Fire Effects Information System (FEIS)
FEIS Home Page
SPECIES: Fraxinus nigra



  Photo © 2004 Dr. Virginia Kline, University of Wisconsin-Madison.

Gucker, Corey L. 2005. Fraxinus nigra. In: Fire Effects Information System, [Online]. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory (Producer). Available: [].




black ash
basket ash
swamp ash

The scientific name of black ash is Fraxinus nigra Marsh. (Oleaceae) [20,51,63,101,110,121]. When citing literature that did not specify species or refers to multiple species within the ash genus (Fraxinus spp.), the common name ash will be used.



Black ash is listed as an endangered species in North Dakota. It is considered "imperiled because of rarity or because of other factors making it very vulnerable to extirpation from the state." This status typically describes species with "6 to 20 occurrences or few (1,000-3,000) remaining individuals" [87]. In Delaware, black ash is a "conservation concern." There are 6 to 20 "known occurrences or populations." Black ash may be susceptible to extinction from the state [82].


SPECIES: Fraxinus nigra
Black ash occurs in many northeastern U.S. states and in several of Canada's eastern provinces. The northernmost portion of black ash's range extends from Newfoundland to southeastern Manitoba [118]. Populations in North Dakota mark the westernmost distribution. Black ash occupies habitat in all of the Great Lake states and reaches its southern limit in northern Virginia [51,118].The U.S. Geological Survey provides a distributional map of black ash.

FRES11 Spruce-fir
FRES15 Oak-hickory
FRES17 Elm-ash-cottonwood
FRES18 Maple-beech-birch
FRES19 Aspen-birch

STATES/PROVINCES: (key to state/province abbreviations)



K081 Oak savanna
K093 Great Lakes spruce-fir forest
K094 Conifer bog
K096 Northeastern spruce-fir forest
K097 Southeastern spruce-fir forest
K098 Northern floodplain forest
K099 Maple-basswood forest
K100 Oak-hickory forest
K101 Elm-ash forest
K102 Beech-maple forest
K103 Mixed mesophytic forest
K104 Appalachian oak forest
K106 Northern hardwoods
K107 Northern hardwoods-fir forest
K108 Northern hardwoods-spruce forest
K109 Transition between K104 and K106

5 Balsam fir
12 Black spruce
13 Black spruce-tamarack
14 Northern pin oak
16 Aspen
17 Pin cherry
18 Paper birch
19 Gray birch-red maple
21 Eastern white pine
23 Eastern hemlock
24 Hemlock-yellow birch
25 Sugar maple-beech-yellow birch
26 Sugar maple-basswood
27 Sugar maple
28 Black cherry-maple
30 Red spruce-yellow birch
31 Red spruce-sugar maple-beech
32 Red spruce
33 Red spruce-balsam fir
34 Red spruce-Fraser fir
35 Paper birch-red spruce-balsam fir
37 Northern white-cedar
38 Tamarack
39 Black ash-American elm-red maple
42 Bur oak
57 Yellow-poplar
58 Yellow-poplar-eastern hemlock
59 Yellow-poplar-white oak-northern red oak
60 Beech-sugar maple
61 River birch-sycamore
62 Silver maple-American elm
63 Cottonwood
64 Sassafras-persimmon
65 Pin oak-sweetgum
87 Sweetgum-yellow-poplar
93 Sugarberry-American elm-green ash
94 Sycamore-sweetgum-American elm
107 White spruce
108 Red maple
203 Balsam poplar
236 Bur oak
252 Paper birch
253 Black spruce-white spruce


Black ash is recognized as a dominant species in the following vegetation classifications:

IL: Horseshoe Bottom Nature Preserve [75]
MI: northern Lower [145]
MN: Voyageur National Park [72]
Northeastern U.S.: [47,104]
WI: [30]
MB: [146]
NS: Saint Lawrence River Valley [32]
southeastern Canada: [47,104]

American elm (Ulmus americana) is listed as a codominant in many black ash habitat and community type descriptions. It is important to note that many American elm populations declined considerably following the introduction of Dutch elm disease in the early 1930s. Some black ash habitat types and community descriptions are from dated literature, and the presence of American elm may be exaggerated in studies that predate population losses to Dutch elm disease.

Black ash-American elm-red maple forest cover type: The black ash-American elm-red maple (Acer rubrum) forest cover type occurs throughout the northeastern United States and eastern Canada. Of the 3 major species, black ash is most restricted to this vegetation type. In the Great Lake states and the western Canadian Range, balsam poplar (Populus balsamifera ssp. balsamifera), balsam fir (Abies balsamea), and yellow birch (Betula alleghaniensis) are common to this cover type. Silver maple (Acer saccharinum), swamp white oak (Quercus bicolor), sycamore (Platanus occidentalis), pin oak (Q. palustris), black tupelo (Nyssa sylvatica), and eastern cottonwood (Populus deltoides ssp. deltoides) are typical of the black ash-American elm-red maple forests of northern Ohio and Indiana. In New England and eastern Canada, sweet birch (B. lenta), paper birch (B. papyrifera), gray birch (B. populifolia), silver maple, and black spruce (Picea mariana) are common. The cover type in New York is habitat for white ash (Fraxinus americana), slippery elm (U. rubra), rock elm (U. thomasii), yellow birch, black tupelo, sycamore, eastern hemlock (Tsuga canadensis), and bur oak (Q. macrocarpa) [104]. The black ash-American elm-red maple cover type in northern Wisconsin and the Upper Peninsula of Michigan is dominated by black ash. On very poorly drained sites, stands are almost pure black ash, and black ash is considered a climax species [39].

Northeastern U.S. and eastern Canada: Black ash is common to many deciduous, coniferous, and mixed lowland forest types in the eastern U.S. and Canada.

In the northern Great Lake states, the greatest black ash biomass production is reported for elm-ash-maple (Ulmus-Fraxinus-Acer spp.) forests. Black ash biomass yields are 2nd greatest in northern white-cedar (Thuja occidentalis) forests and 3rd greatest in balsam fir forests [113]. Tamarack (Larix laricina), balsam fir, northern white-cedar, and red maple are found with black ash in lowland spruce-fir forests of New England, the Great Lake states, and the boreal region of Canada [12,42]. Black spruce-speckled alder (Alnus rugosa) communities are typical of water-logged soils in eastern Canada, the northern Great Lake states, and Maine [31]. Red spruce (P. rubens)-balsam fir vegetation types extending as far south as West Virginia and as far north as maritime provinces of Canada may include black ash trees [52].

Black ash usually comprises less than 20% of the basal area in sugar maple (Acer saccharum)-dominated vegetation in the Great Lake states, New York, New England, Ontario, Quebec, and portions of the Appalachians. In eastern Canada, black ash occupies sugar maple-yellow birch habitats [48]. In northern Wisconsin, upper Michigan, southern Ontario, and southern Quebec black ash is a "less common associate" of the eastern hemlock-yellow birch vegetation type that grades into black ash-American elm-red maple forests on wetter sites [47].

In wet calcareous mixed woods of the maritime provinces, black ash is dominant, and eastern white-cedar and red maple are both typical. These forests occur on poorly drained organic soils. In the early 1800s, black ash occurred in these forests with 6.5% frequency, but in 1993 the frequency of ash was less than 1%. Land clearing, wetland drainage, and tree harvest practices of European settlers are at least partially responsible for the decline in black ash habitat [78].

Illinois: Black ash is common in Illinois' seep and swamp vegetation where silver maple and green ash (F. pennsylvanica) are also typical [75].

Michigan: In northern Lower Michigan, seasonally flooded black ash-alder (Alnus spp.) swamps experience extreme daily and seasonal temperature changes. Black ash also occupies hardwood swamps where basswood (Tilia americana) and northern white-cedar are typical. Hardwood swamps are also seasonally flooded but do not occur in frost pockets. The basal area of black ash in black ash-alder swamps is 7.1±13.1 (s) m²/ha and in hardwood swamps is 6.1±6 m²/ha [145].

In the Indian Bowl area of southwestern Michigan, black ash occurs in tamarack swamps, thought to be an earlier stage of succession to southern hardwood forest. The Indian Bowl is frequently flooded, has organic soils high in calcium, and occupies elevations of 600 to 750 feet (183-229 m) [68]. On the Isle Royale, black ash occurs in 40-year-old paper birch-aspen (Populus spp.)-white spruce (Picea glauca) stands that revegetated burned areas after a late July fire in 1963 [54].

Minnesota: In Voyageurs National Park, researchers recognize 2 vegetation types dominated by black ash. The black ash-elm/trillium (Trillium ssp.) type occupies moist sites, with deep nutrient-rich soils. This type is uncommon but is considered climax. The black ash/yellow marsh marigold (Caltha palustris) habitat type is a climax type on sites that are better drained than those occupied by black ash-elm/trillium [72]. Buell and Bormann [24] recognize a stable basswood-balsam fir-black ash vegetation type on poorly drained sites of Minnesota's Red Lake Indian Reservation.

In the Lake Agassiz Peatlands of Minnesota, black ash dominates the overstory of swamp forests that lie on peatland edges and receive mineral-rich water. Other typical species may include northern white-cedar, tamarack, black spruce, and speckled alder [55]. In the Boundary Waters Canoe Area, black ash occurs with low frequencies in balsam fir-paper birch and red maple-quaking aspen (Populus tremuloides)-paper birch communities [88].

New York: Black ash is common in swamps and on floodplains of New York. In the Adirondacks, black ash occurs in black spruce swamps. Small northern white-cedar, tamarack, and red maple trees also populate these sites [10]. Red maple dominates the hardwood swamps in poorly drained depressions with inorganic soils throughout New York. Black ash, American elm, swamp white oak, butternut (Juglans cinerea) and/or bitternut hickory (Carya cordiformis) may also associate with red maple hardwood swamps. Green ash, red maple, slippery elm, American hornbeam (Carpinus caroliniana), and northern white-cedar may associate with black ash in lowland sites along the Hudson River. Along rivers and lake shores of central and western New York where conditions are uniformly wet and seasonal water fluctuations are low, silver maple-ash swamps are common. Silver maple often makes up 70% of the canopy cover, but black ash, green ash, and white ash are also typical [97]. Huenneke [60] describes black ash in the eastern hemlock-yellow birch-red maple wet vegetation type near Cayuga Lake.

Ohio: Black ash is a dominant species in closed-canopy lowland forests at an average elevation of 860 feet (262 m) in central Ohio; other common species are American elm, honey-locust (Gleditsia triacanthos), and pin oak [16]. Braun [20] describes black ash in northern coniferous forests, eastern hemlock-pine (Pinus spp.)-northern hardwood forests, and beech-maple forests of Ohio. On poorly drained sites that are part of northwestern Ohio's Black Swamp, black ash occurs with silver maple, green ash, American elm, bur oak, and shellbark hickory (Carya laciniosa) [17]. In swamp forests of west-central Ohio's Cedar Bog, northern white-cedar, red maple, black ash, and yellow-poplar (Liriodendron tulipifera) dominate the overstory [27].

Pennsylvania: Black ash occurs in the pin oak-sweet gum (Liquidambar styraciflua) forest cover type in Gettysburg National Military Park and Eisenhower National Historic Site in south-central Pennsylvania [144].

Vermont: In eastern hemlock-northern hardwood forests of central Vermont, sugar maple, beech, white ash, and yellow birch dominate the canopy, but black ash, basswood, eastern hemlock, and American elm also populate the canopy [18].

Wisconsin: In the black ash-yellow birch-eastern hemlock hardwood swamps of Wisconsin's northern lowland forests, black ash is a mid-sized tree (45-70 feet (14-21 m)) with a narrow crown [30]. In northern white-cedar-balsam fir-black ash swamps of northern Wisconsin, black ash is most important on compacted organic soils that are inundated for much of the growing season [25]. Winget and others [140] describe black ash, northern white-cedar, and yellow birch communities on very poorly drained, black muck soils in northern Wisconsin where even in mid-summer the ground water is just 12 inches (3 cm) beneath the soil surface. Black ash is occasional in southern Wisconsin's elm-ash savannah that is restricted to wet meadow sites. Important canopy species include silver maple, river birch (B. nigra), green ash, and swamp white oak [21].

Manitoba: Black ash is now the dominant overstory species in hardwood and mixed hardwood forests of Manitoba that were dominated by American elm in the past. Boxelder (Acer negundo) often dominates the subcanopy layer. This community occurs along small stream floodplains on deep, loamy-clay soils with poor to very poor drainage [146].

In the early 1970s, black ash colonized the Portage la Prairie grassland area of Manitoba. While this area experiences periodic spring flooding, it does not support the wet conditions most often associated with the distribution of black ash. The successful establishment of black ash in prairie grasslands suggests that high moisture levels are not the only factor limiting the range of black ash. Other tree species associated with the Portage la Prairie include bur oak, American elm, green ash, and red-osier dogwood (Cornus sericea ssp. sericea) [102].

Quebec: In the Haut-Saint-Laurent region, the black ash-American elm habitat type occupies hydric sites with little slope and a shallow water table. Pooled water is common throughout the year in this habitat type. Openings in the canopy created by the death of most American elm trees due to Dutch elm disease now support several understory species including blackberries (Rubus spp.), common pricklyash (Zanthoxylum americanum), and broadleaf enchanter's nightshade (Circaea lutetiana ssp. canadensis) [22]. In southern Quebec, black ash is typical of balsam fir-northern white-cedar forests on thick wet soils [42].


SPECIES: Fraxinus nigra
This description provides characteristics that may be relevant to fire ecology, and is not meant for identification. Keys for identification are available [20,51,85,101,110,118,121,141].

Black ash is a native tree described by some as the "slenderest broadleaf tree in the forest" [26]. Black ash is normally a small tree just 40 to 60 feet (12-18 m) tall but can reach 90 feet (27 m) in height [26,59]. Branches do not appear until high up on the trunk; tall trees may be without branches for up to 50 feet (15 m) [26,118]. The narrow trunk is rarely more than 2 feet (0.6 m) in diameter and is often leaning or bent [59]. Black ash bark is soft with shallow grooves that give a scaly or flaky appearance [20,51,59,118]. The shallow, spreading black ash root system makes this species prone to windthrow [39,59]. Fine roots that measure between 0.1 and 0.4 mm in diameter are long and rarely branch [23]. A discussion of black ash mycorrhizal root associations is available [80], as is an in-depth investigation of the microscopic appearance of black ash roots that may be useful in identification [23].

The perfect and/or unisexual black ash flowers are described as tightly packed panicles or racemes and arise from leaf scar axils produced the previous year [20,51]. The opposite leaves are 10 to 16 inches (25-40 cm) long and pinnately compound [51,59,110,118]. Leaflets often occur in groups of 9 but may number 7 or 11. They measure 2 to 8 inches (5-20 cm) long by 0.6 to 2.4 inches (1.5-6 cm) wide [20,51,59,118,121]. The black ash fruit is a sometimes twisted samara most often containing 1 seed but sometimes containing 2 or 3 seeds [20,51,110]. The fruit measures 1 to 1.5 inches (2.5-4 cm) long and is produced in clusters [59,112,118,121]. Often fruits have a spicy odor [112].

Life span: Black ash is a long-lived tree with a relatively rapid growth rate [122]. Heinselman [57] suggests that the typical life span of black ash is 150 years. However, many black ash trees on the edges of Lake Duparquet in northwestern Quebec were over 200 years old, and the oldest tree in the area was 319 years old [127]. In northeastern Minnesota, several black ash trees in relatively pure stands were 250 year old. At 100 years old, black ash trees can be between 39 and 75 feet (12-23 m). Height is not well correlated with age when trees are more than 80 to 100 years old [71].


Black ash is capable of sexual and asexual reproduction. Asexual regeneration typically follows top-kill and is through vegetative stump or root crown sprouting [39,77,112].

Breeding system: Black ash can produce perfect or separate male and female flowers [20,51]. Hosie [59] suggests that male, female, and bisexual flowers can occur on a single tree. In the northeastern U.S., the smallest tree to flower was 3 inches (8 cm) in diameter [142].

Pollination: Ashes are wind pollinated [142].

Seed production: Large viable seed crops are produced intermittently by black ash. The ability to produce seed occurs when trees are 30 to 40 years old [57]. In a review, Sims and others [112] report that good crops of seed are produced at 1- to 8-year intervals. Similarly, Sutherland and others [122] suggest 5 or more years pass between good black ash seed production. For 25 years, researchers monitored black ash seed production in northeastern Wisconsin. They found that seed production was 61% to 100% of full crop for 28% of this time but was less than 36% of full crop for 68% of the time [49]. In 2 years of seed collection in southeastern Michigan, researchers collected a total of 98,032 seeds from 42 different species. During the course of this study black ash failed to produce any "potentially viable seed" [83].

Seed dispersal: The timing of fruit shed and weather conditions can affect the dispersal distances for black ash seed. Sutherland and others [122] report that winds can transport seeds 328 feet (100 m) or more away from the parent tree. Curtis [30] called winter-shed fruits "ice boats" and suggested that long-distance dispersal is likely under these conditions. No actual distances were reported.

Seed banking: Several researchers report that black ash seeds can remain viable for up to 8 years under natural conditions [112,122].

Germination: The germination of black ash seed is a multistage process of stratification and scarification that often takes 2 to 3 years under natural conditions [30,112]. The embryo is immature when seeds are shed and requires warmth and moisture to fully develop. When fully ripe, the embryo is still dormant and requires a cold, moist period to break dormancy. Seeds germinate best on peat or mineral soils with high organic content [30] and can germinate in litter or when covered by 0.5 to 0.75 inch (1-2 cm) of soil [39].

Steinbauer [116] conducted in-depth studies of black ash seed germination. He found that at the time of seed shed the embryo is differentiated into the hypocotyl, epicotyl, and cotyledons, but the embryo is just 1/2 to 2/3rd the size of the seed. Embryos attain maximum size (0.5 inch (14 mm)) after 2 to 3 months at 68 °F (20 °C). Germination does not immediately follow and is likely delayed by mechanical restrictions of the endosperm, suberized layer, and/or seed coat. The digestion process necessary for germination is most efficient after 2 to 3 months at 41 °F (5 °C). Higher temperatures (68-86 °F (20-30 °C)) allow the embryo to break mechanical barriers and germination begins [116]. In the laboratory, maximum germination (87%) of black ash seed occurred after seeds were ripened in peat moss for 18 weeks at 70 °F (21 °C) and then exposed to 39 °F (4 °C) temperatures for 24 weeks [133,134].

Seedling establishment/growth: Black ash seedlings establish under canopy shade on a variety of soils [122]. In a review, Sims and others [112] report that seedling growth is rapid. Seedlings may reach 2 inches (5 cm) in the first 2 weeks of growth. In 1 year, seedlings are often 6 inches (15 cm) tall. Seedling survival is reportedly best at 45% to 50% full sun conditions [112]. While seedlings can establish under a canopy, they will eventually need canopy release for long-term survival [122]. Curtis [30] reports that high densities of black ash seedlings are rare [30]. Others suggest that grass and brush growth on the site can disrupt successful establishment [39].

Bell [11] monitored the growth and mortality rates for an average of 6 black ash trees along Hickory Creek in Illinois. Over the 18 years of the study, the average mean annual growth rate was 3.8±3 (s) mm/year and mortality was 3%±2.2%/year.

Researchers followed the establishment and survival of black ash, green ash, and white ash seedlings in open meadows and in upland and lowland young, successional, and closed-canopy forests of central Ohio. Ashes made up 69.9% of the 2,553 seedlings monitored. Significantly more (p≤0.05) ash seedlings emerged on lowland sites. Average ash seedling production was 241±21(s x) new seedlings/100 m²/year from 1984 to 1993. In 1988 and 1990, seedling production peaked at approximately 800 to 1,000 new seedlings/100 m². Production in 1988 and 1990 was significantly greater (p≤0.05) than for any other year. Peak production was not correlated with any observed annual or seasonal climate events, and the authors suggest that production peaks related to black ash's masting behavior. The average life span of ash seedlings was 5 to 7 months. The seedling population produced in June of 1990 was 916. By October of the same year, 66.7% were dead; by May of 1991, 96.6% were dead. Survivorship was likely affected by white-tailed deer browsing; deer occurred in densities of 0.6 to 0.7 animal/ha in the area [16].

Potential changes in growth: Several factors may affect the growth rate and/or growth form of black ash. In open canopy conditions, black ash exhibits a broader canopy than trees grown in closed-canopy forests [26]. The growth rate of black ash is slower on sites with organic peat and muck soils. Trees are just 30 to 45 feet (9-14 m) after 50 years of growth and only 50 to 60 feet (15-18 m) in 100 years [39]. Immature plants severely browsed by white-tailed deer may develop a shrubby growth form. A single year free of browsing pressure, however, is enough to allow production of a leader branch [30].

Asexual regeneration: Vegetative reproduction is common following damage or top-kill [30]. In reviews, black ash is described as a "vigorous sprouter" following fire, browsing, or cutting. Sprouts are produced from adventitious buds located on the sides of stumps or root crowns [39,112]. Black ash produces 7 to 17 stem sprouts when cut [77].

Asexual vs. sexual regeneration: Along Lake Duparquet in northwestern Quebec, researchers studied numerous characteristics of black ash's sexually and asexually produced plants. In this region, sprouts have higher and more constant mortality rates than seedlings, and sexually reproduced stems reach older ages and produce larger diameters than sprouts. Seedlings more often than sprouts reach canopy height. However, on exposed flooded sites, new (1st-year and older) seedlings experience higher mortality than sprouts, and vegetative reproduction predominates. Likely, the more developed sprout root system allows for a more rapid growth rate and an increased tolerance to flooding. Successful black ash seedling establishment requires periods free of prolonged, intensive flooding [127], but xeric conditions are not tolerated either [128].

Black ash occupies poorly drained swamps, bogs, woodlands, gullies, depressions, lowlands, foothills, valley flats, and stream and lake shores throughout its range [20,26,51,104,118]. In Michigan, black ash is found on shady soggy sites, with moderate nutrient levels, where the weather is cool [19]. Black ash is described in swamps and wet woodlands of Virginia's Blue Ridge Province [141]. In the southern boreal region of Quebec, black ash occurs on floodplains, lowest elevation terraces, and depositional flats with mineral soils [35]. In Minnesota's Glacial Lake Agassiz region, black ash populates peatland margins receiving minerotrophic waters [56].

Soils: Black ash grows on moist to wet, deep, fertile, mineral or organic soils [26]. Mottles and gleys are typical of soils supporting black ash (referenced in [112]). Soils associated with the black ash-American elm-red maple cover type are wet mucks or shallow peat soils that are frequently acidic with mid-levels of nutrients [104]. In hardwood and mixed hardwood vegetation types of Manitoba, black ash dominates the overstory. This vegetation occupies deep, fine, loamy-clay soils with poor to very poor drainage along small river floodplains [146].

Excessive moisture is tolerated by black ash [62], and growth is considered best on sites receiving moving, aerated water with soil pH values between 4.4 and 8.2 [143]. On Quebec's Lake Duparquet floodplain, where black ash occurs in pure stands, flooding records from 1915 to 1991 indicate that flooding occurs between April 7 and July 13. Flooding conditions last an average of 24 days and range between 0 and 65 days [127].

Several areas report more specific soil characteristics for black ash habitats. In southeastern Wisconsin, the relative importance of black ash is significantly ( p<0.05) greater on basin sites than floodplain sites. The basin site soils had significantly lower (p<0.0001) pH and significantly higher organic matter, calcium, and magnesium levels than floodplain soils [38]. In the Lake Agassiz Peatlands of Minnesota, black ash grows in rich swamp forests where the pH is 6 to 6.5, calcium and magnesium concentrations are high, and the moderately decomposed peat layer can be 1 to 6 feet (0.3-1.8 m) deep [55]. Northern Lower Michigan's black ash-alder swamps have an organic matter depth of 16±9 (s) inches (40±22 cm). The pH is 7.3±0.5 (4 inches (10 cm) below soil surface) and calcium and magnesium concentrations are 55.8±7.2 ppm and 20.6±3 ppm, respectively [145]. In alder swamps of Chippewa County, Michigan, where black ash occurs, soils are described as black mucks. These soils have a 10- to 11-inch- (26-28 cm) deep organic layer, pH levels between 6.4 and 6.8, and dissolved oxygen levels of 1.9/mg to 2.0/mg. These alder swamps remained wet until mid-July during the study [92].

Elevation: Very few areas report black ash elevation tolerances. Kudish [70] indicated that black ash occurs between 100 and 2,800 feet (31-853 m) in the Adirondack uplands of New York. In a review, researchers suggest that black ash occupies sites from sea level to the highest elevations in the northern part of its range; in the southern portion of black ash's range it is restricted to elevations above 2,000 feet (610 m) [143].

Weather: Black ash grows in regions with continental climates. Wright [143] described black ash habitats as humid, receiving between 20 and 45 inches (510-1,140 mm) of precipitation annually, having average low January temperatures of 0 to 32 °F (-18 to 0 °C), reaching an average high temperature of 70 °F (21 °C) in July, receiving annual snowfall levels of 30 to 100 inches (760-2,540 mm), and typically having 80 to 180 frost-free days [143].

Some suggest that weather events during the previous and current year's growing season of black ash are significantly (p<0.05) related to radial growth. In the Lake Duparquet region of northwestern Quebec, researchers found that April and May temperatures and August precipitation in the previous year positively affected radial growth in black ash. However, precipitation in the previous April, May, June, and October was negatively associated with radial growth. In the same growing year, April temperature and June precipitation were positively correlated with radial growth, but July precipitation was negatively correlated with black ash radial growth [125]. Information was slightly different when flooded and nonflooded sites were compared. On floodplain sites, growth was not generally affected by temperature, but precipitation in the previous year's August and June and the current year's December positively affected radial growth. On nonflooded sites, radial growth was negatively correlated with the previous year's August temperatures and the same year's May temperatures. The aforementioned relationships were significant (p<0.05) [126].

Black ash is most typical of late successional communities. On wet or swampy sites, black ash is often considered a climax species. The black ash-American elm-balsam fir vegetation type is "definitely climax" on peat soils in Itasca Park, Minnesota. Here the dominant species are successfully regenerating and the community appears stable [65]. Beech-maple swamp forests near Cleveland, Ohio, where black ash is common, are considered "climatic climax" communities [137]. In northern hardwood forests, the elm-ash vegetation type may be the climax community on poorly drained sites [130]. Conway [28] describes black ash as an important component of central Minnesota's oldest bog forests. Pure black ash stands on wet organic soils in north-central Ontario are also deemed climax [112].

Black ash does not represent a climax species in all cases. In mixed stands on moderately drained mineral soils black ash is regarded as a "sub-climax" species [112]. The black ash-American elm-red maple cover type is a "temporary climax" that typically succeeds to tamarack-black spruce communities but is subsequently replaced by northern white cedar [104]. Based on black ash's environmental tolerances, Graham [50] suggests it cannot be a climax species in eastern hemlock-hardwood forests of Michigan's Upper Peninsula. Because black ash does not often reproduce in thick layers of decaying material and is only moderately shade tolerant, it cannot be a climax species in eastern hemlock-hardwood forests.

Shade relationships: Reviews of black ash indicate that initially black ash is moderately shade tolerant but with increasing age, shade tolerance decreases [39,112]. Erdmann and others [39] suggest that seedlings develop best under 45% to 50% of full sunlight conditions.

Several researchers rated black ash's shade tolerance. Rudolf [105] gives black ash a shade tolerance rating of 2.4 on a scale that rates extremely shade-intolerant aspens a 0.7 and extremely shade-tolerant eastern hemlocks a 10. Kaminski and Jackson [62] rate black ash a 4 on a 10-point scale in which 1 corresponds to a complete intolerance of shading.

Response to disturbances: Powerful storms that blow down or damage trees are the most common disturbance in black ash forest habitats. Little is reported on fire, harvesting, or livestock grazing in these habitats. Black ash typically increases following events that provide openings in the canopy.

One and two years following the 1998 ice storm in northern New York, researchers observed black ash damage but did not find obvious changes in diameter distribution [103]. A July wind storm in 1983 in Minnesota's Anoka and Isanti counties caused substantial mortality in both eastern white pine (Pinus strobus) and northern pin oak (Quercus ellipsoidalis) forests. In both forest types, black ash density and basal area initially decreased following the event, but by the 7th poststorm year, black ash basal area and density exceeded prestorm measurements. A summary of the changes in black ash density and basal area is provided below [8]:

Oak forest 1983 b.s.* 1983 a.s. 1990 1993 1997
basal area (m²/ha) 0.8 0.7 1.4 2.0 2.3
density (individuals/ha) 172 148 292 384 376
Pine forest 1983 b.s. 1983 a.s. 1990 1993 1997
basal area (m²/ha) 0.2 0.2 0.6 0.9 1.2
density (individuals/ha) 89 79 155 165 162
*b.s.: before the storm, a.s.: after the storm

Following the widespread mortality of American elm trees in deciduous swamp communities of southeastern Michigan, researchers tracked changes in forest composition. Five to ten years after losing the American elm trees, black ash, red maple, and yellow birch became important overstory and understory species [9].

The following studies suggest that black ash is a resilient and opportunistic species regardless of disturbance type.

Researchers indicate that in northern Lower Michigan an increased presence of black ash and red maple is typical during the secondary succession of wet, bog sites following cutting or fire [45,46]. On a 1st order stream near Duluth, Minnesota, the selective removal of quaking aspen trees by American beavers increased the importance of black ash in the area [61]. Researchers visited upland swamp forests of northeastern Indiana 20 and 53 years after domestic livestock grazing was discontinued. Livestock grazed with "medium to heavy intensity" until 1930 in the area. Black ash did not appear on grazed sites in the 20th postgrazing year but was found in the 53rd postgrazing year. By 1984, the density of black ash on previously grazed sites was 93.9 stems/ha. In nearby ungrazed oak-hickory forests, black ash density was 89.0 stems/ha in 1931, 19.8 stems/ha in 1951, and 19.8 stems/ha in 1984. This study suggests that livestock grazing may prohibit successful black ash establishment [7].

Community change over time: Several have monitored the species composition changes in black ash communities and many have speculated about future changes in black ash forests. The succession of flood plains in north-central United States forests begins with the establishment of shade-intolerant, flood-tolerant pioneers (cottonwoods (Populus spp.) and willows (Salix spp.)). These species are later replaced by more shade-tolerant, flood-tolerant species (ashes and elms). The latest successional communities are dominated by American beeches, basswoods, and white oaks that tolerate heavy shade and flooding [107].

In the Cedar Bog fen of west-central Ohio, researchers assessed age class associations, population structure, density-diameter curves, and life history information that suggested black ash and red maple would increase but remain subdominant to northern white-cedar for the "foreseeable future" [27].

In a 30-year study of Connecticut's mixed hardwood forests, muck soil sites showed an increased abundance of black ash over time. Trees were aged between 25 and 40 years old when monitoring began. In 1927, there were 6 black ash trees/acre, and in 1957 there were 12 trees/acre [89]. Forty years of monitoring in the Indian Bowl area of Berrien County, Michigan, revealed similar increases in black ash. The percentage of total stems belonging to black ash more than doubled over the course of the study. The tamarack swamps that black ash occupied in Indian Bowl had organic soils high in calcium, occupied elevations between 600 and 750 feet (183-229 m), and were relatively free of human-caused disturbances. The increases in black ash at 10-year intervals are provided below. Increases in black ash occurred with general increases in the total number of stems per acre, suggesting black ash increases rather than other species decreases explains black ash's increased percentage of total stems [68,117].

Year 1927 1937 1957 1967
% total stems 2 2.2 2.9 5.7
% total basal area 0.1 0.6 4.9 8
Total stems/acre 312 288 438 438

In northern Lower Michigan, researchers monitored changes during 40 years of secondary succession on 2 lowland sites. Severe disturbances (logging and burning) occurred in the area from 1870 to the early 1920s. At the time of plot establishment, the oldest trees were 10 to 15 years old. One site was a mixed conifer swamp on poorly drained organic soils dominated by northern white-cedar, black spruce, and balsam fir. The other site occurred on a flat, moist sandy plain dominated by quaking aspen. Here the water table varied from a few inches above the soil surface to 30 inches (76 cm) below. The basal area of black ash in mixed conifer-dominated sites in 1981 was lower than in 1938. In the quaking aspen-dominated forests, the basal area of black ash increased substantially from 1938 to 1981. The comparisons between different sites and communities makes assigning the changes in black ash basal area to any single site or community characteristic difficult. The results of this study are summarized below [106]:

Year 1938 1945 1951 1955 1981
Site mixed conifer-dominated
Black ash basal area (cm²) 80 149 154 148 57
Site quaking aspen-dominated
Black ash basal area (cm²) 6 26 94 118 688

In an old-growth, central hardwood forest of east-central Indiana, changes in vegetation composition were compared over a span of 60 undisturbed years. Bur oak trees in the forest were 201 to 306 years old. Black ash density (number of stems/plot) decreased from 1926 to 1986, a change that researchers attributed to increased shading in the forests [4].

Spring flowers and fall fruits are typical for black ash.

State, region Flowering dates Fruiting dates
Illinois May-June [85]  
New York (Adirondack uplands) Flowers just before leaf out ~May 25 [70]  
Virginia and West Virginia April-May (in Virginia and west Virginia) [,141]  
Wisconsin May [30] September [30]
Great Plains May [51,118]  
North-central Plains   August [118]
Ontario (north-central) May-June [112] August-September, fruit dispersed October-early spring [112]

Flowering occurs before black ash trees produce leaves [110]. In northeastern Minnesota, Ahlgren [1] monitored the seasonal development of black ash for 5 years. Observations revealed that flowering began after at least 5 days with minimum temperatures above freezing and spring maximum temperatures exceeding 70 °F (21 °C). First flowers appeared as early as April 27 or as late as May 25. First leaves emerged as early as May 20 or as late as June 8. Leaves changed colors as early as August 29 or as late as September 13. Leaves fell as early as September 19 and as late as October 3 [1].


SPECIES: Fraxinus nigra
Fire adaptations: In reviews, black ash is described as a "vigorous sprouter" following fire, browsing, or cutting. Sprouts are produced from adventitious buds on the sides of stumps or the root crowns [39,112]. Black ash may also survive some fires, as fire scars were noted on trees in the Lake Duparquet area of Quebec [124,127].

Fire regimes: There are widely different fire frequencies reported for black ash habitats, and often times black ash occupies small niches that may or may not burn when most of the forested area experiences fire. Tubbs [130] considers fires rare in the northern hardwood forests of the north-central United States. Wade and others [135] report that the black ash forest cover type burned in mixed and stand replacing fires at 35- to 200-year frequencies. However, on poorly-drained sites within northwestern Ohio's Black Swamp, where black ash occurs, the estimated fire return interval is greater than 600 years [17].

Bergeron [13] reconstructed the presettlement fire regime for boreal forests along the lakeshores and on islands of Lake Duparquet in northwestern Quebec from early historical records and fire scar data. In these boreal forests, the fire cycle has increased since the late 1800s. Ash forests occurred only on lakeshores and made up 6.7% of the area surveyed. The last fire in ash forests occurred an estimated 183 years prior to the study [13].

Black ash is typical of boreal forests surrounding the Great Lakes. These forests experience "short fire return interval crown fires and/or severe surface fire regimes." Fires occur at 50- to 100-year intervals and are typically large (1,000-10,000 acres). Extreme drought conditions are necessary to fuel fires and occur at 20- to 30-year intervals. Heinselman [57] suggests that the fire return interval increases in more eastern forests that receive higher levels of precipitation.

From charcoal records collected in the Lake of the Clouds in the Boundary Waters Canoe Area, where black ash occurs, Swain [123] conservatively estimates the mean fire return interval for the past 1,000 years at 70 to 80 years and indicates that changes in the vegetation following fire were short lived (20-30 years).

From historic records including bearing trees, line descriptions, plat maps, and township summaries from Michigan's Lower Peninsula, the fire cycle in swamp forests where black ash is typical was an estimated 3000 years [136].

The following table provides fire return intervals for plant communities and ecosystems where black ash is important. Find further fire regime information for the plant communities in which this species may occur by entering the species name in the FEIS home page under "Find Fire Regimes".

Community or Ecosystem Dominant Species Fire Return Interval Range (years)
maple-beech-birch Acer-Fagus-Betula spp. >1,000
silver maple-American elm Acer saccharinum-Ulmus americana <5 to 200
sugar maple A. saccharum >1,000
sugar maple-basswood A.saccharum-Tilia americana >1,000
sugarberry-America elm-green ash Celtis laevigata-Ulmus americana-Fraxinus pennsylvanica <35 to 200
beech-sugar maple Fagus spp.-Acer saccharum >1,000
black ash Fraxinus nigra <35 to 200 [135]
tamarack Larix laricina 35-200 [94]
yellow-poplar Liriodendron tulipifera <35 [135]
Great Lakes spruce-fir Picea-Abies spp. 35 to >200
northeastern spruce-fir Picea-Abies spp. 35-200
black spruce P. mariana 35-200
conifer bog* P. mariana-Larix laricina 35-200 [37]
eastern white pine Pinus strobus 35-200
eastern white pine-eastern hemlock P. strobus-Tsuga canadensis 35-200
eastern white pine-northern red oak-red maple P. strobus-Quercus rubra-Acer rubrum 35-200
sycamore-sweetgum-American elm Platanus occidentalis-Liquidambar styraciflua-Ulmus americana <35 to 200 [135]
eastern cottonwood Populus deltoides <35 to 200 [94]
aspen-birch P. tremuloides-Betula papyrifera 35-200 [37,135]
black cherry-sugar maple Prunus serotina-Acer saccharum >1,000
oak-hickory Quercus-Carya spp. <35
northeastern oak-pine Quercus-Pinus spp. 10 to <35 [135]
oak-gum-cypress Quercus-Nyssa-spp.-Taxodium distichum 35 to >200 [86]
northern pin oak Quercus ellipsoidalis <35
bur oak Q. macrocarpa <10 [135]
oak savanna Q. macrocarpa/Andropogon gerardii-Schizachyrium scoparium 2-14 [94,135]
eastern hemlock-yellow birch Tsuga canadensis-Betula alleghaniensis >200 [135]
elm-ash-cottonwood Ulmus-Fraxinus-Populus spp. <35 to 200 [37,135]
*fire return interval varies widely; trends in variation are noted in the species review

Tree with adventitious bud/root crown/soboliferous species root sucker
Crown residual colonizer (on-site, initial community)
Secondary colonizer (on-site or off-site seed sources)


SPECIES: Fraxinus nigra
The literature suggests that black ash is fire sensitive [53] and is top-killed by even moderate-severity surface fires [57]. However, fire-scarred black ash trees were reported outside of the Lake Duparquet floodplain in northwestern Quebec and likely survived a 1944 fire [124,127].

No additional information is available on this topic.

Black ash produces sprouts following fire [57]. Sprouting in black ash is considered "vigorous." Adventitious buds located at the sides of stumps or root crowns produce the sprouts [39,112].

Very few studies assess the recovery of black ash on burned sites. This may be because the wet niches occupied by black ash do not burn often. Following a mid-May fire near Tower, Minnesota, in 1992, burned sites were compared to nearby harvested sites. Logged sites were within 9.3 miles (15 km) of the burned sites and matched burned sites "to the extent possible." The fire burned in quaking aspen-dominated woodlands, but fire severity was not reported. Black ash made up 13% of the total number of live trees on burned sites sampled in the summer of 1994. However, black ash was not among the 9 living species on logged sites. Without predisturbance data, it is not possible to say that black ash fared better on burned than logged sites [109].

In northern Cook County, Minnesota, an August wildfire burned in a 73-year-old jack pine (Pinus banksiana)-black spruce forest. Severity of the fire was not reported, but researchers noted that black ash was present in the forests before and after the fire. Researchers took no measurements or made no estimates of black ash's pre- or postfire distribution [6].

In riparian areas northeast of Thunder Bay, Ontario, the presence of black ash was a significant (p=0.05) indicator of sites adjacent to areas burned in 1999. The fire did little damage to riparian vegetation but "consumed" all but a few remnant trees in the upland boreal mixed woods and conifer-dominated forests. Black ash occurred on just 7% of sampled sites, so statistical significance may be related to the fire's clearing effect but may be what the authors describe as "a statistical artifact" [74].

The fire effects information on black ash is limited. The use of fire or protection from fire for the management of black ash requires more information than is available at this time. Any information on pre- and postfire vegetation characteristics for black ash would be valuable to land managers.


SPECIES: Fraxinus nigra
While not recognized as an important food source for wildlife, black ash is utilized in small quantities by a variety of animals. In a review, black ash is recognized as an important seed source for game birds, songbirds, and small animals, and is utilized as browse by white-tailed deer and moose [143].

Native ungulates: Both moose and white-tailed deer utilize black ash. Utilization by moose increased with their population increases. During the dormant season (mid-September through mid-May), black ash is low preference browse for moose in the Lake Superior region [5]. On Isle Royale in Michigan, black ash made up 0.4% of available browse and made up 0.1% of moose winter diets [3]. After compiling findings from 13 browse surveys done in northern Ontario, Cumming [29] found that black ash comprised less than 1% of moose diets.

On Isle Royale in the sugar maple-yellow birch vegetation type, black ash comprised 2.4% of moose summer diets in 1946. The average degree of black ash browsing on the main island was 13% in 1945, 15% in 1948, 0 in 1950, 22% in 1961, 5% in 1965, and 9% in 1970. Decreased browsing from 1948 to 1950 corresponded to substantial moose die-off; moose populations were increasing from 1950 to 1961 [67].

Utilization of black ash by white-tailed deer likely depends on its availability. In reviews, Sims and others [112] consider black ash important white-tailed deer browse, and Erdmann and others [39] indicate that black ash seedlings and sprouts are readily browsed by white-tailed deer in the Great Lake states. However, in Cook County, Minnesota, and the Upper Peninsula of Michigan, black ash is not widely distributed in white-tailed deer wintering areas and is not important browse [2].

Studies indicate that black ash tolerates heavy browsing. Following heavy clipping (complete utilization of the season's growth) of stems in Cook County, Minnesota, black ash increased output by 19% by the time researchers clipped plants the next year. Output increased by over 300% in successive clippings. Both the number of twigs and the average length of twigs increased with clipping [2]. Erdmann and others [39] in a review suggest that black ash trees can withstand even heavy winter browsing.

Other large mammals: Black ash habitats are used seasonally by both American black bears and bobcats. The presence of black ash may indicate valuable feeding sites for American black bears in the Great Lakes region. The lowland grasses and herbaceous vegetation associated with black ash swamps are a primary early spring (April-May) food [99,100]. Lovallo and Anderson [79] found that female bobcats selected lowland deciduous forests as habitat in northwestern Wisconsin in the summer and the winter. Black ash and alder (Alnus spp.) dominated the lowland forests.

Small mammals: American beavers, rabbits, and other small mammals occasionally feed on black ash bark and stems. In Michigan's Upper Peninsula, American beavers infrequently utilized black ash as a winter food source; however, in North Dakota the small twigs and bark of black ash are preferred by American beaver [76]. On Mantioulin Island, Ontario, snowshoe hare use of black ash was low in the winter season. Five percent of available stems were browsed [34]. In a guide to growing black ash in the Maritime Provinces, authors suggest the use of poison-grain mouse-bait stations in plantations to discourage mice from girdling stems [77].

Birds: Although few studies highlight specific links between birds and black ash, it is likely that the wetland habitats occupied by black ash are attractive to many bird species. It is also likely that birds feed on black ash seeds. Black ash was one of many species investigated in a caloric content study of seeds eaten by birds [66]. In Aitkin County, north-central Minnesota, 2 of 14 located great gray owl nests were found in black ash trees [115]. Black ash habitats are important ruffed grouse roosting and brooding areas. Ruffed grouse used black ash-dominated swamp hardwoods as winter habitat. Swamp hardwoods made up 19% of the winter habitat use (number of plots with roosts/total number of plots of this cover type), and an average of 1.3 roosts/plot were found in black ash-dominated swamps. In the hot summer months, swamps are important brood habitat [36].

Amphibians: Researchers found several frog species in balsam fir-black ash forests of Itasca State Park, Minnesota. Researchers found a total of 855 frogs throughout the 5 years of field studies conducted in mid-August. Of the 855 frogs, 270 occurred in the balsam fir-black ash habitat type. Microclimates, vegetation type and coverage, as well as potential escape areas likely affected habitat choice. The frog species found in the balsam fir-black ash habitat type are shown below [81]:


Number found in balsam fir-black ash habitat type

Total number found

% of total found in balsam fir-black ash habitat type

wood frog 185 372 49.7
spring peeper 29 61 47.5
swamp tree frog 44 75 58.7
tree frog 6 11 54.5
American toad 1 1 100

Palatability/nutritional value: Nutritional contents are reported for black ash seed, wood, and litter. Black ash seed collected near Champaign, Illinois, from November through March of 1954 to 1959 contained an average of 5,625 gram-calories/gram [66]. Researchers in Wisconsin found that the in-vitro dry matter digestibility of black ash wood was 17% and bark was 45%. Free sugars and sugars after hydrolysis made up 6.5% and 10%, respectively, of the carbohydrates in black ash extract [84]. Fresh black ash litter collected over a 2-year period from a marginal fen in Minnesota's Cedar Creek Natural History Area contained 4,376 g cal/g dry weight and 4,714 g cal/g ash-free weight. The dominant trees in the study area were 35 to 45 years old. The nutrient content of the fresh black ash litter is summarized below [96]:

Ash (%)* Calcium (%) Magnesium (%) Nitrogen (%) Phosphorus (%)
7.16 2.69 0.56 2.14 0.14
*oven-dry weight

In a review, Blinn and Buckner [15] report the following foliar nutrient levels for black ash:

Nitrogen* (%) Phosphorus (%) Potassium (%) Calcium (%) Magnesium (%)
2.11 0.17 2.7 2.01 0.47
*oven-dry weight

Aluminum (ppm) Boron (ppm) Copper (ppm) Iron (ppm) Manganese (ppm) Molybdenum (ppm) Zinc (ppm)
216 29 20 288 96 2.7 25

Cover value: Black ash-red maple hardwood swamps are important winter range for white-tailed deer in northern Wisconsin and typically support high deer numbers [25]. A study of bobcat food availability suggests that lowland deciduous habitats dominated by black ash of northwestern Wisconsin are home to several rodent species. In lowland deciduous forests, 3.9 voles, 0.87 mice, 0.87 shrews, and 0.87 chipmunk were captured per 100 trap nights [79].

No information is available on this topic.

Several black ash hybrids and cultivars are used in ornamental landscapes [33]. Information on improving the growth of ornamental black ashes is available [73]. Williams and Hanks [138] discuss many aspects of growing black ash commercially; information is included on seed collection, seed storage, germination, planting, protecting, and lifting.

Black ash wood splits into slats easily, making it ideal for basketry [59]. Native people of northeastern Canada and the United States historically and currently use black ash in basket making. Black ash basketry is common in Maine, New Brunswick, Nova Scotia, and New York. The Passamaquoddy, Penobscot, Maliseet, Micmac, and Mohawk people utilize black ash in their baskets [108].

Wood Products: The wood from black ash trees is not particularly strong and is used mainly for indoor furnishings. Black ash wood is moderately heavy; 1 air-dried cubic foot weighs 34 pounds [26]. The grain is coarse, sapwood is almost white, and heartwood is dark in older trees [26,59]. Wood is used in making cabinets, veneer, paneling, short tool handles, baskets, and indoor furniture [26,59,131]. Treated black ash wood is also used for posts. A study found, however, that oil-treated posts outlast untreated posts. Trees cut in the spring were peeled, air dried to 15% to 25% moisture content, and treated with 5% pentachlorophenol oil solutions. Posts soaked in oil for 24 hours lasted 33 years, while untreated posts lasted just 4.5 years [64].

Several techniques necessary to effectively manage black ash stands are discussed in the literature. For black ash in the Great Lake states, several silvicultural methods such as thinning, regeneration, and cultivation are reviewed [39,77]. There are many regression equations using d.b.h. to estimate the above ground biomass of ashes in Michigan [90,93], Quebec [91], and the Upper Great Lakes region [129].

Black ash trees are susceptible to injury by several agents. See the following references for more information on fungal agents [98,119], insect pests [112,139], and diseases [43]. Solomon and others [114] provide a review of many diseases, insects, and other agents that damage ash trees.

Fraxinus nigra: References

1. Ahlgren, C. E. 1957. Phenological observations of nineteen native tree species in northeastern Minnesota. Ecology. 38(4): 622-628. [74]

2. Aldous, Shaler E. 1952. Deer browse clipping study in the Lake States Region. Journal of Wildlife Management. 16(4): 401-409. [6826]

3. Aldous, Shaler E.; Krefting, Laurits W. 1946. The present status of moose on Isle Royale. Transactions, 11th North American Wildlife Conference. 11: 296-308. [17042]

4. Aldrich, Preston R.; Parker, George R.; Ward, Jeffrey S.; Michler, Charles H. 2003. Spatial dispersion of trees in an old-growth temperate hardwood forest over 60 years of succession. Forest Ecology and Management. 180: 475-491. [44765]

5. Allen, Arthur W.; Jordan, Peter A.; Terrell, James W. 1987. Habitat suitability index models: moose--Lake Superior region. Biol. Rep. 82 (10.155). Washington, DC: U.S. Department of the Interior, Fish and Wildlife Service. 47 p. [11710]

6. Apfelbaum, Steven; Haney, Alan. 1981. Bird populations before and after wildfire in a Great Lakes pine forest. The Condor. 83: 347-354. [8556]

7. Apsley, David K.; Leopold, Donald J.; Parker, George R. 1985. Tree species response to release from domestic livestock grazing. Proceedings, Indiana Academy of Science. 94: 215-226. [23164]

8. Arevalo, Jose Ramon; DeCoster, James K.; McAlister, Suzanne D.; Palmer, Michael W. 2000. Changes in two Minnesota forests during 14 years following catastrophic windthrow. Journal of Vegetation Science. 11(6): 833-840. [49619]

9. Barnes, Burton V. 1976. Succession in deciduous swamp communities of southeastern Michigan formerly dominated by American elm. Canadian Journal of Botany. 54: 19-24. [4914]

10. Barrett, John W.; Ketchledge, Edwin H.; Satterlund, Donald R., eds. 1961. Forestry in the Adirondacks. Syracuse, NY: Syracuse University, State University College of Forestry. 139 p. [21405]

11. Bell, D. T. 1997. Eighteen years of change in an Illinois streamside deciduous forest. Journal of the Torrey Botanical Society. 124(2): 174-188. [41778]

12. Benzie, John W.; Blum, Barton M. 1989. Silviculture of northeastern conifers. In: Burns, Russell M., compiler. The scientific basis for silvicultural and management decisions in the National Forest System. Gen. Tech. Rep. WO-55. Washington, DC: U.S. Department of Agriculture, Forest Service: 18-30. [10243]

13. Bergeron, Yves. 1991. The influence of island and mainland lakeshore landscapes on boreal forest fire regimes. Ecology. 72(6): 1980-1992. [17186]

14. Bernard, Stephen R.; Brown, Kenneth F. 1977. Distribution of mammals, reptiles, and amphibians by BLM physiographic regions and A.W. Kuchler's associations for the eleven western states. Tech. Note 301. Denver, CO: U.S. Department of the Interior, Bureau of Land Management. 169 p. [434]

15. Blinn, Charles R.; Buckner, Edward R. 1989. Normal foliar nutrient levels in North American forest trees: A summary. Station Bulletin 590-1989. St. Paul, MN: University of Minnesota, Minnesota Agricultural Experiment Station. 27 p. [15282]

16. Boerner, Ralph E. J.; Brinkman, Jennifer A. 1996. Ten years of tree seedling establishment and mortality in an Ohio deciduous forest complex. Bulletin of the Torrey Botanical Club. 123(4): 309-317. [48378]

17. Boerner, Ralph E. J.; Cho, Do-Soon. 1987. Structure and composition of Goll Woods, an old-growth forest remnant in northwestern Ohio. Bulletin of the Torrey Botanical Club. 114(2): 173-179. [8711]

18. Bormann, F. H.; Buell, M. F. 1964. Old-age stand of hemlock-northern hardwood forest in central Vermont. Bulletin of the Torrey Botanical Club. 91(6): 451-465. [8856]

19. Brand, Gary J. 1985. Environmental indices for common Michigan trees and shrubs. Res. Pap. NC-261. St. Paul, MN: U.S. Department of Agriculture, Forest Service, North Central Forest Experiment Station. 5 p. [14465]

20. Braun, E. Lucy. 1961. The woody plants of Ohio. Columbus, OH: Ohio State University Press. 362 p. [12914]

21. Bray, J. Roger. 1960. The composition of savanna vegetation in Wisconsin. Ecology. 41(4): 721-732. [24440]

22. Brisson, Jacques; Bergeron, Yves; Bouchard, Andre. 1992. The history and tree stratum of an old-growth forest of Haut-Saint-Laurent region, Quebec. Natural Areas Journal. 12(1): 3-9. [49624]

23. Brundrett, Mark; Murase, Gracia; Kendrick, Bryce. 1990. Comparative anatomy of roots and mycorrhizae of common Ontario trees. Canadian Journal of Botany. 68: 551-578. [11380]

24. Buell, Murray F.; Bormann, F. H. 1955. Deciduous forests of Ponemah Point, Red Lake Indian Reservation, Minnesota. Ecology. 36(4): 646-658. [49625]

25. Christensen, E. M.; Clausen, J. J. (Jones); Curtis, J. T. 1959. Phytosociology of the lowland forests of northern Wisconsin. The American Midland Naturalist. 62(1): 232-247. [49627]

26. Collingwood, G. H.; Brush, Warren D.; [revised and edited by Butcher, Devereux]. 1964. Knowing your trees. 2nd ed. Washington, DC: The American Forestry Association. 349 p. [22497]

27. Collins, Scott L.; Vankat, John L.; Perino, Janice V. 1979. Potential tree species dynamics in the arbor vitae association of Cedar Bog, a west-central Ohio fen. Bulletin of the Torrey Botanical Club. 106(4): 290-298. [49628]

28. Conway, Verona M. 1949. The bogs of central Minnesota. Ecological Monographs. 19(2): 173-206. [16686]

29. Cumming, H. G. 1987. Sixteen years of moose browse surveys in Ontario. Alces. 23: 125-156. [8859]

30. Curtis, John T. 1959. The vegetation of Wisconsin. Madison, WI: The University of Wisconsin Press. 657 p. [7116]

31. Damman, A. W. H.; Johnston, William F. 1980. Black spruce. In: Eyre, F. H., ed. Forest cover types of the United States and Canada. Washington, DC: Society of American Foresters: 11-14. [49853]

32. Dansereau, Pierre. 1959. Phytogeographia Laurentiana. II. The principal plant associations of the Saint Lawrence Valley. Contributions of the Botanical Institute No. 75. Montreal, PQ: University of Montreal, Botanical Institute. 147 p. [8925]

33. Davidson, Campbell G. 1999. 'Northern Treasure' and 'Northern Gem' hybrid ash. Hortscience. 34(1): 151-152. [49630]

34. de Vos, Antoon. 1964. Food utilization of snowshoe hares on Mantioulin Island, Ontario. Journal of Forestry. 62: 238-244. [25071]

35. Denneler, Bernhard; Bergeron, Yves; Begin, Yves. 1999. An attempt to explain the distribution of the tree species composing the riparian forests of Lake Duparquet, southern boreal region of Quebec, Canada. Canadian Journal of Botany. 77: 1744-1755. [40150]

36. Dorney, Robert S. 1959. Relationship of ruffed grouse to forest cover types in Wisconsin. Tech. Bull. 18. Madison, WI: Wisconsin Conservation Department. 31 p. [15906]

37. Duchesne, Luc C.; Hawkes, Brad C. 2000. Fire in northern 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: 35-51. [36982]

38. Dunn, Christopher P.; Stearns, Forest. 1987. A comparison of vegetation and soils in floodplain and basin forested wetlands of southeastern Wisconsin. The American Midland Naturalist. 118(2): 375-384. [49444]

39. Erdmann, Gayne G.; Crow, Thomas R.; Peterson, Ralph M., Jr.; Wilson, Curtis D. 1987. Managing black ash in the Lake States. Gen. Tech. Rep. NC-115. St. Paul, MN: U.S. Department of Agriculture, Forest Service, North Central Forest Experiment Station. 10 p. [22296]

40. Eyre, F. H., ed. 1980. Forest cover types of the United States and Canada. Washington, DC: Society of American Foresters. 148 p. [905]

41. Flora of North America Association. 2004. Flora of North America: The flora. [Online]. Flora of North America Association (Producer). Available: [36990]

42. Frank, Robert M.; Majcen, Zoran; Gagnon, Gilles. 1980. Balsam fir. In: Eyre, F. H., ed. Forest cover types of the United States and Canada. Washington, DC: Society of American Foresters: 10-11. [49851]

43. French, D. W.; Sundaram, S.; Lockhart, B. E. 1989. First report of ash yellows in Minnesota. Plant Disease. 73(11): 938. Abstract. [49632]

44. Garrison, George A.; Bjugstad, Ardell J.; Duncan, Don A.; Lewis, Mont E.; Smith, Dixie R. 1977. Vegetation and environmental features of forest and range ecosystems. Agric. Handb. 475. Washington, DC: U.S. Department of Agriculture, Forest Service. 68 p. [998]

45. Gates, Frank C. 1942. The bogs of northern lower Michigan. Ecological Monographs. 12(3): 213-254. [10728]

46. Gates, Frank C.; Erlanson, C. O. 1925. Enlarged bases in Fraxinus nigra in Michigan. Botanical Gazette. 80(1): 107-110. [49667]

47. Godman, R. M. 1980. Hemlock - yellow birch. In: Eyre, F. H., ed. Forest cover types of the United States and Canada. Washington, DC: Society of American Foresters: 29. [49894]

48. Godman, R. M.; Gagnon, Gilles; Majcen, Zoran. 1980. Sugar maple. In: Eyre, F. H., ed. Forest cover types of the United States and Canada. Washington, DC: Society of American Foresters: 29-30. [49895]

49. Godman, Richard M.; Mattson, Gilbert A. 1976. Seed crops and regeneration problems of 19 species in northeastern Wisconsin. Res. Pap. NC-123. St. Paul, MN: U.S. Department of Agriculture, Forest Service, North Central Forest Experiment Station. 5 p. [3715]

50. Graham, Samuel A. 1941. Climax forests of the Upper Peninsula of Michigan. Ecology. 22(4): 355-362. [11385]

51. Great Plains Flora Association. 1986. Flora of the Great Plains. Lawrence, KS: University Press of Kansas. 1392 p. [1603]

52. Griffin, Ralph H. 1980. Red spruce--balsam fir. In: Eyre, F. H., ed. Forest cover types of the United States and Canada. Washington, DC: Society of American Foresters: 19-20. [49862]

53. Grimm, Eric C. 1984. Fire and other factors controlling the Big Woods vegetation of Minnesota in the mid-nineteenth century. Ecological Monographs. 54(3): 291-311. [22170]

54. Hansen, H. L.; Krefting, L. W.; Kurmis, V. 1973. The forest of Isle Royale in relation to fire history and wildlife. Tech. Bull. 294; Forestry Series 13. Minneapolis, MN: University of Minnesota, Agricultural Experiment Station. 44 p. [8120]

55. Heinselman, M. L. 1970. Landscape evolution, peatland types and the environment in the Lake Agassiz Peatlands Natural Area, Minnesota. Ecological Monographs. 40(2): 235-261. [8378]

56. Heinselman, Miron L. 1963. Forest sites, bog processes, and peatland types in the Glacial Lake Agassiz region, Minnesota. Ecological Monographs. 33: 327-374. [15111]

57. Heinselman, Miron L. 1981. Fire and succession in the conifer forests of northern North America. In: West, Darrell C.; Shugart, Herman H.; Botkin, Daniel B., eds. Forest succession: concepts and applications. New York: Springer-Verlag: 374-405. [29237]

58. Heinselman, Miron L. 1981. Fire intensity and frequency as factors in the distribution and structure of northern ecosystems. In: Mooney, H. A.; Bonnicksen, T. M.; Christensen, N. L.; Lotan, J. E.; Reiners, W. A., technical coordinators. 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: 7-57. [4390]

59. Hosie, R. C. 1969. Native trees of Canada. 7th ed. Ottawa, ON: Canadian Forestry Service, Department of Fisheries and Forestry. 380 p. [3375]

60. Huenneke, Laura Foster. 1982. Wetland forests of Tompkins County, New York. Bulletin of the Torrey Botanical Club. 109(1): 51-63. [22960]

61. Johnston, C. A.; Naiman, R. J. 1990. Browse selection by beaver: effects on riparian forest composition. Canadian Journal of Forestry Research. 20: 1036-1043. [12009]

62. Kaminski, D. A.; Jackson, M. T. 1978. A light and moisture continuum analysis of the presettlement prairie-forest border region of eastern Illinois. The American Midland Naturalist. 99(2): 280-289. [49635]

63. Kartesz, John T.; Meacham, Christopher A. 1999. Synthesis of the North American flora (Windows Version 1.0), [CD-ROM]. Available: North Carolina Botanical Garden. In cooperation with the Nature Conservancy, Natural Resources Conservation Service, and U.S. Fish and Wildlife Service [2001, January 16]. [36715]

64. Kaufert, F. H.; Neetzel, J. R.; Hanson, W. 1978. Thirty-five years of test results on fence posts treated with pentachlorophenol. Minnesota Forestry Research Notes No. 270. St. Paul, MN: University of Minnesota, College of Forestry. 4 p. [49668]

65. Kell, Lucille Lora. 1938. The effect of the moisture-retaining capacity of soils on forest succession in Itasca Park, Minnesota. The American Midland Naturalist. 20(3): 682-694. [49636]

66. Kendeigh, S. Charles; West, George C. 1965. Caloric values of plant seeds eaten by birds. Ecology. 46(4): 553-555. [48440]

67. Krefting, Laurtis W. 1974. The ecology of the Isle Royale moose with special reference to the habitat. Tech. Bull. 297, Forestry Series 15. Minneapolis, MN: University of Minnesota, Agricultural Experiment Station. 75 p. [8678]

68. Kron, Kathleen A. 1989. The vegetation of Indian Bowl wet prairie and its adjacent plant communities. I. Description of the vegetation. Michigan Botanist. 28(4): 179-200. [17358]

69. Kuchler, A. W. 1964. United States [Potential natural vegetation of the conterminous United States]. Special Publication No. 36. New York: American Geographical Society. 1:3,168,000; colored. [3455]

70. Kudish, Michael. 1992. Adirondack upland flora: an ecological perspective. Saranac, NY: The Chauncy Press. 320 p. [19377]

71. Kurmis, Vilis; Kim, Ji Hong. 1989. Black ash stand composition and structure in Carlton County, Minnesota. Staff Paper Series Number 69. St. Paul, MN: University of Minnesota, College of Forestry. 25 p. [49674]

72. Kurmis, Vilis; Webb, Sara L.; Merriam, Lawrence C., Jr. 1986. Plant communities of Voyageurs National Park, Minnesota, U.S.A. Canadian Journal of Botany. 64: 531-540. [16088]

73. Lait, Cameron G.; Saelim, Suomal; Zwiazek, Janusz J.; Zheng, Yao. 2001. Effect of basement sump pump effluent on the growth and physiology of urban black ash and green ash ornamental trees. Journal of Arboriculture. 27(2): 69-77. [49637]

74. Lamb, Eric G.; Mallik, Azim U.; Mackereth, Robert W. 2003. The early impact of adjacent clearcutting and forest fire on riparian zone vegetation in northwestern Ontario. Forest Ecology and Management. 177: 529-538. [43861]

75. Larimore, Richard L.; Phillippe, Loy R.; Simon, Scott D.; [and others]. 2000. Vascular flora of Horseshoe Bottom Nature Preserve, Vermilion County, Illinois. Transactions of the Illinois State Academy of Sciences. 93(1): 3-24. [39658]

76. Lawrence, William H. 1954. Michigan beaver populations as influenced by fire and logging. Ann Arbor, MI: University of Michigan. 219 p. Dissertation. [16480]

77. Lees, J. C.; West, R. C. 1988. A strategy for growing black ash in the maritime provinces. Technical Note No. 201. Fredericton, NB: Canadian Forestry Service - Maritimes. 4 p. [49671]

78. Loo, J.; Ives, N. 2003. The Acadian forest: historical condition and human impacts. The Forestry Chronicle. 79(3): 462-474. [45560]

79. Lovallo, Matthew J.; Anderson, Eric M. 1996. Bobcat (Lynx rufus) home range size and habitat use in northwest Wisconsin. The American Midland Naturalist. 135: 241-252. [27064]

80. Malloch, D.; Malloch, B. 1982. The mycorrhizal status of boreal plants: additional species from northeastern Ontario. Canadian Journal of Botany. 60: 1035-1040. [17718]

81. Marshall, William H.; Buell, Murray F. 1955. A study of the occurrence of amphibians in relation to a bog succession, Itasca State Park, Minnesota. Ecology. 36(3): 381-387. [16690]

82. McAvoy, William A. 2003. Rare vascular plants of Delaware, [Online]. In: Delaware Natural Heritage Program. Smyrna, DE: Delaware Department of Natural Resources and Environmental Control, Division of Fish and Wildlife (Producer). Available: [2005, July 5]. [53814]

83. McEuen, Amy B.; Curran, Lisa M. 2004. Seed dispersal and recruitment limitation across spatial scales in temperate forest fragments. Ecology. 85(2): 507-518. [47472]

84. Millett, M. A.; Baker, A. J.; Feist, W. C.; Mellenberger, R. W.; Satter, L. D. 1970. Modifying wood to increase its in vitro digestibility. Journal of Animal Science. 31(4): 781-788. [49634]

85. Mohlenbrock, Robert H. 1986. [Revised edition]. Guide to the vascular flora of Illinois. Carbondale, IL: Southern Illinois University Press. 507 p. [17383]

86. Myers, Ronald L. 2000. Fire in tropical and subtropical 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: 161-173. [36985]

87. North Dakota Parks and Recreation Department, North Dakota Natural Heritage Program. 2000. North Dakota Natural Heritage Inventory: Nature Preserves Program: Rare plants list 2000. Bismark, ND: Natural Heritage Program. 8 p. [35591]

88. Ohmann, Lewis F.; Ream, Robert R. 1971. Wilderness ecology: virgin plant communities of the Boundary Waters Canoe Area. Res. Pap. NC-63. St. Paul, MN: U.S. Department of Agriculture, Forest Service, North Central Forest Experiment Station. 55 p. [9271]

89. Olson, A. R. 1965. Natural changes in some Connecticut woodlands during 30 years. Bulletin 669. New Haven, CT: The Connecticut Agricultural Experiment Station. 52 p. [39019]

90. Ostrom, Arnold J. 1983. Tree and shrub biomass estimates for Michigan, 1980. Res. Note NC-302. St. Paul, MN: U.S. Department of Agriculture, Forest Service, North Central Forest Experiment Station. 7 p. [8162]

91. Ouellet, D. 1985. Biomass equations for six commercial tree species in Quebec. Forestry Chronicle. 61(3): 218-222. [12614]

92. Parker, George R.; Schneider, G. 1974. Structure and edaphic factors of an alder swamp in northern Michigan. Canadian Journal of Forestry. 4: 499-508. [15113]

93. Parker, George R.; Schneider, G. 1975. Biomass and productivity of an alder swamp in northern Michigan. Canadian Journal of Forestry. 5: 403-409. [15112]

94. Paysen, Timothy E.; Ansley, R. James; Brown, James K.; [and others]. 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-volume 2. Ogden, UT: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 121-159. [36978]

95. Raunkiaer, C. 1934. The life forms of plants and statistical plant geography. Oxford: Clarendon Press. 632 p. [2843]

96. Reiners, W. A.; Reiners, N. M. 1970. Energy and nutrient dynamics of forest floors in three Minnesota forests. The Journal of Ecology. 58(2): 497-519. [49629]

97. Reschke, Carol. 1990. Ecological communities of New York State. Latham, NY: New York State Department of Environmental Conservation, Natural Heritage Program. 96 p. [21441]

98. Riffle, Jerry W.; Peterson, Glenn W., technical coordinators. 1986. Diseases of trees in the Great Plains. Gen. Tech. Rep. RM-129. Fort Collins, CO: U.S. Department of Agriculture, Forest Service, Rocky Mountain Forest and Range Experiment Station. 149 p. [16989]

99. Rogers, Lynn L.; Allen, Arthur W. 1987. Habitat suitability index models: Black bear--upper Great Lakes region. Biol. Rep. 82 (10.144). Washington DC: U.S. Department of the Interior, Fish and Wildlife Service. 54 p. [11711]

100. Rogers, Lynn L.; Wilker, Gregory A.; Scott, Sally S. 1990. Managing natural populations of black bears in wilderness. In: Lime, David W., ed. Managing America's enduring wilderness resource: Proceedings of the conference; 1989 September 11-17; Minneapolis, MN. St. Paul, MN: University of Minnesota, Minnesota Extension Service; Minnesota Agricultural Experiment Station: 363-366. [15409]

101. Roland, A. E.; Smith, E. C. 1969. The flora of Nova Scotia. Halifax, NS: Nova Scotia Museum. 746 p. [13158]

102. Ronald, W. G. 1972. Range extension of black ash, Fraxinus nigra Marsh., in Manitoba. The Canadian Field-Naturalist. 86(1): 73-74. [49652]

103. Rubin, Benjamin D.; Manion, Paul D. 2001. Landscape-scale forest structure in northern New York and potential successional impacts of the 1998 ice storm. The Forestry Chronicle. 77(4): 613-618. [49651]

104. Rudolf, Paul O. 1980. Black ash - American elm - red maple. In: Eyre, F. H., ed. Forest cover types of the United States and Canada. Washington, DC: Society of American Foresters: 37-38. [49904]

105. Rudolf, Paul O. 1990. Pinus resinosa Ait. red pine. In: Burns, Russell M.; Honkala, Barbara H., technical coordinators. Silvics of North America. Volume 1. Conifers. Agric. Handb. 654. Washington, DC: U.S. Department of Agriculture, Forest Service: 442-455. [13246]

106. Sakai, Ann K.; Sulak, JoAnne H. 1985. Four decades of secondary succession in two lowland permanent plots in northern Lower Michigan. The American Midland Naturalist. 113(1): 146-157. [49650]

107. Samson, Fred B. 1979. Lowland hardwood bird communities. In: DeGraaf, Richard M.; Evans, Keith E., compilers. Proceedings of the workshop: Management of northcentral and northeastern forests for nongame birds; 1979 January 23-25; Minneapolis, MN. Gen. Tech. Rep. NC-51. St. Paul, MN: U.S. Department of Agriculture, Forest Service, North Central Forest Experiment Station: 49-66. [18077]

108. Schmidt, Judith G. 1990. Ethnobotany of contemporary Northeastern "Woodland" Indians: its sharing with the public through photography. Advances in Economic Botany. 8: 224-240. [49683]

109. Schulte, Lisa A.; Niemi, Gerald J. 1998. Bird communities of early-successional burned and logged forest. Journal of Wildlife Management. 62(4): 1418-1429. [36413]

110. Seymour, Frank Conkling. 1982. The flora of New England. 2d ed. Phytologia Memoirs 5. Plainfield, NJ: Harold N. Moldenke and Alma L. Moldenke. 611 p. [7604]

111. Shiflet, Thomas N., ed. 1994. Rangeland cover types of the United States. Denver, CO: Society for Range Management. 152 p. [23362]

112. Sims, Richard A.; Kershaw, H. Maureen; Wickware, Gregory M. 1990. The autecology of major tree species in the north central region of Ontario. COFRDA(Canada-Ontario Forest Resources Development Agreement) Report 3302; NWOFTDU (Northwestern Ontario Forest Technology Development Unit) Technical Report 48. Ottawa: Forestry Canada, Ontario Region; Thunder Bay, ON: Ontario Ministry of Natural Resources, Northwestern Ontario Forest Technology Development Unit. 126 p. [49694]

113. Smith, W. Brad. 1986. Biomass yields for small tree, shrubs, and herbs in northern Lake States forests. Res. Pap. NC-277. St. Paul, MN: U.S. Department of Agriculture, Forest Service, North Central Forest Experiment Station. 11 p. [8159]

114. Solomon, J. D.; Leininger, T. D.; Wilson, A. D.; [and others]. 1993. Ash pests: A guide to major insects, diseases, air pollution, injury, and chemical injury. Gen. Tech. Rep. SO-96. New Orleans, LA: U.S. Department of Agriculture, Forest Service, Southern Forest Experiment Station. 45 p. [26704]

115. Spreyer, Mark F. 1987. A floristic analysis of great gray owl habitat in Aitkin County, Minnesota. In: Nero, Robert W.; Clark, Richard J.; Knapton, Richard J.; Hamre, R. H., eds. Biology and conservation of northern forest owls: Symposium proceedings; 1987 February 3-7; Winnipeg, MB. Gen. Tech. Rep. RM-142. Fort Collins, CO: U.S. Department of Agriculture, Forest Service, Rocky Mountain Forest and Range Experiment Station: 96-100. [17930]

116. Steinbauer, George P. 1937. Dormancy and germination of Fraxinus seeds. Plant Physiology. 12: 813-824. [3792]

117. Stephens, George R.; Waggoner, Paul E. 1970. The forests anticipated from 40 years of natural transitions in mixed hardwoods. Bulletin No. 707. New Haven, CT: Connecticut Agricultural Experiment Station. 58 p. [41891]

118. Stephens, H. A. 1973. Woody plants of the North Central Plains. Lawrence, KS: The University Press of Kansas. 530 p. [3804]

119. Stewart, Donald M. 1951. Heart rot of black ash in Minnesota. Phytopathological Notes. 41(6): 569-570. [49648]

120. Stickney, Peter F. 1989. FEIS postfire regeneration workshop--April 12: Seral origin of species comprising secondary plant succession in Northern Rocky Mountain forests. 10 p. Unpublished draft on file at: U.S. Department of Agriculture, Forest Service, Intermountain Research Station, Fire Sciences Laboratory, Missoula, MT. [20090]

121. Strausbaugh, P. D.; Core, Earl L. 1977. Flora of West Virginia. 2nd ed. Morgantown, WV: Seneca Books, Inc. 1079 p. [23213]

122. Sutherland, Elaine Kennedy; Hale, Betsy J.; Hix, David M. 2000. Defining species guilds in the central hardwood forest, USA. Plant Ecology. 147: 1-19. [43742]

123. Swain, Albert M. 1973. A history of fire and vegetation in northeastern Minnesota as recorded in lake sediments. Quaternary Research. 3(3): 383-396. [38931]

124. Tardif, Jacques. 2005. [Email to Corey Gucker]. July 20. Winnipeg, MB: University of Winnipeg, Centre for Forest Interdisciplinary Research. On file with: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory, Missoula, MT; RWU 4403 files. [53810]

125. Tardif, Jacques; Bergeron, Yves. 1993. Radical growth of Fraxinus nigra in a Canadian boreal floodplain in response to climatic and hydrological fluctuations. Journal of Vegetation Science. 4(6): 751-758. [49647]

126. Tardif, Jacques; Bergeron, Yves. 1997. Comparative dendroclimatological analysis of two black ash and two white cedar populations from contrasting sites in the Lake Duparquet region, northwestern Quebec. Canadian Journal of Forest Research. 27(1): 108-116. [49646]

127. Tardif, Jacques; Bergeron, Yves. 1999. Population dynamics of Fraxinus nigra in response to flood-level variations, in northwestern Quebec. Ecological Monographs. 69(1): 107-125. [49645]

128. Tardif, Jacques; Dery, Sephane; Bergeron, Yves. 1994. Sexual regeneration of black ash (Fraxinus nigra Marsh.) in a boreal floodplain. The American Midland Naturalist. 132(1): 124-135. [23927]

129. Ter-Mikaelian, Michael T.; Korzukhin, Michael D. 1997. Biomass equations for sixty-five North American tree species. Forest Ecology and Management. 97: 1-24. [28034]

130. Tubbs, Carl H. 1977. Manager's handbook for northern hardwoods in the north central States. Gen. Tech. Rep. NC-39. St, Paul MI: U.S. Department of Agriculture, Forest Service, North Central Forest Experiment Station. 29 p. [10974]

131. U.S. Department of Agriculture, Forest Service, Forest Products Laboratory. 1974. Wood handbook: wood as an engineering material. Agric. Handb. No. 72. Washington, DC. 415 p. [16826]

132. U.S. Department of Agriculture, Natural Resources Conservation Service. 2005. PLANTS database (2004), [Online]. Available: /. [34262]

133. Vanstone, D. 1974. Seed dormancy in black ash. In: Proceedings, 30th annual meeting of the Western Canadian Society for Horticulture; [Date unknown]; [Location unknown]. [Place of publication unknown]: [Publisher unknown]: 77-84. On file with: U.S. Department of Agriculture, Forest Service, Intermountain Research Station, Fire Sciences Laboratory, Missoula, MT. [22367]

134. Vanstone, D. E.; LaCroix, L. J. 1975. Embryo immaturity and dormancy of black ash. Journal of the American Society for Horticultural Science. 100(6): 630-632. [22368]

135. Wade, Dale D.; Brock, Brent L.; Brose, Patrick H.; [and others]. 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]

136. Whitney, Gordon G. 1986. Relation of Michigan's presettlement pine forests to substrate and disturbance history. Ecology. 67(6): 1548-1559. [8713]

137. Williams, Arthur B. 1936. The composition and dynamics of a beech-maple climax community. Ecological Monographs. 6(3): 318-408. [8346]

138. Williams, Robert D.; Hanks, Sidney H. 1976. Hardwood nurseryman's guide. Agric. Handb. 473. Washington, DC: U.S. Department of Agriculture, Forest Service. 78 p. [4182]

139. Wilson, Ian M.; Haack, Robert A.; Poland, Therese M. 2002. New wood-boring insect kills ash trees. Arborist News. 11(5): 13-14. [47378]

140. Winget, C. H.; Cottam, G.; Kozlowski, T. T. 1965. Species association and stand structure of yellow birch in Wisconsin. Forest Science. 11(3): 369-383. [21189]

141. Wofford, B. Eugene. 1989. Guide to the vascular plants of the Blue Ridge. Athens, GA: The University of Georgia Press. 384 p. [12908]

142. Wright, Jonathan W. 1953. Notes on flowering and fruiting of northeastern trees. Station Paper No. 60. Upper Darby, PA: U.S. Department of Agriculture, Forest Service, Northeastern Forest Experiment Station. 38 p. [5009]

143. Wright, Jonathan W.; Rauscher, H. Michael. 1990. Fraxinus nigra Marsh. black ash. In: Burns, Russell M.; Honkala, Barbara H., technical coordinators. Silvics of North America: Vol. 2. Hardwoods. Agriculture Handbook 654. Washington, DC: U.S. Department of Agriculture, Forest Service: 344-347. [22499]

144. Yahner, R. H.; Storm, G. L.; Melton, R. E.; Vecellio, G. M.; Cottam, D. F. 1991. Floral inventory and vegetative cover type mapping of Gettysburg National Military Park and Eisenhower National Historic Site. Tech. Rep. NPS/MAR/NRTR - 91/050. Philadelphia, PA: U.S. Department of the Interior, National Park Service, Mid-Atlantic Region. 149 p. [17986]

145. Zogg, Gregory P.; Barnes, Burton, V. 1995. Ecological classification and analysis of wetland ecosystems, northern Lower Michigan, U.S.A. Canadian Journal of Forest Research. 25: 1865-1875. [26166]

146. Zoladeski, C. A.; Delorme, R. J.; Wickware, G. M.; [and others]. 1998. Forest ecosystem toposequences in Manitoba. Special Report 12. Edmonton, AB: Natural Resources Canada, Canadian Forest Service, Northern Forestry Centre. 63 p. [35768]

FEIS Home Page