No. 16. Fort Worth, TX: Botanical Research Institute of Texas. 1626 p. [35698]
  • 87. Evans, C. W.; Moorhead, D. J.; Bargeron, C. T.; Douce, G. K. 2006. Invasive plant responses to silvicultural practices in the South. Bugwood Network BW-2006-03. Tifton, GA: The University of Georgia Bugwood Network. 52 p. Available online: http://www.invasive.org/silvicsforinvasives.pdf. [72425]

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Growth Form (according to Raunkiær Life-form classification)

More info on this topic.

More info for the terms: geophyte, phanerophyte

Raunkiaer [254] life form:
Phanerophyte
Geophyte
  • 254. Raunkiaer, C. 1934. The life forms of plants and statistical plant geography. Oxford: Clarendon Press. 632 p. [2843]

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Life Form

More info for the term: tree

Tree

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Fire Regime Table

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Reaction to Competition

Ailanthus is a successional  pioneer species, intolerant of shade (8). It competes  successfully in mixed stands of hardwoods throughout its range,  indicating that it was present at the start of stand  establishment.

    Allelopathic effects on over 35 species of hardwoods and 34  species of conifers have been demonstrated for water extracts of  ailanthus leaves (14). Only white ash (Fraxinus  americana) was not adversely affected. Germination and growth  of slashand Monterey pines (Pinus elliottii and  P radiata) were inhibited by scattering leaves of  ailanthus collected in June and July on the seed bed surface,  while leaves collected in October stimulated germination and  growth (22). Such studies point to a strong allelopathic  role for ailanthus in forest succession.

  • Burns, Russell M., and Barbara H. Honkala, technical coordinators. 1990. Silvics of North America: 1. Conifers; 2. Hardwoods.   Agriculture Handbook 654 (Supersedes Agriculture Handbook 271,Silvics of Forest Trees of the United States, 1965).   U.S. Department of Agriculture, Forest Service, Washington, DC. vol.2, 877 pp.   http://www.na.fs.fed.us/spfo/pubs/silvics_manual/table_of_contents.htm External link.
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James H. Miller

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Rooting Habit

Ailanthus roots are shallow spreading,  often apparent at the soil surface, and roots near the trunk  thicken into enlarged storage structures. These large rounded  structures are assumed to be for water storage, contributing to  the drought hardiness of the species (4). There is a general  absence of a taproot with most roots present in the upper 46 cm  (18 in) of soil. Within this zone, the deeper roots send numerous  small roots to the surface. Adventitious shoots may arise from  any of the surface roots.

  • Burns, Russell M., and Barbara H. Honkala, technical coordinators. 1990. Silvics of North America: 1. Conifers; 2. Hardwoods.   Agriculture Handbook 654 (Supersedes Agriculture Handbook 271,Silvics of Forest Trees of the United States, 1965).   U.S. Department of Agriculture, Forest Service, Washington, DC. vol.2, 877 pp.   http://www.na.fs.fed.us/spfo/pubs/silvics_manual/table_of_contents.htm External link.
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Life History and Behavior

Cyclicity

Phenology

More info on this topic.

More info for the terms: allelopathy, phenology, schizocarp, tree

Leaf expansion typically begins in early spring, with trees-of-heaven flowering and dispersing pollen in late spring [148,211]. Tree-of-heaven's seasonal development may sometimes be slower than associated woody species. On Nantucket Island, Massachusetts, tree-of-heaven was noted in a 1912 publication as "nearly naked" in early June, when other tree species had already leafed out [26]. Seed ripening begins in late summer and continues through fall. Schizocarps usually persist on female trees through winter [198,211], but they may disperse anytime from October through the next spring [211]. In New York, schizocarp clusters usually broke off in fall, while individual schizocarps often persisted until spring [230].

Tree-of-heaven phenology by state and region
Area Event Time
Arkansas flowers April-May
fruits September-spring [147]
California flowers May
seeds ripen September-October [149]
Carolinas flowers late May-early June
fruits July-October [250]
Florida flowers spring [324]
Illinois flowers June-July [214]
New Jersey seeds disperse October-early April;
about half disperse October-November [181]
New Mexico flowers June-July [199]
New York seeds germinate June
seeds disperse October-April  [249]
Texas flowers April-May
fruits September-October[308]
West Virginia flowers June-July [280]
fruits late October-early April;
most dispersal October-November [180]
Great Plains flowers mid-May-June [114]
New England fruits mid-August-mid-October [267]
Pacific Northwest flowers June-July [137]
Southeast flowers May-July [82]

Seasonally, tree-of-heaven's allelopathic toxins are greatest in spring and decline as the growing season progresses [311]. See Impacts and Control for more information on allelopathy.

  • 114. Great Plains Flora Association. 1986. Flora of the Great Plains. Lawrence, KS: University Press of Kansas. 1392 p. [1603]
  • 137. Hitchcock, C. Leo; Cronquist, Arthur; Ownbey, Marion; Thompson, J. W. 1961. Vascular plants of the Pacific Northwest. Part 3: Saxifragaceae to Ericaceae. Seattle, WA: University of Washington Press. 614 p. [1167]
  • 147. Hunter, Carl G. 1989. Trees, shrubs, and vines of Arkansas. Little Rock, AR: The Ozark Society Foundation. 207 p. [21266]
  • 148. Hunter, John C. 1995. Ailanthus altissima (Miller) Swingle: its biology and recent history. California Exotic Pest Plant Council News. 3(4): 4-5. [45846]
  • 149. Hunter, John. 2000. Ailanthus altissima (Miller) Swingle. In: Bossard, Carla C.; Randall, John M.; Hoshovsky, Marc C., eds. Invasive plants of California's wildlands. Berkeley, CA: University of California Press: 32-36. [46752]
  • 180. Landenberger, Rick E.; Kota, Nathan L.; McGraw, James B. 2007. Seed dispersal of the non-native invasive tree Ailanthus altissima into contrasting environments. Plant Ecology. 192(1): 55-70. [69766]
  • 181. Landenberger, Rick E.; Warner, Timothy A.; McGraw, James B. 2009. Spatial patterns of female Ailanthus altissima across an urban-to-rural land use gradient. Urban Ecosystems. 12(4): 437-448. [79727]
  • 198. Martin, Patrick H.; Canham, Charles D. 2010. Dispersal and recruitment limitation in native versus exotic tree species: life-history strategies and Janzen-Connell effects. Oikos. 119(5): 807-824. [79723]
  • 199. Martin, William C.; Hutchins, Charles R. 1981. A flora of New Mexico. Volume 2. Germany: J. Cramer. 2589 p. [37176]
  • 211. Miller, James H. 1990. Ailanthus altissima (Mill.) Swingle ailanthus. In: Burns, Russell M.; Honkala, Barbara H., tech. coords. Silvics of North America: Vol. 2. Hardwoods. Agriculture Handbook 654. Washington, DC: U.S. Department of Agriculture, Forest Service: 101-104. [46753]
  • 214. Mohlenbrock, Robert H. 1986. [Revised edition]. Guide to the vascular flora of Illinois. Carbondale, IL: Southern Illinois University Press. 507 p. [17383]
  • 230. Pan, Elizabeth; Bassuk, Nina. 1985. Effects of soil type and compaction on the growth of Ailanthus altissima seedlings. Journal of Environmental Horticulture. 3(4): 158-162. [45476]
  • 249. Rabe, Elizabeth Pan. 1985. Distribution and growth response of Ailanthus altissima in the urban environment. Ithaca, NY: Cornell University. 87 p. Thesis. [45753]
  • 250. Radford, Albert E.; Ahles, Harry E.; Bell, C. Ritchie. 1968. Manual of the vascular flora of the Carolinas. Chapel Hill, NC: The University of North Carolina Press. 1183 p. [7606]
  • 26. Bicknell, Eugene P. 1912. The ferns and flowering plants of Nantucket--X. Bulletin of the Torrey Botanical Club. 39(9): 415-428. [77402]
  • 267. Seymour, Frank Conkling. 1982. The flora of New England. 2nd ed. Phytologia Memoirs 5. Plainfield, NJ: Harold N. Moldenke and Alma L. Moldenke. 611 p. [7604]
  • 280. Strausbaugh, P. D.; Core, Earl L. 1977. Flora of West Virginia. 2nd ed. Morgantown, WV: Seneca Books. 1079 p. [23213]
  • 308. Vines, Robert A. 1960. Trees, shrubs, and woody vines of the Southwest. Austin, TX: University of Texas Press. 1104 p. [7707]
  • 311. Voigt, Garth K.; Mergen, Francois. 1962. Seasonal variation in toxicity of Ailanthus leaves to pine seedlings. Botanical Gazette. 123(4): 262-265. [46735]
  • 324. Wunderlin, Richard P. 1998. Guide to the vascular plants of Florida. Gainesville, FL: University Press of Florida. 806 p. [28655]
  • 82. Duncan, Wilbur H.; Duncan, Marion B. 1988. Trees of the southeastern United States. Athens, GA: The University of Georgia Press. 322 p. [12764]

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Flower/Fruit

Fl. Per.: May-June Fr. Per.: July-August.
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Life Cycle

Persistence: PERENNIAL, DECIDUOUS

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Reproduction

Ailanthus reproduces both sexually and asexually. Asexual reproduction is by vegetative sprouting from stumps or root portions (Hu 1979). Flowering occurs rather late in the spring (June). Ailanthus has the longest winter dormancy of all the trees in its native Chinese habitat (Hu 1979). Precocious flowering is not a rare occurrence in this species and has been observed in seedlings only 6 weeks after germination (Feret 1973).

Seeds ripen in large crowded clusters from September to October of the same year and may persist on the tree through the following winter (Little 1974, Hu 1979). An individual tree can produce 325,000 seeds per year which are easily wind-dispersed (Bory and Clair-Maczulajtys 1980). These seeds average over 30,000 per kilogram. This amount yields up to 6-7000 "usable plants" (Little 1974). Limited testing of ailanthus seeds indicate that they have dormant embryos, and that germination is benefited by stratification on moist sand for 60 days at 41 F (Little 1974).

Seedlings establish themselves rapidly by producing a well formed tap root in less than three months (Adamik and Brauns 1957). In more compacted soils these seedlings put forth long rope-like lateral roots to exploit a greater soil volume (Rabe and Bassuk 1984). Ailanthus grows quickly in full sunlight and averages a meter of growth in height per year for at least the first 4 years (Adamik and Brauns 1957). The trees may grow to 15-20 meters tall but have a rather short lifespan of less than 50 years (Adamik 1955).

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Biology and Spread

Tree-of-heaven reproduces both sexually (by seeds) and asexually through vegetative sprouting. Flowering occurs late in the spring. Ailanthus is dioecious, with male and female flowers on separate plants. The fruits, or samaras, occur in terminal clusters on female plants during the summer, and may persist on the tree through the winter. One study reports that an individual tree can produce as many as 325,000 seeds per year. Established trees also produce numerous suckers from the roots and resprout vigorously from cut stumps and root fragments.

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Vegetative Reproduction

The dense thickets of ailanthus  reproduction on disturbed soils of road cuts and city building  sites develop from root sprouts. Prolific root and stump  sprouting has discouraged use of ailanthus as an ornamental  species. After death or injury of the main stem the  wide-spreading shallow root system can give rise to an abundance  of sprouts. Sprouts have shown first-year height growth of 3 to 4  m (10 to 13 ft) (19). Thus, the species can be easily  propagated from either root cuttings or from coppicing.

  • Burns, Russell M., and Barbara H. Honkala, technical coordinators. 1990. Silvics of North America: 1. Conifers; 2. Hardwoods.   Agriculture Handbook 654 (Supersedes Agriculture Handbook 271,Silvics of Forest Trees of the United States, 1965).   U.S. Department of Agriculture, Forest Service, Washington, DC. vol.2, 877 pp.   http://www.na.fs.fed.us/spfo/pubs/silvics_manual/table_of_contents.htm External link.
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Seedling Development

Seeds, can be sown immediately upon  ripening or stratified until spring. In nurseries, seeds are  usually sown in the spring and seedlings transplanted early the  following spring. Germination is epigeal. Vigorous first-year  seedling growth of 1 to 2 m (3.3 to 6.6 ft) has been reported  (1,11). Average survival on 11 different plantings in  Indiana strip mines was 74 percent after the first growing  season and then decreased to 58 percent after the first winter  (5). This illustrates the winter damage and mortality frequently  reported (1,7).

    Because ailanthus is intolerant of shade, reproduction in natural  stands appears sparse and erratic except by sprouting.

  • Burns, Russell M., and Barbara H. Honkala, technical coordinators. 1990. Silvics of North America: 1. Conifers; 2. Hardwoods.   Agriculture Handbook 654 (Supersedes Agriculture Handbook 271,Silvics of Forest Trees of the United States, 1965).   U.S. Department of Agriculture, Forest Service, Washington, DC. vol.2, 877 pp.   http://www.na.fs.fed.us/spfo/pubs/silvics_manual/table_of_contents.htm External link.
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Seed Production and Dissemination

Pollination occurs in  the spring and clusters of seed ripen from September to October.  The fruit is a samara with the seed in the center of a thin,  oblong wing, well adapted for wind dispersal. The ripe samaras  are greenish yellow or reddish brown. The seed usually persists  on the female tree through the winter, characterizing their  appearance, but can be dispersed any time from October to the  following spring. The species is a prolific seeder; the most  abundant seed production is from trees that are 12 to 20 years.

    After collection, seeds should be spread to air-dry. Number of  seeds per kilogram averages from 27,000 to 33,000 (12,235 to  14,970lb) and germination after cold stratification averages 65  to 85 percent (7,18). Seeds should be stored dry in  sealed containers. The recommended cold stratification is 50 C  (410 F) in moist sand for 60 days.

  • Burns, Russell M., and Barbara H. Honkala, technical coordinators. 1990. Silvics of North America: 1. Conifers; 2. Hardwoods.   Agriculture Handbook 654 (Supersedes Agriculture Handbook 271,Silvics of Forest Trees of the United States, 1965).   U.S. Department of Agriculture, Forest Service, Washington, DC. vol.2, 877 pp.   http://www.na.fs.fed.us/spfo/pubs/silvics_manual/table_of_contents.htm External link.
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Flowering and Fruiting

The yellowish-green flowers of  ailanthus appear from mid-April to July, south to north,  depending on latitude. The flowers are arranged in large panicles  at the ends of new shoots. A dioecious species, it bears male and  female flowers on different trees, with male trees producing  three to four times more flowers than are usually found on female  trees (11). Male flowers are more conspicuous than female  ones, emitting a disagreeable odor that attracts numerous  insects. The foul odor of the male flowers makes the tree less  favored for ornamental plantings in cities.

  • Burns, Russell M., and Barbara H. Honkala, technical coordinators. 1990. Silvics of North America: 1. Conifers; 2. Hardwoods.   Agriculture Handbook 654 (Supersedes Agriculture Handbook 271,Silvics of Forest Trees of the United States, 1965).   U.S. Department of Agriculture, Forest Service, Washington, DC. vol.2, 877 pp.   http://www.na.fs.fed.us/spfo/pubs/silvics_manual/table_of_contents.htm External link.
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James H. Miller

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Growth

More info for the terms: density, ramet, tree

The tree-of-heaven embryo is well equipped for rapid growth. Although it lacks an endosperm, it has 2 large cotyledons with stored oils that provide energy for emergence and early growth [104,175,197,211,328]. Whether initial regeneration is accomplished from seed or by cloning, tree-of-heaven usually grows quickly on favorable sites. It is among the fastest-growing trees in North America [166,244,259]. Both the common name (tree-of-heaven) and the scientific name (Ailanthus, sky-tree) refer to the species' ability to attain height quickly [71,308]. In the eastern United States, tree-of-heaven's annual growth rate averaged 6 feet (1.8 m) for bole sprouts, 2.7 feet (0.8 m) for root sprouts, and 1.3 feet (6.5 m) for seedlings [151]. Root sprouts in California may exceed 3.5 feet (1 m) in their 1st year [148]. Tree-of-heaven sprouts generally grow faster than seedlings, although seedlings often grow 3.3 to 6.6 feet (1-2 m) in their 1st year [211]. A fact sheet states that tree-of-heaven may reach 80 feet (20 m) tall and 6 feet (2 m) in diameter in 10 years [87]. Two years after planting in a New York City common garden, height growth of tree-of-heaven seedlings was at least 3 times that of native sweetgum (Liquidambar styraciflua) and nonnative Norway maple seedlings [230].

Mean seedling stem and root growth of 3 tree species after 3 years in a common garden [230]
Species

Stem length (cm)

Lateral root length (cm)

Mean Minimum/ maximum Mean Minimum/ maximum
tree-of-heaven 82.2 31/ 172 114.4 53/ 200
sweetgum 51.0 12/ 77 23.8 2/ 46
Norway maple 36.1 23/ 49 33.2 14/ 66

Even with its rapid height growth, tree-of-heaven may concentrate early growth in roots. A greenhouse study showed tree-of-heaven seedlings had higher root:shoot ratios than native sweetgum, American sycamore (Platanus occidentalis), and nonnative princesstree seedlings; this was true whether tree-of-heaven was grown in disturbed soils that lacked organic matter or in soils collected from mixed-hardwood forests left undisturbed for ≥50 years [215,216].

Tree-of-heaven saplings may average 3 feet (1 m) of height growth per year for at least 4 years [1]. Relatively rapid growth continued into the pole size class in New York: pole-sized trees-of-heaven growing in canopy gaps gained 2 to 4 mm of radial growth annually, the highest rate of 6 tree species measured (the other 5 species were native) [166]. In a New England survey, trees-of-heaven reached 33 to 49 feet (10-15 m) in height and 3.7 to 4.3 inches (9-11 cm) DBH in 30 years [1], and a 55-year-old tree on the George Washington National Forest, West Virginia, had a DBH of 15 inches (37 cm) [247]. In North America, growth is usually fastest for trees-of-heaven in California's mediterranean climate. Trees in the Central Valley have an 8-month growing season, so those trees may be 35 to 63 feet (10-20 m) tall by 12 to 20 years of age [149]. In Pennsylvania, growth slowed greatly after age 20 to 25, with height increases of 3 inches (7.6 cm) or less per year [151].

Once established, tree-of-heaven density increases by root sprouting. One ramet may occupy over 1 acre (0.4 ha). Sprout growth slows to several centimeters per year if sprouts become shaded [149]. In West Virginia, Kowarik [173] reported an average growth rate of 0.36 foot/year (0.11 m) for tree-of-heaven sprouts suppressed in the understory of an oak (Quercus spp.)-sugar maple forest.

Browsing and/or unfavorable site conditions can reduce tree-of-heaven growth. Cattle, deer, and small rodent browsing may slow tree-of-heaven establishment and growth [229]. Browsing effects may vary with animal density and by site. In a New York oak-hickory woodland, Forgione [99] found no significant differences in tree-of-heaven seedling establishment on open plots and plots with white-tailed deer exclosures. On Mediterranean islands of Spain, France, and Greece, tree-of-heaven clones on intermittent streams were significantly smaller than those on old fields and roadsides (P=0.022), and clones at relatively high elevations were larger than those at low elevations (P=0.004) [292].

  • 1. Adamik, Karl; Brauns, Friedrich E. 1957. Ailanthus glandulosa (tree-of-heaven) as pulpwood. Part II. Tappi. 40(7): 522-527. [46739]
  • 104. Gleason, Henry A.; Cronquist, Arthur. 1991. Manual of vascular plants of northeastern United States and adjacent Canada. 2nd ed. New York: New York Botanical Garden. 910 p. [20329]
  • 148. Hunter, John C. 1995. Ailanthus altissima (Miller) Swingle: its biology and recent history. California Exotic Pest Plant Council News. 3(4): 4-5. [45846]
  • 149. Hunter, John. 2000. Ailanthus altissima (Miller) Swingle. In: Bossard, Carla C.; Randall, John M.; Hoshovsky, Marc C., eds. Invasive plants of California's wildlands. Berkeley, CA: University of California Press: 32-36. [46752]
  • 151. Illick, Joseph S.; Brouse, E. F. 1926. The ailanthus tree in Pennsylvania. Bulletin 38. Harrisburg, PA: Pennsylvania Department of Forests and Waters. 29 p. [46734]
  • 166. Knapp, Liza B.; Canham, Charles D. 2000. Invasion of an old-growth forest in New York by Ailanthus altissima: sapling growth and recruitment in canopy gaps. Journal of the Torrey Botanical Society. 127(4): 307-315. [46142]
  • 173. Kowarik, Ingo. 1995. Clonal growth in Ailanthus altissima on a natural site in West Virginia. Journal of Vegetation Science. 6: 853-856. [45195]
  • 175. Kozlowski, T. T. 2002. Physiological ecology of natural regeneration of harvested and disturbed forest stands: implications for forest management. Forest Ecology and Management. 158(1-3): 195-221. [42122]
  • 197. Marshall, P. E.; Kozlowski, T. T. 1973. Cotyledon inactivation and early seedling development. American Journal of Botany. 60(4): 25-26. [46135]
  • 211. Miller, James H. 1990. Ailanthus altissima (Mill.) Swingle ailanthus. In: Burns, Russell M.; Honkala, Barbara H., tech. coords. Silvics of North America: Vol. 2. Hardwoods. Agriculture Handbook 654. Washington, DC: U.S. Department of Agriculture, Forest Service: 101-104. [46753]
  • 215. Moore, James E. 2006. Effects of soil type and soil moisture on the germination and establishment of exotic and native trees of the North Carolina Piedmont. Greensboro, NC: The University of North Carolina. 48 p. Thesis. [72014]
  • 216. Moore, James E.; Lacey, Elizabeth P. 2009. A comparison of germination and early growth of four early successional tree species of the southeastern United States in different soil and water regimes. The American Midland Naturalist. 162(2): 388-394. [79718]
  • 229. Ostfeld, Richard S.; Manson, Robert H.; Canham, Charles D. 1997. Effects of rodents on survival of tree seeds and seedlings invading old fields. Ecology. 78(5): 1531-1542. [46148]
  • 230. Pan, Elizabeth; Bassuk, Nina. 1985. Effects of soil type and compaction on the growth of Ailanthus altissima seedlings. Journal of Environmental Horticulture. 3(4): 158-162. [45476]
  • 244. Petrides, G. A.; Peterson, Roger Troy. 1986. A field guide to North American trees and shrubs: Northeastern and north-central United States and southeastern and south-central Canada. 2nd ed. Boston: Houghton Mifflin. 428 p. [46760]
  • 247. Pomp, Jonathan A. 2008. Disturbances, prescribed fire, and invasion by exotic plants in a xeric mixed-oak and oak-pine dominated area of the ridge and valley in eastern West Virginia. Morgantown, WV: West Virginia University. 173 p. Thesis. [79748]
  • 259. Sachs, R. M.; Low, C. B. 1983. Yields in high density, short rotation intensive culture (SRIC)-- plantations of Eucalyptus and other hardwood species. In: Standiford, Richard B.; Ledig, F. Thomas, technical coordinators. Proceedings of a workshop on Eucalyptus in California; 1983 June 14-16; Sacramento, CA. Gen. Tech. Rep. PSW-69. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station: 71-75. [19574]
  • 292. Traveset, Anna; Brundu, Giuseppe; Carta, Luisa; Mprezetou, Irene; Lambdon, Philip; Manca, Manuela; Medail, Frederic; Moragues, Eva; Rodrguez-Perez, Javier; Siamantziouras, Akis-Stavros D.; Suehs, Carey M.; Troumbis, Andreas Y.; Vila, Montserrat; Hulme, P. 2008. Consistent performance of invasive plant species within and among islands of the Mediterranean basin. Biological Invasions. 10(6): 847-858. [79731]
  • 308. Vines, Robert A. 1960. Trees, shrubs, and woody vines of the Southwest. Austin, TX: University of Texas Press. 1104 p. [7707]
  • 328. Zasada, John C.; Little, Silas. 2008. Ailanthus altissima (P. Mill.) Swingle: ailanthus. In: Bonner, Franklin T., Karrfalt, Robert P., eds. Woody plant seed manual. Agric. Handbook No. 727. Washington, DC: U.S. Department of Agriculture, Forest Service: 224-226. [46269]
  • 71. Diggs, George M., Jr.; Lipscomb, Barney L.; O'Kennon, Robert J. 1999. Illustrated flora of north-central Texas. Sida Botanical Miscellany, No. 16. Fort Worth, TX: Botanical Research Institute of Texas. 1626 p. [35698]
  • 87. Evans, C. W.; Moorhead, D. J.; Bargeron, C. T.; Douce, G. K. 2006. Invasive plant responses to silvicultural practices in the South. Bugwood Network BW-2006-03. Tifton, GA: The University of Georgia Bugwood Network. 52 p. Available online: http://www.invasive.org/silvicsforinvasives.pdf. [72425]
  • 99. Forgione, Helen M. 1993. Limits to the establishment and growth of tree-of-heaven explored. Restoration & Management Notes. 11(1): 70-71. [22459]

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Growth and Yield

Information on the growth and yield of  ailanthus in the United States at this time is lacking. Maximum  heights are often reported as 17 to 27 m (56 to 90 ft) and a  maximum d.b.h. as 100 cm (40 in) (10,12). A short-lived  species, it lives 30 to 50 years (20). On arid sites, 15  m (50 ft) or more of height growth can be reached in 25 years,  with a straight bole for 10 to 12 m (33 to 40 ft) (7). At a New  England location, trees reached a 10 to 15 m (33 to 49 ft) height  and 9 to 11 cm (3.7 to 4.3 in) d.b.h. in 30 years (11).

  • Burns, Russell M., and Barbara H. Honkala, technical coordinators. 1990. Silvics of North America: 1. Conifers; 2. Hardwoods.   Agriculture Handbook 654 (Supersedes Agriculture Handbook 271,Silvics of Forest Trees of the United States, 1965).   U.S. Department of Agriculture, Forest Service, Washington, DC. vol.2, 877 pp.   http://www.na.fs.fed.us/spfo/pubs/silvics_manual/table_of_contents.htm External link.
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Molecular Biology and Genetics

Genetics

In the two centuries since its introduction into North America,  ailanthus has probably become differentiated into genetically  different subpopulations based on seed traits. Seed  characteristics of ailanthus have been identified as traits that  differentiate varieties and geographical strains. Ailanthus with  bright red samaras compared to the more common greenish yellow  has been named Ailanthus altissima var. erythrocarpa  (Carr.) Rehd. A study of 11 seed sources from California and  Eastern States found that seed width and weight were correlated  with latitude (6). Northern sources have wider, heavier seed than  the more southern sources.

  • Burns, Russell M., and Barbara H. Honkala, technical coordinators. 1990. Silvics of North America: 1. Conifers; 2. Hardwoods.   Agriculture Handbook 654 (Supersedes Agriculture Handbook 271,Silvics of Forest Trees of the United States, 1965).   U.S. Department of Agriculture, Forest Service, Washington, DC. vol.2, 877 pp.   http://www.na.fs.fed.us/spfo/pubs/silvics_manual/table_of_contents.htm External link.
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Molecular Biology

Barcode data: Ailanthus altissima

The following is a representative barcode sequence, the centroid of all available sequences for this species.


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Statistics of barcoding coverage: Ailanthus altissima

Barcode of Life Data Systems (BOLDS) Stats
Public Records: 10
Specimens with Barcodes: 19
Species With Barcodes: 1
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Conservation

Conservation Status

National NatureServe Conservation Status

Canada

Rounded National Status Rank: NNA - Not Applicable

United States

Rounded National Status Rank: NNA - Not Applicable

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NatureServe Conservation Status

Rounded Global Status Rank: GNR - Not Yet Ranked

Reasons: Native to central China and widely planted, it now occurs in practically every state of the United States, and from Canada to Argentina, and is also escaped in Europe. Distribution and abundance in native range not known.

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Tree-of-heaven is classified as a noxious or invasive plant on National Forest System lands [298,300] and in many states. Information on state-level noxious weed status of plants in the United States is available at Plants Database.
  • 298. U.S. Department of Agriculture, Forest Service, Eastern Region. 2004. Eastern Region invasive plants ranked by degree of invasiveness as based on information from states, [Online]. In: Noxious weeds and non-native invasive plants. Section 3: Invasive plants. Milwaukee, WI: Eastern Region (Producer). Available: http://www.fs.fed.us/r9/wildlife/range/weed/Sec3B.htm [2010, November 10]. [46748]
  • 300. U.S. Department of Agriculture, Forest Service, Southern Region. 2001. Regional invasive exotic plant species list, [Online]. In: Regional Forester's list and ranking structure: invasive exotic plant species of management concern. In: Invasive plants of southern states list. Southeast Exotic Pest Plant Council (Producer). Available: http://www.se-eppc.org/fslist.cfm [2003, August 25]. [44944]

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Global Short Term Trend: Increase of 10 to >25%

Comments: Trend in native range in China not known, but the species has become much more abundant globally in the past century.

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Threats

Comments: Although only occasionally found in nondisturbed areas (Kowarik 1983), ailanthus is a prolific seed producer, grows rapidly and can successfully compete with the native vegetation. It produces toxins which prevent the establishment of other species (Mergen 1959). The root system is aggressive enough to cause damage to sewers and foundations (Hu 1979).

Ailanthus was not nominated by any specific preserve manager, but is recognized by TNC staff as an important exotic weed. A recent survey (2 March 1985) of CNPS members showed a wide distribution of this tree throughout California. Members of both the Mt. Lassen and Sequoia chapters consider it a major pest at low elevations. There are also reports of it growing in Santa Cruz, Riverside, San Bernardino, Los Angeles and San Diego counties.

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Management

Restoration Potential: Recovery potential is unknown.

Management Requirements: Weed control involves three fundamental objectives: prevention, eradication and control.

From a practical viewpoint, methods of weed management are commonly categorized under the following categories: physical, thermal, managerial, biological, and chemical (Watson 1977). Physical methods include both manual and mechanical methods. Thermal methods include both broadcast burning or spot treatment with a flame thrower. Managerial methods include the encouragement of competitive displacement by native plants and prescribed grazing. Biological control is usually interpreted as the introduction of insects or pathogens which are highly selective for a particular weed species. Chemical control includes both broadcast and spot application.

The most desirable approach is that of an integrated pest management plan. This involves the optimum use of all control strategies to control weeds. This approach is generally accepted as the most effective, economical, and environmentally sound long-term pest control strategy (Watson 1977). In cases where more than one control technique is used, the various techniques should be compatible with one another. Broadcast herbicide application, for example, may not work well with certain managerial techniques (i.e., plant competition).

PHYSICAL CONTROL. The two types of physical control methods discussed below, manual and mechanical, produce slash (i.e., cutting debris) that can be disposed of by several techniques. If cut before seeds are produced it may be piled and left for enhancement of wildlife habitat (i.e., cover for small mammals). Debris may be fed through a mechanical chipper and used as mulch during revegetation procedures. Care should be taken to prevent vegetative reproduction from cuttings. Burning the slash piles is also effective in disposing of slash.

MANUAL CONTROL. Manual methods use hand labor to remove undesirable vegetation. These methods are highly selective and permit weeds to be removed without damage to surrounding native vegetation.

Hand Pulling: Ailanthus is probably best controlled by manual removal of young seedlings. Seedlings are best pulled after a rain when the soil is loose. This facilitates removal of the rooting system, which may resprout if left in the ground. After the tap root has developed, this would be extremely difficult. Plants should be pulled as soon as they are large enough to grasp but before they produce seeds.

The Bradley Method is one sensible approach to manual control of weeds (Fuller and Barbe 1985). This method consists of hand weeding selected small areas of infestation in a specific sequence, starting with the best stands of native vegetation (those with the least extent of weed infestation) and working towards those stands with the worst weed infestation. Initially, weeds that occur singly or in small groups should be eliminated from the extreme edges of the infestation. The next areas to work on are those with a ratio of at least two natives to every weed. As the native plant stabilizes in each cleared area, work deeper into the center of the most dense weed patches. This method has great promise on nature reserves with low budgets and with sensitive plant populations. More detailed information is contained in Fuller and Barbe (1985).

Cutting: Manually operated tools such as brush cutters, power saws, axes, machetes, loppers and clippers can be used to cut ailanthus. This is an important step before many other methods are tried, as it removes the above-ground portion of the plant. For thickly growing, multi-stemmed shrubs and trees, access to the base of the plant may not only be difficult but dangerous where footing is uncertain.

Hand Digging: The removal of rootstocks by hand digging is a slow but sure way of destroying weeds which resprout from their roots. The work must be thorough to be effective as every piece of root that breaks off and remains in the soil may produce a new plant. Such a technique is only suitable for small infestations and around trees and shrubs where other methods are not practical.

Girdling: Girdling involves manually cutting away bark and cambial tissues around the trunks of undesirable trees such as ailanthus. This is a relatively inexpensive method and is done with an ordinary ax in the spring when the trees are actively growing. Hardwoods are known to resprout below the girdle unless the cut is treated with herbicides. Although it may be undesirable to leave standing dead trees in an area, this technique has been shown to reduce stump sprouting in live oaks, and may be a useful technique for controlling ailanthus.

MECHANICAL CONTROL. Mechanical methods use mechanized equipment to remove above ground vegetation. These methods are often non-selective in that all vegetation on a treated site is affected. Mechanical control is highly effective at controlling woody vegetation on gentle topography with few site obstacles such as rocks, stumps or logs. Most mechanical equipment is not safe to operate on slopes over 30 percent. It is also of limited use where soils are highly susceptible to compaction or erosion or where excessive soil moisture is present. Site obstacles such as rocks, stumps or logs also reduce efficiency.

Chopping, Cutting or Mowing: Saplings may be trimmed back by tractor-mounted mowers on even ground or by scythes on rough or stony ground. Unwanted vegetation can be removed faster and more economically in these ways than by manual means and with less soil disturbance than with scarification. However, these methods are non-selective weed eradication techniques. They reduce the potential for biological control through plant competition and open up new niches for undesirable vegetation. In addition, wildlife forage is eliminated.

Saplings usually require several cuttings before the underground parts exhaust their reserve food supply. If only a single cutting can be made, the best time is when the plants begin to flower. At this stage the reserve food supply in the roots has been nearly exhausted, and new seeds have not yet been produced. After cutting or chopping with mechanical equipment, ailanthus resprouts from root crowns in greater density if not treated with herbicides.

PRESCRIBED BURNING. A flame thrower or weed burner device can be used as a spot treatment to heat-girdle the lower stems of small trees. This technique has advantages of being less costly than basal and stem herbicide treatments and is suitable for use during wet weather and snow cover. Ailanthus resprouts after heat-girdling (Cozzo 1972).

MANAGERIAL CONTROL. In most cases ailanthus prevents the establishment of other native plants and must be initially removed. Following physical or thermal removal of mature plants, root crowns must be treated to prevent resprouting. Seedlings of native plant species usually cannot establish fast enough to compete with sprout growth from untreated stumps. Ailanthus is shade tolerant, so presumably can and will sprout under other plants.

Prescribed grazing: The continued removal of the tops of seedlings and resprouts by grazing animals prevents seed formation and also gradually weakens the underground parts. Grazing must be continued until the seedbank is eliminated, as the suppressed plants return quickly after livestock is removed and begin to dominate pastures again.

BIOLOGICAL CONTROL. The term "biological control" is used here to refer to the use of insects or pathogens to control weeds. The introduction of exotic natural enemies to control plants is a complex process and must be thoroughly researched before implementation to prevent biological disasters. Such tools are not normally suitable for preserve managers to implement.

Biological control of ailanthus has not been addressed to any extent beyond the anecdotal stage. No susceptibilty of ailanthus to parasites was found or noticed in Austrian nurseries (Adamik and Brauns 1957). French (1972) notes that the zonate leafspot (Cristulariella pyramidalis) causes defoliation of ailanthus in Florida. In India, Atteva fabricella is considered an ailanthus defoliator (Misra 1978) and Italian seedlings, weakened by cold, were weakly parasitized by the fungus Placosphaeria spp. (Magnani 1975).

Please notify the California Field office of The Nature Conservancy of any field observations in which a native insect or pathogen is seen to have detrimental effects on ailanthus. These reports will be used to update this Element Stewardship Abstract. Management techniques which may encourage the spread of species-specific agents may be desirable in controlling ailanthus.

CHEMICAL CONTROL. Methods of chemical control of ailanthus are poorly explored in the literature. Detailed information on herbicides in general is available in such publications as Weed Science Society of America (1983). The Weed Science Society reference gives specific or USDA (1984) information on nomenclature, chemical and physical properties of the pure chemical, use recommendations and precautions, physiological and biochemical behavior, behavior in or on soils and toxological properties for several hundred chemicals. Comprehensive coverage of this information will not be presented in this Element Stewardship Abstract. In applying herbicides it is recommended that a dye be used in the chemical mixture to mark the treated plants and thus minimize waste.

The following discussion highlights herbicide application methods which may be useful in controlling ailanthus. Herbicides may be applied non-selectively (i.e., broadcast applications) or selectively (i.e., spot applications). Both types of applications have advantages and disadvantages and will be discussed separately.

Broadcast Herbicide Application: In general, when using broadcast application methods, plants should be sprayed only when in full leaf. Results are poor prior to full leaf development. The best results have been obtained when plants are in the fruiting stage in late summer or early autumn (Mathews 1960).

Kolarvskij (1967) reports that 2,4-D can stop seedling growth in alianthus, and Sterrett et al. (1971) found that a mixture of 2- chloroethyl phosphoric acid and potassium iodide gives 80-100% defoliation of ailanthus within 3 weeks.

Spot Chemical Methods: Spot chemical methods consist of various techniques for manually applying herbicides to individual plants or small clumps of plants (such as stump resprouts). These methods are highly selective as only specific plants are treated. They are most efficient when the density of stems to be treated is low.

Jones and Stokes Associates (1984) reviewed a variety of spot chemical techniques. The following is an excerpt from this report, listing techniques in order of increasing possibility of herbicide exposure to the environment or to humans in the vicinity of treated plants.

1) Stem injection: Herbicides are injected into wounds or cuts in the stems or trunks of plants to be killed. The herbicide must penetrate to the cambial tissue and be water-soluble to be effective. The chemical is then translocated throughout the tree and can provide good root-kill, and thus prevents resprouting.

2) Cut stump treatment: Herbicides are directly applied to the cambial area around the edges of freshly cut stumps. Application must occur within 5-20 minutes of cutting to ensure effectiveness. McHenry (1985) suggests late spring as the best season to do this. In early spring sap may flow to the surface of the cut and rinse the chemical off. At other times of the year translocation is too poor to adequately distribute the chemical. Applications may be made with backpack sprayers, sprinkling cans, brush and pail, or squeeze bottles. This treatment is effective in killing root systems of sprouting hardwoods. Picloram should not be used for this technique as it is known to "flashback" through root grafts between treated and untreated plants and may damage the untreated individuals.

Tre-Hold, an asphalt based formulation containing 1% NAA ethylester has been used as a sprout retardant on ailanthus with varying degrees of effectiveness (Amchem Products 1967).

3) Basal/Stem sprays: High concentrations of herbicides in oil or other penetrating carriers are applied, using backpack sprayers, to the basal portion of stems to be killed. The oil carrier is necessary for the mixture to penetrate bark and enter the vascular system. This method gives good root kill, especially in the fall when vascular fluids are moving toward the roots. This method may be easier to use with small diameter stems than the two previous techniques.

4) Herbicide pellets: Pelletized or granular herbicides are scattered at the bases of unwanted plants. Subsequent rainfall dissolves the pellets and leaches the herbicide down to the root system. Optimal time for treatment is towards the end of the rainy season to prevent leaching beyond the root zone.

Management Programs: Tim Thomas (1985) has removed a small stand of ailanthus in the Santa Monica Mountains National Recreation Area, by pulling up young saplings and is currently monitoring the site to see if it resprouts.

Contact: Tim Thomas, Park Ranger, Santa Monica Mountains National Recreation Area 22900 Ventura Blvd. Woodland Hills, CA 91364, (213) 888-3440.

Management Research Needs: What types of undisturbed habitats does it invade? How do native species respond to ailanthus toxins, and how is recovery potential of an area previously occupied by ailanthus affected by these toxins? What is the chemical make-up of these toxins? What can be used to buffer the effects of the toxins so that understory native seedling growth is encouraged? At what age is the tap root so long that it precludes ailanthus removal by hand?

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Impacts and Control

More info for the terms: allelopathy, competition, cover, density, fire management, fresh, hardwood, invasive species, litter, natural, nonnative species, prescribed fire, presence, root crown, root sprout, selection, succession, top-kill, tree

Impacts: Tree-of-heaven is invasive in many regions of the United States. It can have detrimental effects on ecosystem processes, damage structures, and poses risk to human health.

Invasiveness: Tree-of-heaven's preference for disturbed, early-seral habitats, ability to spread from root sprouts, prodigious seed production, and rapid growth make it an "aggressive" invader [47]. Hammerlynck [122] speculated that tree-of-heaven invasiveness may be due in part to its unusually high capacity to photosynthesize and its high water-use efficiency. These abilities, coupled with pollution [207,253] and drought [87] tolerance, make tree-of-heaven especially successful in urban environments and may also help it invade wildlands [122]. Although it is more common in populated areas (see Site Characteristics), it may spread from developed areas to wildlands [146], especially those disturbed by logging [181] or other canopy-opening events. Tree-of-heaven is most invasive in eastern deciduous forests [34,161,163,166,173,228]. It has invaded the Wayne National Forest, Ohio [79], and is common in white oak-red oak-chestnut oak-Carolina basswood/eastern hophornbeam (Quercus alba-Q. rubra-Q. prinus-Tilia americana var. caroliniana/Ostrya virginiana) forest alliances of the Uwharrie National Forest, North Carolina [224]. In 2007, the Alabama Invasive Plant Council determined there were "extensive and dense" tree-of-heaven infestations in Alabama's managed forests and wildlands [2]. In California, tree-of-heaven is most invasive in riparian zones [44,81] but also invades oak woodlands and valley grasslands [44]. Tellman [287] states tree-of-heaven is "rapidly becoming a problem species" in the Southwest, where it invades riparian zones and other moist areas.

Tree-of-heaven has been rated a threat or potential threat in many areas of the United States. It is rated a potential invader in low-montane areas of the Cascade Range, the Sierra Nevada, and the Middle Rocky Mountains [231]; a high threat to northeastern deciduous and riparian forests and a potentially high threat to northeastern coniferous and mixed forests, grasslands, and fresh and tidal wetlands [70]; and a high threat to oak-hickory forests of the Southeast [279]. Other ratings of tree-of-heaven invasiveness as of 2010 include:

Ratings of tree-of-heaven's invasiveness by state
Rating Area Affected ecosystems
West
Potentially high threat coastal southern Oregon and coastal California mixed-evergreen, coniferous, and riparian forests, grasslands, chaparral, and wetlands [165]
very invasive, especially on disturbed sites Willamette Valley, Oregon Oregon prairie and white oak woodlands [222]
Hawaii
Large potential threat throughout native Hawaiian plant communities [272,321]
Northeast
1 of the top 10 most invasive weeds Bronx River Parkway Reservation, New York riparian and urban forests [100]
Appalachians
Low threat Oak Ridge National Environmental Research Park, Tennessee oak-hickory [78]
Southeast
Highly invasive Savage Neck Dunes Natural Area Preserve on the Delmarva Peninsula, Virginia Chesapeake Bay beach, dune, and maritime forest communities [225]
Highly invasive Petersburg National Battlefield and Colonial National Historical Park, Virginia oak-gum-cypress, loblolly-shortleaf pine, oak-hickory [237] and oak-hickory, oak-gum-cypress, maple-beech-birch, old-field, fresh wetland, and saltmarsh [236] communities, respectively
Most invasive and rapidly spreading nonnative species on site Booker T. Washington National Monument, Virginia oak-hickory, maple-beech-birch, and old-field communities [235]

There is some controversy about tree-of-heaven's ability to invade intact ecosystems. Some authors note that although tree-of-heaven established in North America over 100 years ago, it has not spread to many sites that appear to be good habitat for the species [219]. Hunter [148] considers it "only potentially invasive, and also potentially eradicable" in California. Huebner's [142] model predicts that in wildlands, tree-of-heaven will mostly spread along nonforested corridors and invade forests slowly. Tree-of-heaven may not invade closed-canopy forests [93,148]. It was ranked the least invasive of 18 nonnative, invasive species on the Oak Ridge National Environmental Research Park, Tennessee [78]. Long-distance seed dispersal, however, may enable tree-of-heaven to quickly invade disturbed openings in forest interiors [142]. Merriam [210] estimated a 4.76% increase in tree-of-heaven's rate of spread per year in North Carolina. Further information and research are needed to recognize undisturbed sites at risk for tree-of-heaven invasion [139].

Effects on ecosystem processes: As an early-seral species favoring disturbed sites (see Successional Status), tree-of-heaven grows extremely rapidly and interferes with growth of native species. The large, interconnected roots effectively occupy underground space and crowd out native species. Tree-of-heaven sometimes forms large thickets, displacing native vegetation [172,173]. It may affect natural successional trajectories, in part from competition for light and nutrients in early-successional environments, and possibly from allelopathy [129,130,131,140,184]. Tree-of-heaven and Amur honeysuckle (Lonicera maackii) were the most abundant and ubiquitous woody species in disturbed urban areas of Ohio. The authors speculate that these exotic species invasions have the potential to modify forest composition and ecological function of urban riparian systems [240].

Allelopathic species may alter stand structure and alter key ecosystem processes [314]. Tree-of-heaven's reputed allelopathy may slow succession in plant communities where it is invasive [129,163]. It is apparently toxic to other plants, rodents, and microbes. In an abstract of their laboratory work, Greer and Aldrich [116] report higher toxicity in leaves of young (≤2 years) trees-of-heaven than in leaves of older trees; they also found that minor injury to tree-of-heaven increases toxin production. Concentration of allelopathic chemicals is highest in young tree-of-heaven stands [45,184]; allelopathy may help tree-of-heaven seedlings establish [184] and clones to spread [209]. Seasonally, toxins are greatest in spring and decline as the growing season progresses. Allelopathic chemicals are present in all portions of the tree, but they are most concentrated in roots. The litter is also likely allelopathic. In the greenhouse, slash (Pinus elliottii) and Monterey pine (P. radiata) seed germination was inhibited by fresh tree-of-heaven litter. Allelopathy of tree-of-heaven litter was highest during pine's spring germination period and dwindled through the growing season [311]. In a red maple-sugar maple-northern red oak forest in northwestern Connecticut, tree-of-heaven did not inhibit emergence or survival of either red maple, sugar maple, or northern red oak seedlings beneath tree-of-heaven canopies, but tree-of-heaven significantly reduced seedling growth of red maple (R²=0.33), sugar maple (R²=0.31), and northern red oak (R²=0.49) compared to seedling growth on control sites. Activated carbon was added to the soil on control sites to neutralize the effects of tree-of-heaven's allelopathic chemicals. Allelopathic effects in the soil were positively related to nearness of tree-of-heaven trunks, and soils lost their allelopathic effects about 20 feet (5 m) from the trunks. Cumulative allelopathic effects were proportional to tree-of-heaven density, regardless of tree-of-heaven size [107].

Tree-of-heaven may alter litter layer depth and increase available soil nitrogen in native plant communities. In Spain, tree-of-heaven litter decayed faster than litter of native English elm (P=0.01), and nitrogen release was greater beneath trees-of-heaven than beneath English elms (P=0.005). Soils beneath trees-of-heaven were not higher in nitrogen, however; the authors speculated this may be due to quick nitrogen uptake by nearby plants [50]. Studies on Mediterranean islands of Spain, France, Italy, and Greece found tree-of-heaven presence significantly decreased soil carbon:nitrogen ratios and reduced diversity of native species compared to uninvaded plots (P<0.05 for both variables) [307]. In aquatic ecosystems, preference of invertebrate detritus-feeders for tree-of-heaven litter over litter of native trees (see Palatability) may alter decay rates of native species [284]. Relative palatability of tree-of-heaven litter may affect successional trajectories and increase invasibility of mixed-hardwood communities. In a greenhouse study, earthworms consumed or buried nearly 100% of tree-of-heaven litter; in turn, this increased establishment and growth of nonnative tall fescue (Schedonorus arundinaceus), which had been seeded onto mesocosms (soil-filled tubs) with litter, soil, and earthworms. Tall fescue recruitment was less in mesocosms with native American chestnut (Castanea dentata), northern red oak, or yellow-popular litter than in mesocosms with tree-of-heaven litter [22]. A study in a sugar maple-white ash-northern red oak forest in Connecticut found significantly greater total soil nitrogen, calcium, and nutrient- cycling rates on sites with tree-of-heaven compared to sites without it. This effect increased in soil samples nearer to tree-of-heaven and with increasing tree-of-heaven DBH [106].

Socioeconomic factors: In developed areas, tree-of-heaven roots can damage buildings, foundations, and water facilities [140]. The rapidly growing, extensive root system also allows the tree to establish on steep to vertical structures including roofs and cracked walls, which are damaged if seedlings are not promptly killed [7,262]. Tree-of-heaven has damaged archeological sites in Europe. A study in Mediterranean Italy found it was the only nonnative tree species establishing in and damaging archeological remains [51]. In Portugal, tree-of-heaven roots damaged the walls and roof of the 800-year-old Sé Velha of Coimbra Cathedral after establishing in the wall mortar and clay roof tiles [7]. The water-seeking roots can stop up sewer lines and invade wells and cisterns, damaging infrastructures and giving potable water an unpleasant taste [62,140].

Tree-of-heaven poses human health risks. The pollen can cause an allergic reaction [68]. The sap causes a dermatitis reaction in some people [68,319], and prolonged exposure of broken skin to sap can have serious consequences. For at least one tree remover, exposure to tree-of-heaven sap on rope burns resulted in an elevated heart rate and chest pain that was severe enough to require hospitalization for several days [29].

Control: In all cases where invasive species are targeted for control, the potential for other invasive species to fill their void must be considered no matter what method is employed [38]. Control of biotic invasions is most effective when it employs a long-term, ecosystem-wide strategy rather than a tactical approach focused on battling individual invaders [192].

Prevention: It is commonly argued that the most cost-efficient and effective method of managing invasive species is to prevent their establishment and spread by maintaining "healthy" natural communities [192,270] (e.g., avoid road building in wildlands [296]) and by monitoring several times each year [155]. Managing to maintain the integrity of the native plant community and mitigate the factors enhancing ecosystem invasibility is likely to be more effective than managing solely to control the invader [138]. Weed prevention and control can be incorporated into many types of management plans, including those for logging and site preparation, grazing allotments, recreation management, research projects, road building and maintenance, and fire management [301]. See the Guide to noxious weed prevention practices [301] for specific guidelines in preventing the spread of weed seeds and propagules under different management conditions. The Center for Invasive Plant Management provides an online guide to noxious weed prevention practices. Nursery businesses can reduce tree-of-heaven introductions by not stocking tree-of-heaven and discouraging its use [126]. Gonzalez and Christoffersen [108] give suggestions for alternative landscaping species that are native in the Southeast and Southwest.

Posttreatment monitoring and retreatment are essential for this root-sprouting, rapidly growing species (see Regeneration Processes). Monitoring efforts are best concentrated on the most disturbed areas in a site, particularly along potential pathways for tree-of-heaven invasion: roadsides, trails, parking lots, fencelines, trails, and waterways [40,46,141]. In a West Virginia study, tree-of-heaven occurrence was heaviest along interstate freeways I-68 and I-79 [141]. Fortunately, tree-of-heaven's pattern of roadside and trail invasion makes accessibility, early detection, and treatment relatively easy on many sites [40]. Treated areas need checking once or twice a year, with any new sprouts or seedlings retreated as soon as possible so that plants do not have time to build up carbohydrate reserves and grow larger [139]. Whenever there is a nearby tree-of-heaven seed source, disturbed sites require monitoring and follow-up treatments to prevent tree-of-heaven invasion. Initial summer treatment impacts trees when their root reserves are low. Targeting female trees-of-heaven for control helps slow seed dissemination [139]. Monitoring is most effective when continued for at least a year after tree-of-heaven sprouting appears controlled [149]. Tree-of-heaven may show up on sites where treatments for other invasive weeds have created open, disturbed conditions. For example, tree-of-heaven and Norway maple seedlings invaded a New Jersey site after Norway maple removal treatments (cutting mature trees and hand-pulling Norway maple seedlings). Tree-of-heaven was not present on study plots prior to Norway maple removal [315].

Fire: Prescribed fire is not recommended to control tree-of-heaven due to tree-of-heaven's ability to establish from root sprouts and seed after disturbance [87,149] (see Fire Management Considerations). Nava-Constan and others' [54] experiment in Spain (see Physical and/or mechanical treatment) demonstrates tree-of-heaven's ability to increase by sprouting after top-kill. However, fire may be used as the initial top-kill treatment for tree-of-heaven control or for spot treatment. Instead of using mechanical or chemical methods to top-kill stems, a flame thrower or weed burner can heat-girdle tree-of-heaven boles [56]. As with all top-kill methods, tree-of-heaven sprouts after heat girdling [56,87], so follow-up treatments are needed to control sprouts.

Cultural: Maintaining a healthy overstory can help minimize invasive potential for tree-of-heaven [270]. Establishing a thick cover of native trees or grass helps shade out tree-of-heaven and discourages tree-of-heaven regrowth [139]. Broadcasting seed of native tree species may help slow tree-of-heaven establishment on some disturbed sites. In West Virginia, seedling establishment experiments in a harvested mixed-hardwood community showed yellow-poplar seedling survivorship 2 years after sowing was higher than that of tree-of-heaven seedlings (80% vs. 28%, P<0.01) on selection cuts. However, tree-of-heaven survivorship was higher than that of yellow-poplar on clearcut and unharvested control sites [171]. Moore and Lacey [216] found sweetgum and American sycamore germinated and established more quickly in the greenhouse than nonnative trees, including tree-of-heaven (P<0.001); they suggested establishing native tree seedlings on disturbed sites to help reduce invasion of nonnative tree species such as tree-of-heaven [216]. If artificial regeneration of native trees is indicated, it is important to establish the native seedlings quickly. With one of the fastest growth rates of any tree in North America [166], young trees-of-heaven may grow faster than and overtop young native tree species [149,166,173].

Physical and/or mechanical: Mechanical treatments, including cutting or girdling, are a good first step in controlling tree-of-heaven. Mechanical treatment alone encourages both stump and root sprouts, so follow-up treatments are required [149,316]. Cutting stems before flowering prevents seed spread, and cutting at ground level prevents bole sprouts [149]. Root and root crown sprouts can be controlled by further cutting treatments or herbicides [139,149,178], although herbicides are more effective (see Chemical control). Unless the treatment area is heavily shaded, it usually takes at least 5 years of follow-up mechanical treatment to control sprouts [58,139]. Removing the roots eliminates sprouting [58,87] but is impractical on most sites. Cutting without further treatment is not recommended because it promotes tree-of-heaven sprouting [58] and may increase tree-of-heaven abundance. A study in a Mediterranean ecosystem of Spain found that after tree-of-heaven was cut twice a year for 5 years, its density and leaf area index were greater on cut than on uncut plots (P<0.05) [54].

In small areas, seedlings can be controlled by hand pulling. Seedlings quickly develop extensive root systems, so the entire root needs to be removed to prevent sprouting [178]. Seedling and root sprout top-growth looks similar, but root sprouts are connected by large lateral roots. Tree-of-heaven seedlings can sometimes be compared to the variable number of leaflets and thicker stems of sprouts [149]. Grubbing roots may be effective for saplings [294]. Except for small infestations, grubbing for mature trees or well-established tree-of-heaven colonies. The root systems are extensive and nearly impossible to entirely remove, and even a small root fragment can produce root sprouts [139,149].

Biological: Biological control of invasive species has a long history that indicates many factors must be considered before using biological controls. Refer to these sources: [305,320] and the Weed control methods handbook [294] for background information and important considerations for developing and implementing biological control programs.

As of this writing (2010), there were no biological control agents approved for tree-of-heaven [134,260,294]. Eucryptorrhynchus brandti and E. chinensis, weevils native to China, are apparently host-specific tree-of-heaven feeders [72,134,260]. As of 2009, they were being tested as possible control agents for tree-of-heaven [134,260]. A wilt fungus (Verticullum albo-atrum) is also being tested for tree-of-heaven control [265]. Ding and others [73] provide a review of these and other biological control agents being tested for tree-of-heaven as of 2006.

Chemical: Herbicides are effective in gaining initial control of a new invasion or a severe infestation, but they are rarely a complete or long-term solution to weed management [42]. See the Weed control methods handbook [294] large infestations when incorporated into long-term management plans that include replacement of weeds with desirable species, careful land use management, and prevention of new infestations. Control with herbicides is temporary, as it does not change conditions that allow infestations to occur in the first place (for example, [326]).

Systemic herbicides that kill roots (for example, triclopyr and glyphosate) currently provide the best chemical control for tree-of-heaven. Dicamba, imazapyr, and methsulfuron methyl have also provided control [83,84,139,178,275]. See The Nature Conservancy's Weed control methods handbook for considerations on the use of herbicides in Natural Areas and detailed information on specific chemicals. See these sources for information pertaining to chemical of tree-of-heaven in particular: [83,139,145,178,199,212,275,276,294,294,304,311,312,317].

Several studies indicate that herbicides control tree-of-heaven better than cutting [40,54,208], and probably better than prescribed fire (see Fire studies). In oak-hickory communities of Shenandoah National Park, low-volume basal application of herbicides (triclopyr, picloram, imazapyr, and combinations) gave better tree-of-heaven control than cutting. At posttreatment year 2, a shift toward native herbs had occurred on plots where tree-of-heaven was controlled, while nonnative herbs including garlic mustard (Alliaria petiolata) and burdock (Arctium minus) were more prevalent on plots where tree-of-heaven density remained high [40].

Mean tree-of-heaven density 2 years after control treatments in Shenandoah National Park [40]
Treatment Stems/acre
cutting 5,645
imazapyr 363
picloram + triclopyr* 81
*Several herbicide combinations and application rates were used. See Burch and Zedaker [40] for details.

Herbicides meant for tree-of-heaven may kill nontarget trees, even when injected into tree-of-heaven stems. Spraying may be indicated when there are large thickets without nontarget species or as a follow-up treatment to other control methods, but in mixed stands herbicides will probably have a greater impact on nontarget species that lack tree-of-heaven's ability to root sprout than on tree-of-heaven [139,178,275,294]. Tree-of-heaven roots may exude herbicides, so caution is recommended when treating trees-of-heaven growing next to high-value trees [83]. In southeastern Ohio, 17.5% of native hardwoods within 10 feet (3 m) of trees-of-heaven injected with imazapyr were also killed. The authors surmised that root grafts and/or shared mycorrhizae translocated imazapyr from tree-of-heaven to native hardwood roots [187].

Chemical control programs targeting herbaceous species may unintentionally increase tree-of-heaven, depending upon the herbicides used. In West Virginia, diuron, simazine, and terbacil treatments for rough pigweed (Amaranthus retroflexus), barnyard grass (Echinochloa crus-galli), and other herbaceous weeds in a commercial apple (Malus sylvestris) orchard successfully reduced most herbaceous weeds; however, tree-of-heaven and nonnative tall fescue (Schedonorus arundinaceus) dominated the ground layer of plots treated with diuron and simazine. Terbacil gave best control of tree-of-heaven [295].

Integrated management: A combination of complementary control methods may be helpful for rapid and effective control of tree-of-heaven. Integrated management includes not only killing the target plant, but establishing desirable species and discouraging nonnative, invasive species over the long term. In a black oak community in Rondeau Provincial Park, Ontario, cutting and applying glyphosate to tree-of-heaven stumps best controlled trees-of-heaven for 2 years, while cutting alone increased tree-of-heaven density over pretreatment levels. Hand-pulling and mulching was done on seedlings that had not yet developed taproots and on juveniles (<20 inches (60 cm) tall)); juveniles were extracted by the roots to prevent sprouting [208]:

Tree-of-heaven density (shoots/m²) after control treatments in Rondeau Provincial Park [208]
  Juveniles Control Mature trees
Treatment   Hand-pulling & mulch Cut stump & glyphosate Cut stump Untreated Glyphosate-injected
Pretreatment 12.7a 11.8a 12.8a 13.4a 14.2a
Posttreatment year 1 1.7b 0.8b 9.2a 10.6a 9.8a
Posttreatment year 2 5.8b 1.0c 20.9d 10.9a 8.9a
Within rows, means followed by different letters are significantly different (P=0.05). Means of juvenile trees on experimental plots are compared only with means of juvenile trees on control plots, and means of mature trees on experimental plots are compared only with means of mature trees on control plots.

In an experiment in the Mediterranean region of Spain (see Physical and/or mechanical control), a single stump cutting followed by glyphosate treatment significantly reduced tree-of-heaven biomass, density, and leaf area index compared to single cutting, twice-yearly cutting, and control treatments (P<0.05) [54].
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Prevention and Control

Do not plant tree of heaven or spread its seeds when moving soil from infested areas. Before attempting control, ensure that you are not mistaking a native species like staghorn sumac, ash or walnut for tree of heaven. Elimination of tree of heaven requires diligence. Targeting large female trees for control will help reduce spread by seed. Because vegetative spread by male and female trees will continue to be a threat, elimination of all trees must be the long term goal. Systemic herbicides with active ingredients like glyphosate and triclopyr are most effective and can be applied to bark, cut stems or foliage.

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These species are introduced in Switzerland.
  • Aeschimann, D. & C. Heitz. 2005. Synonymie-Index der Schweizer Flora und der angrenzenden Gebiete (SISF). 2te Auflage. Documenta Floristicae Helvetiae N° 2. Genève.   http://www.crsf.ch/ External link.
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Relevance to Humans and Ecosystems

Benefits

Cultivation

The preference is full or partial sun and moist to mesic conditions. Many kinds of soil are tolerated, including those containing loam, clay, rocky material, and sand. This tree tolerates most types of air pollution, although it is somewhat sensitive to ozone. It will also grow in contaminated ground that contains mercury and other toxic compounds. Growth and development are quite fast, although longevity of individual trees is short (usually about 50 years). The roots and foliage secrete a phytotoxic chemical, ailanthione, that inhabits the germination of seeds and stunts the growth of other species of plants. The wide-ranging roots can clog sewer lines and water pipes, and they have been known to penetrate street pavement and uplift the foundation of buildings.
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Economic Uses

Uses: Folk medicine

Comments: Valued for wood products and medicine

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Other uses and values

More info for the terms: fresh, tree

Tree-of-heaven has been widely planted as an ornamental because it grows quickly, can be trained into an attractive shape, and has attractive foliage and fruits. It was once widely cultivated in North America [312,324] and is still available as a horticultural plant [126]. It is planted less frequently now [312,324] because of its disagreeable odor and strong tendency to spread into areas where it is not wanted. It is occasionally used for shelterbelts and urban plantings [211,328].

Tree-of-heaven's tolerance to pollution has management uses. It is a bioindicator of ozone pollution, to which it is sensitive. When subjected to heavy ozone concentrations, the leaves show spotting damage and drop off [111]. Conversely, tree-of-heaven tolerates high levels of sulfur and mercury pollution, concentrating mercury in its leaves (review by [175]). It has been used to rehabilitate mine spoils in the eastern United States. Tolerant of saline soils and low pH, tree-of-heaven shows better growth on mine spoils than many native species [245]. Due to its tendency to spread on disturbed sites, however, it is not generally recommended for rehabilitation [147,178].

Tree-of-heaven provides shade, medicine, wood, clothing, and food for humans. The species has a long history of folk medicine and cultural use in Asia [140]. It is used as an astringent, antispasmodic, anthelmintic, and parasiticide. Fresh stem bark is used to treat diarrhea and dysentery; root bark is used for heat ailments, epilepsy, and asthma.  The fruits are used to regulate menstruation and treat ophthalmic diseases. Leaves are an astringent and used in lotions for seborrhea and scabies [9,140]. Laboratory studies show tree-of-heaven has a potential role in modern medicine. Tree-of-heaven extracts have antibacterial, antioxidant [251], and antiinflammatory [154] properties. Pharmacological research is focusing on possible use of tree-of-heaven extracts for treating cancer, malaria, and HIV-1 infection [9,36,52,226]. In China, tree-of-heaven is grown commercially as a host for Attacus cynthia, a silkworm that produces coarse, durable silk [140,308]. Tree-of-heaven is a food for honeybees worldwide. Initially bad-tasting, tree-of-heaven honey ages to a high-quality, flavorful product [59,211].

Putative allelopathic tree-of-heaven extracts have potential use as herbicides [64,131,190].

Wood Products: Tree-of-heaven wood resembles ash (Fraxinus spp.) wood in appearance and quality. It is easily worked with tools and glue, and takes a finish well. Alden [4] and Moslemi and Bhagwat [219] summarize manufacturing properties of tree-of-heaven wood. Berchem and others [23] and Adamik and Brauns [1] provide information on properties and potential uses of tree-of-heaven wood fiber.

Tree-of-heaven is an important timber and fuelwood tree in China, and is planted for timber and afforestation in New Zealand, the Middle East, eastern Europe, and South America [14,140,268,304,328]. Zasada and Little [328] provide information on tree-of-heaven cultivation.

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  • 190. Lin, Lee-Juian; Peiser, Galen; Ying, Bai-Ping; Mathias, Kristina; Karasina, Faina; Wang, Zhan; Itatani, Joyce; Green, Laddie; Hwang, Yih-Shen. 1995. Identification of plant growth inhibitory principles in Ailanthus altissima and Castela tortuosa. Journal of Agricultural Food Chemistry. 43(6): 1708-1711. [45851]
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  • 251. Rahman, Atiqur; Kim, Eun Lyang; Kang, Sun Chul. 2009. Antibacterial and antioxidant properties of Ailanthus altissima Swingle leaf extract to reduce foodborne pathogens and spoiling bacteria. Journal of Food Safety. 29(4): 499-510. [79726]
  • 268. Shafiq, Muhammad; Nizami, M. I. 1986. Growth behaviour of different plants under gullied area of Pothwar Plateau. The Pakistan Journal of Forestry. 36(1): 9-15. [46127]
  • 304. Udvardy, L. 1998. Spreading and coenological circumstances of the tree of heaven (Ailanthus altissima) in Hungary. Acta Botanica Hungarica. 41(1-4): 299-314. [46454]
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  • 324. Wunderlin, Richard P. 1998. Guide to the vascular plants of Florida. Gainesville, FL: University Press of Florida. 806 p. [28655]
  • 328. Zasada, John C.; Little, Silas. 2008. Ailanthus altissima (P. Mill.) Swingle: ailanthus. In: Bonner, Franklin T., Karrfalt, Robert P., eds. Woody plant seed manual. Agric. Handbook No. 727. Washington, DC: U.S. Department of Agriculture, Forest Service: 224-226. [46269]
  • 36. Bray, D. H.; Boardman, P.; O'Neill, M. J.; Chan, K. L.; Phillipson, J. D.; Warhurst, D. C.; Suffness, M. 1987. Plants as a source of antimalarial drugs. 5. Activities of Ailanthus altissima stem constituents and of some related quassinoids. Phytotherapy Research. 1(1): 22-24. [46125]
  • 4. Alden, Harry A. 1995. Hardwoods of North America. Gen. Tech. Rep. FPL-GTR-83. Madison, WI: U.S. Department of Agriculture, Forest Service, Forest Products Laboratory. 136 p. Available online: http://www.fpl.fs.fed.us/documnts/fplgtr/fplgtr83.pdf [2004, January 6]. [46270]
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  • 59. Dalby, Richard. 2000. Minor bee plants in a major key: tamarisk, ailanthus and teasel. American Bee Journal. 140(1): 60-61. [43996]
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  • 9. Ansari, S. H.; Ali, M. 1999. Recent developments in the chemistry of Ailanthus altissima. Hamdard Medicus. 42(3): 58-63. [46264]

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Importance to Livestock and Wildlife

More info for the terms: cover, litter, tree

There are few reports of either wildlife or domestic animal use of tree-of-heaven. White-tailed deer and domestic goats browse the foliage [35,147,308], but tree-of-heaven browse is apparently not preferred. In mixed-hardwood stands of Virginia, white-tailed deer browsed 0.4% of available tree-of-heaven seedlings and 12.6% of tree-of-heaven saplings in recently logged forests but preferred black tupelo (Nyssa sylvatica). Browsing pressure on tree-of-heaven was greater in mature stands—where other browse was less available—with white-tailed deer utilizing 33.3% of tree-of-heaven seedlings and 41.7% of saplings. Across tree species, browsing pressure was significantly greater in mature than logged stands (P=0.02) [49]. Meadow voles also browse tree-of-heaven [43]. An old-field study in New York showed meadow voles preferred tree-of-heaven seedlings over eastern white pine seedlings, but white-footed mice preferred eastern white pine, sugar maple, and white ash seedlings over tree-of-heaven seedlings [229].

Wildlife consumption of tree-of-heaven seeds is apparently light. A few birds, including pine grosbeak and crossbills, eat the seeds [147]. A New Jersey study found granivorous rodents ignored tree-of-heaven seeds in an old field [193].

Invertebrates use tree-of-heaven; the few studies available as of 2010 suggested tree-of-heaven is important in the diet of some invertebrate species. In a mixed-hardwood forest in New York, invertebrates browsed tree-of-heaven seedlings preferentially [43]. Tree-of-heaven nectaries attract ants, which may defend trees-of-heaven against other insects, including potential pollinators. Ants sometimes colonize hollow boles of fungus-infested trees-of-heaven [5]. A study in Maryland found detritus-feeding, aquatic isopods and caddisflies preferred tree-of-heaven litter to litter of 6 native species, possibly because tree-of-heaven litter decayed more rapidly than that of native species [284]. A greenhouse study found nonnative earthworms (Lumbricus terrestris) preferred tree-of-heaven litter to that of native yellow-poplar [22].

Palatability and nutritional value: Tree-of-heaven is unpalatable to ungulates [99]. The bark and leaves contain saponins, quassinoids, and other bitter compounds that discourage consumption [10,131,190,308].

Tree-of-heaven is a fairly good source of protein, especially early in the growing season [15].

Nutritional content  (%) of tree-of-heaven browse in Pakistan [15]
  Digestible matter Crude protein Neutral- detergent fiber Acid- detergent fiber Hemi-
cellulose
Acid- detergent lignin Ash Dry matter digestibility*
Spring 65.3 27.2 22.3 17.9 4.4 4.8 9.4 78.56
Winter 66.3 10.5 26.0 18.3 7.7 2.6 13.5 67.26
*For domestic goats.

The seeds are a good source of fatty oils [32,156]. Seed collected in the United States had 56% fatty oil and 23% protein content [10].

Cover value: No information is available on this topic.

  • 10. Ansari, S. H.; Ali, M. 2003. Two new phytosterols from Ailanthus altissima (Mill) Swingle. In: Bernath, J.; Szoke, E.; Mathe, I.; Blunden, G.; Kery, A., eds. Proceedings, international conference on medicinal and aromatic plants (Part II); 2001 July 8-11; Budapest, Hungary. In: Acta Horticulture. Leuven, Belgium: International Society for Horticultural Science; 597: 91-94. [46145]
  • 131. Heisey, Rod M. 1996. Identification of an allelopathic compound from Ailanthus altissima (Simaroubaceae) and characterization of its herbicidal activity. American Journal of Botany. 83(2): 192-200. [45475]
  • 147. Hunter, Carl G. 1989. Trees, shrubs, and vines of Arkansas. Little Rock, AR: The Ozark Society Foundation. 207 p. [21266]
  • 15. Azim, A.; Khan, A. G.; Ahmad, J.; Ayaz, M.; Mirza, I. H. 2002. Nutritional evaluation of fodder tree leaves with goats. Asian-Australian Journal of Animal Science. 15(1): 34-37. [46153]
  • 156. Kapoor, N.; Bedi, K. L.; Tikoo, M. K.; Kapoor, S. K.; Sarin, Y. K. 1990. Some lesser known tree-borne oilseeds of India. Journal of the Oil Technologists Association of India. 22(3): 65-66. [46156]
  • 190. Lin, Lee-Juian; Peiser, Galen; Ying, Bai-Ping; Mathias, Kristina; Karasina, Faina; Wang, Zhan; Itatani, Joyce; Green, Laddie; Hwang, Yih-Shen. 1995. Identification of plant growth inhibitory principles in Ailanthus altissima and Castela tortuosa. Journal of Agricultural Food Chemistry. 43(6): 1708-1711. [45851]
  • 193. Manson, Robert H.; Stiles, Edmund W. 1998. Links between microhabitat preferences and seed predation by small mammals in old fields. Oikos. 82(1): 37-50. [49558]
  • 22. Belote, R. Travis; Jones, Robert H. 2009. Tree leaf litter composition and nonnative earthworms influence plant invasion in experimental forest floor mesocosms. Biological Invasions. 11(4): 1045-1052. [79743]
  • 229. Ostfeld, Richard S.; Manson, Robert H.; Canham, Charles D. 1997. Effects of rodents on survival of tree seeds and seedlings invading old fields. Ecology. 78(5): 1531-1542. [46148]
  • 284. Swan, Christopher M.; Healey, Benjamin; Richardson, David C. 2008. The role of native riparian tree species in decomposition of invasive tree of heaven (Ailanthus altissima) leaf litter in an urban stream. Ecoscience. 15(1): 27-35. [79746]
  • 308. Vines, Robert A. 1960. Trees, shrubs, and woody vines of the Southwest. Austin, TX: University of Texas Press. 1104 p. [7707]
  • 32. Bory, G.; Clair-Maezulajtys, D. 1989. Lipid content and fatty acid composition of seeds of Ailanthus altissima (Mill) Swingle (Simaroubaceae). Indian Journal of Plant Physiology. 31(1): 12-16. [46745]
  • 35. Bourke, C. A. 1996. Lack of toxicity of Ailanthus altissima (tree-of-heaven) for goats. Australian Veterinary Journal. 74(6): 465. [45850]
  • 43. Cadenasso, M. L.; Pickett, S. T. A. 2000. Linking forest edge structure to edge function: mediation of herbivore damage. Journal of Ecology. 88(1): 31-44. [80030]
  • 49. Carter, William K.; Fredericksen, Todd S. 2007. Tree seedling and sapling density and deer browsing incidence on recently logged and mature non-industrial private forestlands in Virginia, USA. Forest Ecology and Management. 242(2-3): 671-677. [66560]
  • 5. Aldrich, Preston R.; Brusa, Anthony; Heinz, Cheryl A.; Greer, Gary K.; Huebner, Cynthia. 2008. Floral visitation of the invasive stinking ash in western suburban Chicago. Transactions of the Illinois State Academy of Science. 101(1-2): 1-12. [79787]
  • 99. Forgione, Helen M. 1993. Limits to the establishment and growth of tree-of-heaven explored. Restoration & Management Notes. 11(1): 70-71. [22459]

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Special Uses

Ailanthus's main importance remains in urban forestry, the  original purpose of its importation into the United States. The  species, tolerance of noxious emissions of gases and various  dusts assures its continued use for plantings in industrial  environments. Tolerance of poor soils and low soil moisture  dictates its selection for city plantings in arid climates as  well as shelterbelt plantings and on strip mine reclamation  projects, although its unfavorable traits (odor and root  sprouting) have decreased city plantings.

    Root sprouting into fields is also a problem in shelterbelt  plantings.

    Pollinating insects are attracted by the male flowers. Honey from  ailanthus has been reported as having an initial foul taste that  disappears with aging, resulting in an exceptionally good tasting  honey (13).

  • Burns, Russell M., and Barbara H. Honkala, technical coordinators. 1990. Silvics of North America: 1. Conifers; 2. Hardwoods.   Agriculture Handbook 654 (Supersedes Agriculture Handbook 271,Silvics of Forest Trees of the United States, 1965).   U.S. Department of Agriculture, Forest Service, Washington, DC. vol.2, 877 pp.   http://www.na.fs.fed.us/spfo/pubs/silvics_manual/table_of_contents.htm External link.
Creative Commons Attribution Non Commercial 3.0 (CC BY-NC 3.0)

James H. Miller

Source: Silvics of North America

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Risks

Stewardship Overview: Ailanthus is a fast growing tree, a prolific seed producer, a persistant stump and root sprouter and an aggressive competitor with respect to the surrounding vegetation. It occurs primarily in disturbed areas, though it may invade undisturbed habitats. It was brought into California mainly by the Chinese who came to California during the goldrush in the 1890's, and frequently occurs in abandoned mining sites. Little work has been done on developing biological or chemical control methods. The most effective means of control may be to pull seedlings by hand before the tap root develops.

Species Impact: Although only occasionally found in nondisturbed areas (Kowarik 1983), Ailanthus is a prolific seed producer, grows rapidly and can successfully compete with the native vegetation. It produces toxins which prevent the establishment of other species (Mergen 1959). The root system is aggressive enough to cause damage to sewers and foundations (Hu 1979).

Ailanthus was not nominated by any specific preserve manager, but is recognized by TNC staff as an important exotic weed. A recent survey (2 March 1985) of CNPS members showed a wide distribution of this tree throughout California. Members of both the Mt. Lassen and Sequoia chapters consider it a major pest at low elevations. There are also reports of it growing in Santa Cruz, Riverside, San Bernardino, Los Angeles and San Diego counties.

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© NatureServe

Source: NatureServe

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Ecological Threat in the United States

Tree-of-heaven is a fast-growing tree and a prolific seeder, that can take over sites, replacing native plants and forming dense thickets. Ailanthus also produces chemicals that prevent the establishment of other plant species nearby. Its root system may be extensive and has been known to cause damage to sewers and foundations.

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U.S. National Park Service Weeds Gone Wild website

Source: U.S. National Park Service

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Ecological Threat in the United States

A common tree in urban areas where it causes damage to sewers and structures, ailanthus poses a greater threat to agriculture and natural ecosystems. It is a vigorous growing tree and prolific seeder that establishes dense stands that push out natives. Tree of heaven contains chemicals, including ailanthone, that have been found to have strong allelopathic (herbicidal) affects on the growth of other plants which help it establish and spread.

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Wikipedia

Ailanthus altissima

"Tree of heaven" redirects here. For the TV show, see Tree of Heaven (TV series).

Ailanthus altissima /ˈlænθəs ælˈtɪsɨmə/,[2] commonly known as tree of heaven, ailanthus, or in Standard Chinese as chouchun (Chinese: 椿; pinyin: chòuchūn; literally: "foul smelling tree"), is a deciduous tree in the Simaroubaceae family. It is native to both northeast and central China, as well as Taiwan. Unlike other members of the genus Ailanthus, it is found in temperate climates rather than the tropics. The tree grows rapidly and is capable of reaching heights of 15 metres (49 ft) in 25 years. However, the species is also short lived and rarely lives more than 50 years, though its remarkable suckering ability makes it possible for this tree to clone itself indefinitely and live considerably longer [3] (since they are linked to the mother tree and thus partly fed by it, the suckers are less vulnerable than the seedlings and can grow faster).

In China, the tree of heaven has a long and rich history. It was mentioned in the oldest extant Chinese dictionary and listed in countless Chinese medical texts for its purported ability to cure ailments ranging from mental illness to baldness. The roots, leaves and bark are still used today in traditional Chinese medicine, primarily as an astringent. The tree has been grown extensively both in China and abroad as a host plant for the ailanthus silkmoth, a moth involved in silk production. Ailanthus has become a part of western culture as well, with the tree serving as the central metaphor and subject matter of the best-selling American novel A Tree Grows in Brooklyn by Betty Smith.

The tree was first brought from China to Europe in the 1740s and to the United States in 1784. It was one of the first trees brought west during a time when chinoiserie was dominating European arts, and was initially hailed as a beautiful garden specimen. However, enthusiasm soon waned after gardeners became familiar with its suckering habits and its foul smelling odour. Despite this, it was used extensively as a street tree during much of the 19th century. Outside of Europe and the United States, the plant has been spread to many other areas beyond its native range. In a number of these, it has become an invasive species due to its ability both to colonise disturbed areas quickly and to suppress competition with allelopathic chemicals. It is considered a noxious weed in Australia, the United States, New Zealand and many countries of central, eastern and southern Europe. The tree also resprouts vigorously when cut, making its eradication difficult and time consuming. In many urban areas, it has acquired the derisive nicknames of "ghetto palm", "stink tree", and "tree of Hell".

Description[edit]

Botanical drawing of the leaves, flowers and samaras from Britton and Brown's 1913 Illustrated flora of the northern states and Canada

A. altissima is a medium-sized tree that reaches heights between 17 and 27 metres (56 and 90 ft) with a diameter at breast height of about 1 metre (40 in).[4] The bark is smooth and light grey, often becoming somewhat rougher with light tan fissures as the tree ages. The twigs are stout, smooth to lightly pubescent, and reddish or chestnut in colour. They have lenticels as well as heart-shaped leaf scars (i.e. a scar left on the twig after a leaf falls) with many bundle scars (i.e. small marks where the veins of the leaf once connected to the tree) around the edges. The buds are finely pubescent, dome shaped, and partially hidden behind the petiole, though they are completely visible in the dormant season at the sinuses of the leaf scars.[5] The branches are light to dark gray in colour, smooth, lustrous, and containing raised lenticels that become fissures with age. The ends of the branches become pendulous. All parts of the plant have a distinguishing strong odour that is often likened to peanuts, cashews,[6] or rotting cashews.[7]

The leaves are large, odd- or even-pinnately compound, and arranged alternately on the stem. They range in size from 30 to 90 cm (0.98 to 2.95 ft) in length and contain 10–41 leaflets organised in pairs, with the largest leaves found on vigorous young sprouts. The rachis is light to reddish-green with a swollen base. The leaflets are ovate-lanceolate with entire margins, somewhat asymmetric and occasionally not directly opposite to each others. Each leaflet is 5 to 18 cm (2.0 to 7.1 in) long and 2.5 to 5 cm (0.98 to 1.97 in) wide. They have a long tapering end while the bases have two to four teeth, each containing one or more glands at the tip.[5] The leaflets' upper sides are dark green in colour with light green veins, while the undersides are a more whitish green. The petioles are 5 to 12 mm (0.20 to 0.47 in) long.[6] The lobed bases and glands distinguish it from similar sumac species.

Bark and flowers of A. altissima
Immature seeds on a female tree.

The flowers are small and appear in large panicles up to 50 cm (20 in) in length at the end of new shoots. The individual flowers are yellowish green to reddish in colour, each with five petals and sepals.[4][6] The sepals are cup-shaped, lobed and united while the petals are valvate (i.e. they meet at the edges without overlapping), white and hairy towards the inside.[5][8][9] They appear from mid-April in the south of its range to July in the north. A. altissima is dioecious, with male and female flowers being borne on different individuals. Male trees produce three to four times as many flowers as the females, making the male flowers more conspicuous. Furthermore, the male plants emit a foul-smelling odour while flowering to attract pollinating insects. Female flowers contain ten (or rarely five through abortion) sterile stamens (stamenoides) with heart-shaped anthers. The pistil is made up of five free carpels (i.e. they are not fused), each containing a single ovule. Their styles are united and slender with star-shaped stigmas.[5][8] The male flowers are similar in appearance, but they of course lack a pistil and the stamens do function, each being topped with a globular anther and a glandular green disc.[5] The seeds borne on the female trees are 5 mm in diameter and each is encapsulated in a samara that is 2.5 cm long (1 in) and 1 cm (0.39 in) broad, appearing July though August, but can persist on the tree until the next spring. The samara is large and twisted at the tips, making it spin as it falls, assisting wind dispersal,[4][6] and aiding buoyancy for long-distance dispersal through hydrochory.[10] The females can produce huge amounts of seeds, normally around 30,000 per kilogram (14,000/lb) of tree,[4] and fecundity can be estimated non-destructively through measurements of dbh.[10]

Taxonomy[edit]

The first scientific descriptions of the tree of heaven were made shortly after it was introduced to Europe by the French Jesuit Pierre Nicholas d'Incarville. D'Incarville had sent seeds from Peking via Siberia to his botanist friend Bernard de Jussieu in the 1740s. The seeds sent by d'Incarville were thought to be from the economically important and similar looking Chinese varnish tree (Toxicodendron vernicifluum), which he had observed in the lower Yangtze region, rather than the tree of heaven. D'Incarville attached a note indicating this, which caused much taxonomic confusion over the next few decades. In 1751, Jussieu planted a few seeds in France and sent others on to Philip Miller, the superintendent at the Chelsea Physic Garden, and to Philip C. Webb, the owner of an exotic plant garden in Busbridge, England.[5]

Confusion in naming began when the tree was described by all three men with three different names. In Paris, Linnaeus gave the plant the name Rhus succedanea, while it was known commonly as grand vernis du Japon. In London the specimens were named by Miller as Toxicodendron altissima and in Busbridge it was dubbed in the old classification system as Rhus Sinese foliis alatis. There are extant records from the 1750s of disputes over the proper name between Philip Miller and John Ellis, curator of Webb's garden in Busbridge. Rather than the issue being resolved, more names soon appeared for the plant: Jakob Friedrich Ehrhart observed a specimen in Utrecht in 1782 and named it Rhus cacodendron.[5]

Light was shed on the taxonomic status of ailanthus in 1788 when René Louiche Desfontaines observed the samaras of the Paris specimens, which were still labelled Rhus succedanea, and came to the conclusion that the plant was not a sumac. He published an article with an illustrated description and gave it the name Ailanthus glandulosa, placing it in the same genus as the tropical species then known as A. integrifolia (white siris, now A. triphysa). The name is derived from the Ambonese word ailanto, meaning "heaven-tree" or "tree reaching for the sky".[5][11] The specific glandulosa, referring to the glands on the leaves, persisted until as late as 1957, but it was ultimately made invalid as a later homonym at the species level.[5] The current species name comes from Walter T. Swingle who was employed by the United States Department of Plant Industry. He decided to transfer Miller's older specific name into the genus of Desfontaines, resulting in the accepted name Ailanthus altissima.[12] Altissima is Latin for "tallest",[13] and refers to the sizes the tree can reach. The plant is sometimes incorrectly cited with the specific epithet in the masculine (glandulosus or altissimus), which is incorrect since botanical, like Classical Latin, treats most tree names as feminine.

There are three varieties of A. altissima:

  • A. altissima var. altissima, which is the type variety and is native to mainland China.
  • A. altissima var. tanakai, which is endemic to northern Taiwan highlands. It differs from the type in having yellowish bark, odd-pinnate leaves that are also shorter on average at 45 to 60 cm (18 to 24 in) long with only 13–25 scythe-like leaflets.[14][15][16] It is listed as endangered in the IUCN Red List of threatened species due to loss of habitat for building and industrial plantations.[17]
  • A. altissima var. sutchuenensis, which differs in having red branchlets.[14][15]

Distribution and habitat[edit]

A. altissima is native to northern and central China, Taiwan[18] and northern Korea.[19] In Taiwan it is present as var. takanai.[17] In China it is native to every province except Gansu, Heilongjiang, Hainan, Jilin, Ningxia, Qinghai, Xinjiang, and Tibet.[14]

The tree prefers moist and loamy soils, but is adaptable to a very wide range of soil conditions and pH values. It is drought-hardy, but not tolerant of flooding. It also does not tolerate deep shade.[4] In China it is often found in limestone-rich areas.[15] The tree of heaven is found within a wide range of climatic conditions.[4] In its native range it is found at high altitudes in Taiwan[17] as well as lower ones in mainland China.[5] In the U.S. it is found in arid regions bordering the Great Plains, very wet regions in the southern Appalachians, cold areas of the lower Rocky Mountains and throughout much of the California Central Valley. Prolonged cold and snow cover cause dieback, though the trees re-sprout from the roots.[4]

Ailanthus altissima growing in Australia.

As an exotic plant[edit]

The earliest introductions of A. altissima to countries outside of its native range were to the southern areas of Korea as well as to Japan. It is possible that the tree is native to these areas, but it is generally agreed that the tree was a very early introduction.[20] Within China itself it has also been naturalised beyond its native range in areas such as Qinghai, Ningxia and Xinjiang.[15]

In 1784, not long after Jussieu had sent seeds to England, some were forwarded to the United States by William Hamilton, a gardener in Philadelphia. In both Europe and America it quickly became a favoured ornamental, especially as a street tree, and by 1840 it was available in most nurseries.[5][11] The tree was separately brought to California in the 1890s by Chinese immigrants who came during the California Gold Rush. It has escaped cultivation in all areas where it was introduced, but most extensively in the United States.[18] It has naturalised across much of Europe, including Germany,[21] Austria, Switzerland, the Czech Republic, the Pannonian region (i.e. southeastern Central Europe around the Danube river basin from Austria, Slovakia and Hungary south to the Balkan ranges) and most countries of the Mediterranean Basin.[19] In Montenegro[22] and Albania[23][24] A. altissima is widespread in both rural and urban areas and while in the first it was introduced as an ornamental plant, it very soon invaded native ecosystems with disastrous results and became an invasive species.[22] Ailanthus has also been introduced to Argentina,[18] Australia (where it is a declared weed in New South Wales and Victoria),[25] New Zealand (where it is listed under the National Pest Plant Accord and is classed an "unwanted organism"),[26] the Middle East and in some countries in South Asia such as Pakistan.[27]

In North America, A. altissima is present from Massachusetts in the east, west to southern Ontario, southwest to Iowa, south to Texas, and east to the north of Florida. On the west coast it is found from New Mexico west to California and north to Washington.[4][18] In the east of its range it grows most extensively in disturbed areas of cities, where it was long ago present as a planted street tree.[5][18] It also grows along roads and railways. For example, a 2003 study in North Carolina found the tree of heaven was present on 1.7% of all highway and railroad edges in the state and had been expanding its range at the rate of 4.76% counties per year.[28] Similarly, another study conducted in southwestern Virginia determined that the tree of heaven is thriving along approximately 30% of the state's interstate highway system length or mileage.[29] It sometimes enters undisturbed areas as well and competes with native plants.[18] In western North America it is most common in mountainous areas around old dwellings and abandoned mining operations.[30][31]

Ecology[edit]

A female bearing a heavy load of seeds in Valladolid, Spain

Ailanthus is an opportunistic plant that thrives in full sun and disturbed areas. It spreads aggressively both by seeds and vegetatively by root sprouts, re-sprouting rapidly after being cut.[4] It is considered a shade-intolerant tree and cannot compete in low-light situations,[32] though it is sometimes found competing with hardwoods, but such competition rather indicates it was present at the time the stand was established.[4] On the other hand, a study in an old-growth hemlock-hardwood forest in New York found that Ailanthus was capable of competing successfully with native trees in canopy gaps where only 2 to 15% of full sun was available. The same study characterised the tree as using a "gap-obligate" strategy in order to reach the forest canopy, meaning it grows rapidly during a very short period rather than growing slowly over a long period.[33] It is a short lived tree in any location and rarely lives more than 50 years.[4] Ailanthus is among the most pollution-tolerant of tree species, including sulfur dioxide, which it absorbs in its leaves. It can withstand cement dust and fumes from coal tar operations, as well as resist ozone exposure relatively well. Furthermore, high concentrations of mercury have been found built up in tissues of the plant.[18]

Ailanthus has been used to re-vegetate areas where acid mine drainage has occurred and it has been shown to tolerate pH levels as low as 4.1 (approximately that of tomato juice). It can withstand very low phosphorus levels and high salinity levels. The drought-tolerance of the tree is strong due to its ability to effectively store water in its root system.[18] It is frequently found in areas where few trees can survive. The roots are also aggressive enough to cause damage to subterranean sewers and pipes.[5] Along highways it often forms dense thickets in which few other tree species are present, largely due to the toxins it produces to prevent competition.[18]

Female tree growing in Chicago, Illinois

Ailanthus produces an allelopathic chemical called ailanthone, which inhibits the growth of other plants.[34] The inhibitors are strongest in the bark and roots, but are also present in the leaves, wood and seeds of the plant. One study showed that a crude extract of the root bark inhibited 50% of a sample of garden cress (Lepidium sativum) seeds from germinating. The same study tested the extract as an herbicide on garden cress, redroot pigweed (Amaranthus retroflexus), velvetleaf (Abutilon theophrasti), yellow bristlegrass (Setaria pumila), barnyard grass (Echinochloa crusgalli), pea (Pisum sativum cv. Sugar Snap) and maize (Zea mays cv. Silver Queen). It proved able to kill nearly 100% of seedlings with the exception of velvetleaf, which showed some resistance.[35] Another experiment showed a water extract of the chemical was either lethal or highly damaging to 11 North American hardwoods and 34 conifers, with the white ash (Fraxinus americana) being the only plant not adversely affected.[36] The chemical does not, however, affect the tree of heaven's own seedlings, indicating that A. altissima has a defence mechanism to prevent autotoxicity.[34] Resistance in various plant species has been shown to increase with exposure. Populations without prior exposure to the chemicals are most susceptible to them. Seeds produced from exposed plants have also been shown to be more resistant than their unexposed counterparts.[37]

Leaves in autumn

The tree of heaven is a very rapidly growing tree, possibly the fastest growing tree in North America.[38] Growth of one to two metres (3.3 to 6.6 ft) per year for the first four years is considered normal. Shade considerably hampers growth rates. Older trees, while growing much slower, still do so faster than other trees. Studies found that Californian trees grew faster than their East Coast counterparts, and American trees in general grew faster than Chinese ones.[38]

In northern Europe the tree of heaven was not considered naturalised in cities until after the Second World War. This has been attributed to the tree's ability to colonise areas of rubble of destroyed buildings where most other plants would not grow.[19] In addition, the warmer microclimate in cities offers a more suitable habitat than the surrounding rural areas (it is reckoned that the tree requires a mean annual temperature of 8 degrees Celsius to grow well, which limits its spread to more northern and higher altitude areas). For example, one study in Germany found the tree of heaven growing in 92% of densely populated areas of Berlin, 25% of its suburbs and only 3% of areas outside the city altogether.[19] In other areas of Europe this is not the case as climates are mild enough for the tree to flourish. It has colonised natural areas in Hungary, for example, and is considered a threat to biodiversity at that country's Aggtelek National Park.[19]

Several species of Lepidoptera utilise the leaves of ailanthus as food, including the Indian moon moth (Actias selene) and the common grass yellow (Eurema hecabe). In North America the tree is the host plant for the ailanthus webworm (Atteva aurea), though this ermine moth is native to Central and South America and originally used other members of the mostly tropical Simaroubaceae as its hosts.[39] In its native range A. altissima is associated with at least 32 species of arthropods and 13 species of fungi.[15]

Due to the tree of heaven's weedy habit, landowners and other organisations often resort to various methods of control in order to keep its populations in check. For example, the city of Basel in Switzerland has an eradication program for the tree.[19] It can be very difficult to eradicate, however. Means of eradication can be physical, thermal, managerial, biological or chemical. A combination of several of these can be most effective, though they must of course be compatible. All have some positive and negative aspects, but the most effective regimen is generally a mixture of chemical and physical control. It involves the application of foliar or basal herbicides in order to kill existing trees, while either hand pulling or mowing seedlings in order to prevent new growth.[40][note 1]

Uses[edit]

A male ailanthus silkmoth from the Texas A&M University insect collection

In addition to its use as an ornamental plant, the tree of heaven is also used for its wood, medicinal properties, and as a host plant to feed silkworms of the moth Samia cynthia, which produces silk that is stronger and cheaper than mulberry silk, although with inferior gloss and texture. It is also unable to take dye. This type of silk is known under various names: "pongee", "eri silk" and "Shantung silk", the last name being derived from Shandong Province in China where this silk is often produced. Its production is particularly well known in the Yantai region of that province. The moth has also been introduced in the United States.[5]

The pale yellow, close-grained and satiny wood of ailanthus has been used in cabinet work.[41] It is flexible and well suited to the manufacture of kitchen steamers, which are important in Chinese cuisine for cooking mantou, pastries and rice. Zhejiang Province in eastern China is most famous for producing these steamers.[5] It is also considered a good source of firewood across much of its range as it moderately hard and heavy, yet readily available.[42] The wood is also used to make charcoal for culinary purposes.[43] There are problems with using the wood as lumber, however. Because the trees exhibit rapid growth for the first few years, the trunk has uneven texture between the inner and outer wood, which can cause the wood to twist or crack during drying. Techniques have been developed for drying the wood so as to prevent this cracking, allowing it to be commercially harvested. Although the live tree tends to have very flexible wood, the wood is quite hard once properly dried.[44]

Cultivation[edit]

Tree of heaven is a popular ornamental tree in China and valued for its tolerance of difficult growing conditions.[15] It was once very popular in cultivation in both Europe and North America, but this popularity dropped, especially in the United States, due to the disagreeable odor of its blossoms and the weediness of its habit. The problem of odor was previously avoided by only selling pistillate plants since only males produce the smell, but a higher seed production also results.[11] Michael Dirr, a noted American horticulturalist and professor at the University of Georgia, reported meeting, in 1982, a grower who could not find any buyers. He further writes (his emphasis):

For most landscaping conditions, it has no value as there are too many trees of superior quality; for impossible conditions this tree has a place; selection could be made for good habit, strong wood and better foliage which would make the tree more satisfactory; I once talked with an architect who tried to buy Ailanthus for use along polluted highways but could not find an adequate supply [...]

—Michael A. Dirr,  Manual of Woody Landscape Plants[45]

In Europe, however, the tree is still used in the garden to some degree as its habit is generally not as invasive as it is in America. In the United Kingdom it is especially common in London squares, streets, and parks, though it is also frequently found in gardens of southern England and East Anglia. It becomes rare in the north, occurring only infrequently in southern Scotland. It is also rare in Ireland.[46] In Germany the tree is commonly planted in gardens.[21] The tree has furthermore become unpopular in cultivation in the west because it is short-lived and that the trunk soon becomes hollow, making trees more than two feet in diameter unstable in high winds.[41]

A few cultivars exist, but they are not often sold outside of China and probably not at all in North America:

  • ‘Hongye’ – The name is Chinese and means "red leaves". As the name implies it has attractive vivid red foliage[47]
  • ‘Thousand Leaders’[47]
  • ‘Metro’ – A male cultivar with a tighter crown than usual and a less weedy habit[48]
  • ‘Erythrocarpa’ – The fruits are a striking red[48]
  • ‘Pendulifolia’ – Leaves are much longer and hang elegantly[48]

Medicinal[edit]

Nearly every part of A. altissima has some application in Chinese traditional medicine. One of the oldest recipes, recorded in a work from 732 AD, is used for treating mental illness. It involved chopped root material, young boys' urine and douchi. After sitting for a day the liquid was strained out and given to the patient over the course of several days.[5]

Another source from 684 AD, during the Tang dynasty and recorded in Li Shizhen's Compendium of Materia Medica, states that when the leaves are taken internally, they make one incoherent and sleepy, while when used externally they can be effectively used to treat boils, abscesses and itches. Yet another recipe recorded by Li uses the leaves to treat baldness. This formula calls for young leaves of ailanthus, catalpa and peach tree to be crushed together and the resulting liquid applied to the scalp to stimulate hair growth.[5]

The dried bark, however, is still an officinal drug and is listed in the modern Chinese materia medica as chun bai pi (Chinese: 椿白皮; pinyin: chūnbáipí), meaning "white bark of spring". Modern works treat it in detail, discussing chemical constituents, how to identify the product and its pharmaceutical uses. It is prepared by felling the tree in fall or spring, stripping the bark and then scraping off the hardest, outermost portion, which is then sun-dried, soaked in water, partially re-dried in a basket and finally cut into strips. The bark is said to have cooling and astringent properties and is primarily used to treat dysentery, intestinal hemorrhage, menorrhagia and spermatorrhea. It is only prescribed in amounts between 4 and 10 grams, so as not to poison the patients. Li's Compendium has 18 recipes that call for the bark. Asian and European chemists have found some justification for its medical use as it contains a long list of active chemicals that include quassin and saponin, while ailanthone, the allelopathic chemical in the tree of heaven, is a known antimalarial agent.[49] It is available in most shops dealing in Chinese traditional medicine.[5] A tincture of the root-bark has been used successfully in treating cardiac palpitation, asthma and epilepsy.[8]

The samaras are also used in modern Chinese medicine under the name feng yan cao (simplified Chinese: 凤眼草; traditional Chinese: 鳳眼草; pinyin: fèngyǎncǎo), meaning "herbal phoenix eye". They are used as a hemostatic agent, spermatorrhea and for treating patients with blood in their feces or urine. It was clinically shown to be able to treat trichomoniasis, a vaginal infection caused by the protozoan Trichomonas vaginalis.[5] In the West, an extract of the bark sold under the synonym A. glandulosa is sometimes used as an herbal remedy for various ailments including cancer.[50]

Anecdotal evidence suggests that the plant may be mildly toxic. The noxious odours have been associated with nausea and headaches, as well as with contact dermatitis reported in both humans and sheep, who also developed weakness and paralysis. It contains a quinone irritant, 2,6-dimethoxybenzoquinone, as well as active quassinoids (ailanthone itself being one) which may account for these effects, but they have, however, proved difficult or impossible to reproduce in humans and goats. In one trial a tincture from the blossom and foliage caused nausea, vomiting and muscular relaxation.[49]

Ailanthus altissima has potent anti-anaphylactic and anti-inflammatory properties.[51]

Culture[edit]

China[edit]

In addition to the tree of heaven's various uses, it has also been a part of Chinese culture for many centuries and has more recently attained a similar status in the west. Within the oldest extant Chinese dictionary, the Erya, written in the 3rd century BC, the tree of heaven is mentioned second among a list of trees. It was mentioned again in a materia medica compiled during the Tang dynasty in 656 AD. Each work favoured a different character, however, and there is still some debate in the Chinese botanical community as to which character should be used. The current name, chouchun (Chinese: 臭椿; pinyin: chòuchūn), means "stinking spring", and is a relatively new appellation. People living near the lower Yellow River know it by the name chunshu (simplified Chinese: 椿树; traditional Chinese: 椿樹; pinyin: chūnshù), meaning "spring tree". The name stems from the fact that A. altissima is one of the last trees to come out of dormancy, and as such its leaves coming out would indicate that winter was truly over.[5]

In Chinese literature, ailanthus is often used for two rather extreme metaphors, with a mature tree representing a father and a stump being a spoiled child. This manifests itself occasionally when expressing best wishes to a friend's father and mother in a letter, where one can write "wishing your ailanthus and daylily are strong and happy", with ailanthus metaphorically referring to the father and daylily to the mother. Furthermore, one can scold a child by calling him a "good-for-nothing ailanthus stump sprout", meaning the child is irresponsible. This derives from the literature of Zhuangzi, a Taoist philosopher, who referred to a tree that had developed from a sprout at the stump and was thus unsuitable for carpentry due to its irregular shape. Later scholars associated this tree with ailanthus and applied the metaphor to children who, like stump sprouts of the tree, will not develop into a worthwhile human being if they don't follow rules or traditions.[52]

United States[edit]

The 1943 book A Tree Grows in Brooklyn by Betty Smith uses the tree of heaven as its central metaphor, using it as an analogy for the ability to thrive in a difficult environment. At the time as well as now, ailanthus was common in neglected urban areas.[11][53] She writes:

There's a tree that grows in Brooklyn. Some people call it the Tree of Heaven. No matter where its seed falls, it makes a tree which struggles to reach the sky. It grows in boarded up lots and out of neglected rubbish heaps. It grows up out of cellar gratings. It is the only tree that grows out of cement. It grows lushly...survives without sun, water, and seemingly earth. It would be considered beautiful except that there are too many of it.

A Tree Grows in BrooklynIntroduction

Ailanthus is also sometimes counter-nicknamed "tree from hell" due to its prolific invasiveness and the difficulty in eradicating it.[53][54] In certain parts of the United States, the species has been nicknamed the "ghetto palm" because of its propensity for growing in the inhospitable conditions of urban areas, or on abandoned and poorly maintained properties.[55][56]

Until March 26, 2008, a 60-foot (18 m)-tall member of the species was a prominent "centerpiece" of the sculpture garden at the Noguchi Museum in the borough of Queens in New York City. The tree had been spared by the sculptor Isamu Noguchi when in 1975 he bought the building which would become the museum and cleaned up its back lot. The tree was the only one he left in the yard, and the staff would eat lunch with Noguchi under it. "[I]n a sense, the sculpture garden was designed around the tree", said a former aide to Noguchi, Bonnie Rychlak, who later became the museum curator. By 2008, the old tree was found to be dying and in danger of crashing into the building, which was about to undergo a major renovation. The museum hired the Detroit Tree of Heaven Woodshop, an artists' collective, to use the wood to create benches, sculptures and other amenities in and around the building. The tree's rings were counted, revealing its age to be 75, and museum officials hoped it would regenerate from a sucker.[57]

Europe[edit]

Ingo Vetter, a German artist and professor of fine arts at Umeå University in Sweden, was influenced by the idea of the "ghetto palm" and installed a living ailanthus tree taken from Detroit for an international art show called Shrinking Cities at the Kunst-Werke Institute for Contemporary Art in Berlin in 2004.[55][56]

See also[edit]

Notes[edit]

  1. ^ For a more thorough discussion, see the entry for Ailanthus ailtissima in the Wikimanual of Gardening at Wikibooks.

References[edit]

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  35. ^ Heisy, Rod M. (May 1990). "Allelopathic and Herbicidal Effects of Extracts from Tree of Heaven". American Journal of Botany 77 (5): 662–670. doi:10.2307/2444812. JSTOR 2444812. 
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  51. ^ Kang TH, Choi IY, Kim SJ, Moon PD, Seo JU, Kim JJ, An NH, Kim SH, Kim MH, Um JY, Hong SH, Kim HM, Jeong HJ Ailanthus altissima Swingle has anti-anaphylactic effect and inhibits inflammatory cytokine expression via suppression of nuclear factor-kappaB activation." In Vitro Cell Dev Biol Anim. 2010 Jan;46(1):72-81
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In Pakistan it is cultivated as a roadside tree on hills.
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Names and Taxonomy

Taxonomy

Comments: Called Ailanthus glandulosa in older literature.

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The scientific name of tree-of-heaven is Ailanthus altissima (Mill.) Swingle. It is in quassia (Simaroubaceae) [71,104,105,114,136,137,158,199,214,250,280,317,323,324], a family of mostly tropical woody plants [285].
  • 104. Gleason, Henry A.; Cronquist, Arthur. 1991. Manual of vascular plants of northeastern United States and adjacent Canada. 2nd ed. New York: New York Botanical Garden. 910 p. [20329]
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  • 114. Great Plains Flora Association. 1986. Flora of the Great Plains. Lawrence, KS: University Press of Kansas. 1392 p. [1603]
  • 136. Hitchcock, C. Leo; Cronquist, Arthur. 1973. Flora of the Pacific Northwest. Seattle, WA: University of Washington Press. 730 p. [1168]
  • 137. Hitchcock, C. Leo; Cronquist, Arthur; Ownbey, Marion; Thompson, J. W. 1961. Vascular plants of the Pacific Northwest. Part 3: Saxifragaceae to Ericaceae. Seattle, WA: University of Washington Press. 614 p. [1167]
  • 158. Kartesz, John T. 1999. A synonymized checklist and atlas with biological attributes for the vascular flora of the United States, Canada, and Greenland. 1st ed. In: Kartesz, John T.; Meacham, Christopher A. Synthesis of the North American flora (Windows Version 1.0), [CD-ROM]. Chapel Hill, NC: North Carolina Botanical Garden (Producer). In cooperation with: The Nature Conservancy; U.S. Department of Agriculture, Natural Resources Conservation Service; U.S. Department of the Interior, Fish and Wildlife Service. [36715]
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  • 285. Swearingen, Jil; Pannill, Phil. 2005. Fact sheet: Tree-of-heaven Ailanthus altissima (Mill.) Swingle, [Online]. In: Weeds gone wild: Alien plant invaders of natural areas. The Plant Conservation Alliance's Alien Plant Working Group (Producer). Available: http://www.nps.gov/plants/alien/fact/aial1.htm [2010, August 27]. [46267]
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  • 323. Wu, Z. Y.; Raven, P. H.; Hong, D. Y., eds. 2010. Flora of China, [Online]. Volumes 1-25. Beijing: Science Press; St. Louis, MO: Missouri Botanical Garden Press. In: eFloras. St. Louis, MO: Missouri Botanical Garden; Cambridge, MA: Harvard University Herbaria (Producers). Available: http://www.efloras.org/flora_page.aspx?flora_id=2 and http://flora.huh.harvard.edu/china. [72954]
  • 324. Wunderlin, Richard P. 1998. Guide to the vascular plants of Florida. Gainesville, FL: University Press of Florida. 806 p. [28655]
  • 71. Diggs, George M., Jr.; Lipscomb, Barney L.; O'Kennon, Robert J. 1999. Illustrated flora of north-central Texas. Sida Botanical Miscellany, No. 16. Fort Worth, TX: Botanical Research Institute of Texas. 1626 p. [35698]

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Common Names

tree-of-heaven

tree of heaven

stink tree

Chinese sumac

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Synonyms

Ailanthus altissima forma erythrocarpa (Carr.) Schneider [267]

Ailanthus glandulosa Desf. [153]
  • 153. Jepson, Willis Linn. 1925. A manual of the flowering plants of California. Berkeley, CA: University of California Press. 1238 p. [19365]
  • 267. Seymour, Frank Conkling. 1982. The flora of New England. 2nd ed. Phytologia Memoirs 5. Plainfield, NJ: Harold N. Moldenke and Alma L. Moldenke. 611 p. [7604]

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