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SPECIES:  Sassafras albidum


SPECIES: Sassafras albidum
AUTHORSHIP AND CITATION : Sullivan, Janet. 1993. Sassafras albidum. In: Fire Effects Information System, [Online]. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory (Producer). Available: [].
ABBREVIATION : SASALB SYNONYMS : S.variifolium (Salisb.) K. & Ze. S. sassafras (L.) Karsten S. officinale (Nees. & Eberm.) S. triloba Raf. S. triloba var. mollis Raf. SCS PLANT CODE : SAAL5 COMMON NAMES : sassafras white sassafras common sassafras ague tree cinnamon wood smelling stick saloop gumbo file mitten tree TAXONOMY : The currently accepted scientific name of sassafras is Sassafras albidum (Nutt.) Nees. [41,61]. Some authorities consider red sassafras [S. a. var. molle (Raf.) Fern.] a distinct variety [8,30,82]; other authors consider it synonymous with the type variety [53,61,68]. LIFE FORM : Tree, Shrub FEDERAL LEGAL STATUS : No special status OTHER STATUS : Sassafras is listed under "Special Concern-Possibly Extirpated" in Maine [22].


SPECIES: Sassafras albidum
GENERAL DISTRIBUTION : Sassafras occurs from southwestern Maine west to extreme southern Ontario and central Michigan; southwest to Illinois, Missouri, eastern Oklahoma, and eastern Texas; and east to central Florida.  It is extinct in southeastern Wisconsin, but its range is extending into northern Illinois [41]. ECOSYSTEMS :    FRES10  White - red - jack pine    FRES12  Longleaf - slash pine    FRES13  Loblolly - shortleaf pine    FRES14  Oak - pine    FRES15  Oak - hickory    FRES16  Oak - gum - cypress    FRES17  Elm - ash - cottonwood    FRES18  Maple - beech - birch    FRES19  Aspen - birch STATES :      AL  AR  CT  DE  FL  GA  IL  IN  IA  KS      KY  LA  ME  MD  MA  MI  MS  MO  NH  NJ      NY  NC  OH  OK  PA  RI  SC  TN  TX  VT      VA  WV BLM PHYSIOGRAPHIC REGIONS : NO-ENTRY KUCHLER PLANT ASSOCIATIONS :    K083  Cedar glades    K089  Black Belt    K100  Oak - hickory forest    K101  Elm - ash forest    K104  Appalachian oak forest    K106  Northern hardwoods    K110  Northeastern oak - pine forest    K111  Oak - hickory - pine forest    K112  Southern mixed forest SAF COVER TYPES :     14  Northern pin oak     15  Red pine     16  Aspen     20  White pine - northern red oak - red maple     21  Eastern white pine     40  Post oak - blackjack oak     43  Bear oak     44  Chestnut oak     45  Pitch pine     46  Eastern redcedar     50  Black locust     52  White oak - black oak - northern red oak     53  White oak     55  Northern red oak     57  Yellow-poplar     60  Beech - sugar maple     61  River birch - sycamore     64  Sassafras - persimmon     70  Longleaf pine     71  Longleaf pine - scrub oak     75  Shortleaf pine     76  Shortleaf pine - oak     78  Virginia pine - oak     79  Virginia pine     80  Loblolly pine - shortleaf pine     81  Loblolly pine     83  Longleaf pine - slash pine     84  Slash pine     85  Slash pine - hardwood     88  Willow oak - water oak - diamondleaf oak    108  Red maple    110  Black oak SRM (RANGELAND) COVER TYPES : NO-ENTRY HABITAT TYPES AND PLANT COMMUNITIES : The sassafras-persimmon (Diospyros virginiana) cover type is a successional type common on abandoned farmlands throughout its range. Sassafras is a common component of the bear oak (Quercus ilicifolia) type, which is a scrub type on dry sites along the Coastal Plain [41]. In dry pine-oak forests, sassafras sprouts prolifically and is a shrub-layer dominant [72].  It achieves short-term dominance by producing extensive thickets where few other woody plants can establish [32]. In the northern parts of its range, sassafras occurs in the understory of open stands of aspen (Populus spp.) and in northern pin oak (Q. ellipsoidalis) stands [41]. Common tree associates of sassafras not previously mentioned include sweetgum (Liquidambar styraciflua), flowering dogwood (Cornus florida), elms (Ulmus spp.), hickories (Carya spp.), and American beech (Fagus grandifolia).  Minor associates include American hornbeam (Carpinus caroliniana), eastern hophornbeam (Ostrya virginiana), and pawpaw (Asimina triloba).  On poor sites, particularly in the Appalachian Mountains, sassafras is frequently associated with black locust (Robinia pseudoacacia), and sourwood (Oxydendron arboreum).  In old fields with deep soils, sassafras commonly grows with elms, ashes (Fraxinus spp.), sugar maple (Acer saccharum), yellow-poplar (Liriodendron tulipifera), and oaks [41]. Sassafras is listed as a subdominant on subxeric and submesic sites in the following classification:  Landscape ecosystem classification for South Carolina [51].


SPECIES: Sassafras albidum
WOOD PRODUCTS VALUE : Sassafras wood is soft, brittle, light, and has limited commercial value [41].  It is durable, however, and is used for cooperage, buckets, fenceposts, rails, cabinets, interior finish, and furniture [24,41,83]. Carey and Gill [9] rate its value for firewood as good, their middle rating. IMPORTANCE TO LIVESTOCK AND WILDLIFE : Sassafras leaves and twigs are consumed by white-tailed deer in both summer and winter.  In some areas it is an important deer food [41]. Sassafras leaf browsers include woodchucks, marsh rabbits, and black bears [83].  Rabbits eat sassafras bark in winter [8].  Beavers will cut sassafras stems [15].  Sassafras fruits are eaten by many species of birds including northern bobwhites [58], eastern kingbirds, great crested flycatchers, phoebes, wild turkeys, catbirds, flickers, pileated woodpeckers, downy woodpeckers, thrushes, vireos, and mockingbirds. Some small mammals also consume sassafras fruits [16,65,75,83]. For most of the above mentioned animals, sassafras is not consumed in large enough quantities to be important.  Carey and Gill [9] rate its value to wildlife as fair, their lowest rating. PALATABILITY : Palatability of sassafras to white-tailed deer is rated as good throughout its range [41]. NUTRITIONAL VALUE : The nutritional value of sassafras winter twigs is fair [67].  Seasonal changes in nutrient composition of sassafras leaves and twigs has been reported.  Crude protein ranged from a high of 21.0 percent in April leaves to a low of 6.1 in January twigs [7]. Sassafras fruits are high in lipids and energy value [85]. COVER VALUE : NO-ENTRY VALUE FOR REHABILITATION OF DISTURBED SITES : Sassafras is used for restoring depleted soils in old fields [41]. Sassafras occurs on sites that have been largely denuded of other vegetation by the combination of frequent fire and toxic emissions from zinc smelters.  Sassafras persistence on these sites is attributed to root sprouting; seedling reproduction is severely curtailed by the high level of toxins in the soil [52]. OTHER USES AND VALUES : Sassafras oil is extracted from the root bark for use by the perfume industry, primarily for scenting soaps.  It is also used as a flavoring agent and an antiseptic [41,83].  Large doses of the oil may be narcotic [83].  Root bark is also used to make tea, which in weak infusions is a pleasant beverage, but induces sweating in strong infusions.  The leaves can be used to flavor and thicken soups [41,83].  The mucilaginous pith of the root is used in preparations to soothe eye irritations [83]. Because of its durability, sassafras was used for dugout canoes by Native Americans [49]. OTHER MANAGEMENT CONSIDERATIONS : Overstory removal often results in an increase in sassafras stems, particularly by sprouting [81].  Sassafras thickets may displace more desirable species for a short time, but few sassafras stems will occupy space in the overstory [62].  Some herbicides control sassafras [5]. Complete top-kill was achieved with injection of 2,4-D, picloram, and glyphosate, with no apparent sprouting 2 years after treatment [66]. Arsenal (an imidazolinone-based herbicide) also controls sassafras [57]. Other herbicides do not control root sprouting [33,62]. Dense stands of sassafras are difficult to convert to pine or more desirable hardwoods [41].  Mowing is not effective in controlling sassafras; root sprouts quickly replace or increase aboveground stems [5]. Sassafras is difficult to transplant because of the sparse, far-ranging root system [75]. In North Carolina, mechanical removal of all nondesirable stems (intensive silvicultural cleaning) increased the amount of sassafras browse available to white-tailed deer. .  Prior to the cleaning, sassafras was out of reach of the deer; sprouts arising after the cleaning were within reach [18]. Major diseases of sassafras include leaf blight, leaf spot, Nectria canker and American mistletoe (Phoradendron flavescens) [41]. Insect pests of sassafras are mostly minor; the most damaging insects are the larvae of wood-boring weevils, gypsy moths, loopers, and Japanese beetles [41]. Sassafras is extremely sensitive to ozone [43].


SPECIES: Sassafras albidum
GENERAL BOTANICAL CHARACTERISTICS : Sassafras is a native, deciduous, aromatic tree or large shrub, with a flattened, oblong crown [41,83].  On the best sites, height ranges up to 98 feet (30 m) [41].  In the northern parts of its range, sassafras tends to be shrubby, especially on dry, sandy sites, and reaches a maximum of 40 feet (12 m) [49].  The bark of older stems is deeply furrowed, or irregularly broken into broad, flat ridges [38,83].  The variety of leaf shapes to be found on one individual is a distinctive trait of the species.  Leaves can be entire, one-lobed, or two-lobed. The fruit is a drupe [41].  The root system is shallow, with prominent lateral roots.  Root depth ranges from 6 to 20 inches (15-50 cm). RAUNKIAER LIFE FORM :       Phanerophyte REGENERATION PROCESSES : Sexual reproduction:  Sassafras is sexually mature by 10 years of age, and best seed production occurs between 25 and 50 years of age.  Good seed crops are produced every 1 to 2 years.  Seeds are dispersed by birds, water, and small mammals.  Sassafras seeds are usually dormant until spring, but some germination occurs in the fall immediately following dispersal [41].  Stratification in sand for 30 days at 41 degrees Fahrenheit (5 deg C) breaks the natural dormancy.  Average germination rate is around 85 percent [83].  Since sassafras seeds are relatively large, initial establishment is not highly dependent on available soil nutrients.  Other factors appear to play a greater role. Seedling establishment occurred at higher than randomly expected frequencies on microsites with greater ground cover, less light, or deeper litter than other microsites [14].  Sassafras seeds were found in seed banks under red pine (Pinus resinosa), eastern white pine (P. strobus), and Virginia pine (P. virginiana) stands [6].  Sassafras seedling reproduction is usually sparse and erratic in wooded areas.  In these areas, reproduction is usually vegetative [32,41]. Asexual reproduction:  Sassafras forms dense thickets of root sprouts, and young trees sprout from the stump [41].  After clearcutting in upland hardwood stands (Indiana), 86.5 percent of sassafras regeneration was of seedling or seedling sprout origin; the remainder was of stump sprout origin [36]. SITE CHARACTERISTICS : Sassafras occurs on nearly all soil types within its range, but is best developed on moist, well-drained sandy loams in open woodlands [41]. Optimum soil pH ranges from 6.0 to 7.0, but sassafras also occurs on acid sands in eastern Texas [41,75].  It is intolerant of poorly drained soils [32].  Sassafras occurs along fence rows and on dry ridges and upper slopes, particularly following fire [41].  Sassafras occurs at elevations ranging from Mississippi River bottomlands up to 4,000 feet (1,220 m) in the southern Appalachian Mountains, occasionally up to 4,900 feet (1,500 m) [24,41]. SUCCESSIONAL STATUS : Facultative Seral Species Sassafras is a frequent pioneer in old fields, and is a member of seral stands in the Southeast [41].  In old-field succession in Tennessee, sassafras was a dominant member of a 15-year-old stand, and was not present in a 48-year-old stand [11].  In Virginia, sassafras persists to mid-successional stages with black locust, Virginia pine, pitch pine, eastern white pine, scarlet oak, blackjack oak, and post oak [86].  It also occurs in the canopy of old-growth forests in Illinois and Michigan [45,71].  In the Michigan stands sassafras decreased in relative density during a 20-year study [45].  The persistence of sassafras into later seres and climax stands may be a result of gap capture; in an old-growth forest in Massachusetts, older sassafras trees appear to be associated with hurricane and/or windthrow gaps.  There was no evidence of fire disturbance in this forest [25].  Human activities and disturbance can foster sassafras establishment in old-growth stands.  The relatively high abundance of sassafras under Virginia pine stands is associated with a greater frequency of tree-fall gaps under Virginia pine than under red pine or eastern white pine [6].  Sassafras seedlings in Table Mountain pine (Pinus pungens) stands are able to exploit canopy gaps at the expense of Table Mountain pine [87]. A detailed study of age structure in mixed forests in Virginia reveals another role for sassafras.  In 45- to 80-year-old mixed hardwoods and mixed pine stands, sassafras seedlings and saplings occur in large numbers.  They rarely survive more than 30 years except on moist sites. On relatively dry sites, sassafras does not survive long enough to occupy upper canopy positions.  But since sassafras sprouts prolifically, there is a constant turnover of sassafras stems; older stems die back and are replaced by new ramets.  Sassafras in the understory produces fruit under these conditions.  In these stands, sassafras is apparently functioning as a dominant shrub [72]. In New Jersey, fragmented mixed oak forests were compared with forests that were continuous.  Sassafras was present in 63 percent of the fragments, compared to 25 percent of the continuous stands [37]. Sassafras exhibits a positive response to overstory removal; overstory defoliation by gypsy moths results in an increase in the number of sassafras stems [1]. An unusual pure stand of sassafras was reported by Lamb [59] in 1923. This stand appeared to have remained essentially pure and intact for over 100 years.  The trees were described as fully mature, slow growing, and the soil was very fertile.  It is possible that the persistence of this stand, and the competitive success of sassafras in pioneer communities are related to the presence of terpenoid allelopathic substances in sassafras leaves .  These substances affect, among other species, American elm (Ulmus americana) and box elder (Acer negundo). The susceptibility of these species appears to be related to their habit of germination immediately following dispersal.  The toxic terpenes are washed off of summer leaves and are less concentrated in winter and spring when no fresh leaves are present [31,34]. SEASONAL DEVELOPMENT : Depending upon latitude, sassafras flowers from March to May [24], and fruits ripen from June to September [68,76,77].


SPECIES: Sassafras albidum
FIRE ECOLOGY OR ADAPTATIONS : Sassafras is moderately resistant to fire damage to aboveground growth. It is also highly resilient to such damage; sassafras sprouts vigorously following top-kill, even after repeated fires [54].  In Indiana, sassafras occurs in black oak (Quercus velutina) stands with a mean fire interval of 11.1 years [47].  Sassafras establishment on these sites appears to be related to the frequency and severity of fire.  Sassafras did not occur on sites which had burned more often (mean fire interval of 5.2 years).  The stands with longer fire-free intervals burned more severely than those with shorter intervals.  The more severe disturbance probably created more favorable conditions for sassafras seedling establishment [48]. An increase in the frequency of sassafras in New Jersey forests since European settlement has been attributed, at least in part, to an increase in fire frequency [73]. The bear oak type, in which sassafras frequently occurs, is a product of periodic fire and droughty soils [44].  Sassafras also occurs in the Table Mountain pine-pitch pine (Pinus rigida) type, another fire-adapted community [42]. Sassafras bark is less resistant to heat than chestnut oak (Quercus prinus), white oak (Q. alba), and northern red oak (Q. rubra); equally as resistant as hickory and red maple (Acer rubrum); and more resistant than witchhazel (Hamamelis virginiana), fire cherry (Prunus pensylvanica), serviceberry (Amelanchier spp.), and bear oak [20]. FIRE REGIMES : Find 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". POSTFIRE REGENERATION STRATEGY :    Tree with adventitious-bud root crown/soboliferous species root sucker    Ground residual colonizer (on-site, initial community)    Initial-offsite colonizer (off-site, initial community)    Crown residual colonizer (on-site, initial community)


SPECIES: Sassafras albidum
IMMEDIATE FIRE EFFECT ON PLANT : Low-severity fires kill seedlings and small saplings.  Moderate- and high-severity fires injure mature trees, providing entry for pathogens [41,75].  In oak savanna in Indiana, sassafras showed significantly less susceptibility to low-severity fire than other species [4].  Sassafras exhibited 21 percent mortality of stems after prescribed fire in western Tennessee.  This was the lowest mortality of all hardwoods present. Season of burning did not affect susceptibility [17]. DISCUSSION AND QUALIFICATION OF FIRE EFFECT : NO-ENTRY PLANT RESPONSE TO FIRE : Sassafras occurs on charcoal hearths, which are patches of ground that were used for charcoal making.  These areas are characterized by very poor soil structure.  Sassafras on these sites shows poor growth [10]. The effects of annual and 5-year interval prescribed burning over a 27-year period in Tennessee has been reported.  After 6 years, sassafras density was higher on annually burned plots than on unburned plots.  The highest sassafras density occurred on the 5-year interval plots [80]. Sassafras gradually decreased with increasing canopy closure on the 5-year interval plots.  By year 27, however, sassafras was eliminated from the annually burned plots.  Sassafras was also eliminated from unburned plots; these plots developed closed canopies which are unfavorable to sassafras [19]. A large number of root sprouts occurred after sapling and small diameter sassafras trees were top-killed by fire in an Illinois post oak (Quercus stellata) stand [12].  Sprout production by top-killed sassafras was stimulated by prescribed fire, and greatly increased its cover in the shrub layer [13]. In Illinois, the number of small sassafras stems increased after a single winter prescribed fire from 9 percent frequency to 36 percent frequency.  This increase was largely due to root sprouting by top-killed plants.  The number of sassafras seedlings also increased after the same fire [3].  In Virginia, in Table Mountain pine stands that experienced a high-severity wildfire (98 percent top-kill), sassafras increased from 0 to 12.1 in relative importance in 1 year. Sassafras also increased on plots experiencing low-severity fire, but the difference in importance value was not as great [42]. In the absence of fire or other disturbances, sassafras frequency decreases with increasing canopy closure; the number of new sassafras seedlings also decreases with canopy closure [2,3]. Fire does not always lead to increased sassafras.  Grelen [40] reported sassafras occurrence on unburned, young slash pine (Pinus elliottii) plots but not on plots burned annually, biennially, or triennially in March or May over the course of 12 years.  In Florida, sassafras was found on unburned, 15-year-old old fields, but not on oldfield plots that were burned annually in February or March for 15 years [26].
The following Research Project Summaries provide information on prescribed
fire use and postfire response of plant community species, including sassafras,
that was not available when this species review was originally written:
Prescribed fire for hardwood control in southern pine stands results in
the predominance of American beautyberry (Callicarpa americana) and
sassafras.  This predominance is a useful indicator of temporary control
over other hardwoods that usually occupy later seres and are more
serious competitors of pine.  Prescribed fire at 8- to 12-year intervals
can control sprout growth or new plant invasion [74].

In South Carolina, a prescribed January fire in loblolly pine increased
sassafras browse quality and availability.  Prior to the fire, sassafras
stems were out of reach of white-tailed deer [21].  The protein content
of sassafras leaves and twigs was highest in June following prescribed
fire.  By September, the protein content of all browse plants was
similar on burned and unburned sites [23].  After logging and
prescribed burning in an oak-pine stand in South Carolina, white-tailed
deer browsed sassafras heavily [27].

Frequent prescribed fire can improve spring and summer forage quality in
the southern pine forests, where sassafras often occurs.

Prescribed fire on utility rights-of-way does not control sassafras [5].
Vigorous root sprouting maintains sassafras even after repeated fires.
Annual prescribed fire, however, may have a detrimental effect on
sassafras fruit production [50].  On some sites, repeated annual fires
may eventually eliminate sassafras [19,26,40].

A regression equation to calculate the relationship of sassafras bark
thickness to stem diameter has been reported [46].  An equation for
predicting standing sassafras dry weight (and therefore fuel loading)
from sassafras basal diameter has also been reported [70].


SPECIES: Sassafras albidum
REFERENCES :  1.  Allen, David; Bowersox, Todd. 1989. Regeneration in oak stands following        gypsy moth defoliations. In: Rink, George; Budelsky, Carl A., eds.        Proceedings, 7th central hardwood conference; 1989 March 5-8;        Carbondale, IL. Gen. Tech. Rep. NC-132. St. Paul, MN: U.S. Department of        Agriculture, Forest Service, North Central Forest Experiment Station:        67-73.  [9369]  2.  Anderson, Roger C.; Schwegman, John E. 1991. Twenty years of        vegetational change on a southern Illinois barren. Natural Areas        Journal. 11(2): 100-107.  [16256]  3.  Anderson, Roger C.; Van Valkenburg, Charles. 1977. Response of a        southern Illinois grassland community to burning. Transactions, Illinois        State Academy of Science. 69(4): 399-414.  [19481]  4.  Apfelbaum, Steven I.; Haney, Alan W. 1990. Management of degraded oak        savanna remnants in the upper Midwest: preliminary results from three        years of study. In: Hughes, H. Glenn; Bonnicksen, Thomas M., eds.        Restoration `89: the new management challenge: Proceedings, 1st annual        meeting of the Society for Ecological Restoration; 1989 January 16-20;        Oakland, CA. Madison, WI: The University of Wisconsin Arboretum, Society        for Ecological Restoration: 280-291.  [14705]  5.  Arner, Dale H. 1981. Prescribed burning in utility rights-of-way        management. In: Wood, Gene W., ed. Prescribed fire and wildlife in        southern forests: Proceedings of a symposium; 1981 April 6-8; Myrtle        Beach, SC. Georgetown, SC: Clemson University, Belle W. Baruch Forest        Science Institute: 163-166.  [14823]  6.  Artigas, Francisco J.; Boerner, Ralph E. J. 1989. Advance regeneration        and seed banking of woody plants in Ohio pine plantations: implications        for landscape change. Landscape Ecology. 2(3): 139-150.  [13633]  7.  Blair, Robert M.; Short, Henry L.; Burkart, Leonard F.; [and others].        1980. Seasonality of nutrient quality and digestibility of three        southern deer browse species. Res. Pap. SO-161. New Orleans, LA: U.S.        Department of Agriculture, Forest Service, Southern Forest Experiment        Station. 13 p.  [15864]  8.  Brown, Russell G.; Brown, Melvin L. 1972. Woody plants of Maryland.        Baltimore, MD: Port City Press. 347 p.  [21844]  9.  Carey, Andrew B.; Gill, John D. 1980. Firewood and wildlife. Res. Note        299. Broomall, PA: U.S. Department of Agriculture, Forest Service,        Northeastern Forest Experiment Station. 5 p.  [9925] 10.  Clatterbuck, Wayne K. 1991. Forest development following disturbances by        fire and by timber cutting for charcoal production. In: Nodvin, Stephen        C.; Waldrop, Thomas A., eds. Fire and the environment: ecological and        cultural perspectives: Proceedings of an international symposium; 1990        March 20-24; Knoxville, TN. Gen. Tech. Rep. SE-69. Asheville, NC: U.S.        Department of Agriculture, Forest Service, Southeastern Forest        Experiment Station: 60-65.  [16634] 11.  Clebsch, Edward E. C.; Busing, Richard T. 1989. Secondary succession,        gap dynamics, and community structure in a southern Appalachian cove        forest. Ecology. 70(3): 728-735.  [6972] 12.  Coates, Darryl T.; Lyman, Kevin J.; Ebinger, John E. 1992. Woody        vegetation structure of a post oak flatwoods in Illinois. Castanea.        57(3): 196-201.  [19714] 13.  Cole, Kenneth L.; Benjamin, Pamela K.; Klick, Kenneth F. 1990. The        effects of prescribed burning on oak woods and prairies in the Indiana        Dunes. Restoration & Management Notes. 8(1): 37-38.  [13552] 14.  Collins, Scott L.; Good, Ralph E. 1987. The seedling regeneration niche:        habitat structure of tree seedlings in an oak-pine forest. Oikos. 48:        89-98.  [8637] 15.  Crawford, Hewlette S.; Hooper, R. G.; Harlow, R. F. 1976. Woody plants        selected by beavers in the Appalachian Ridge and Valley Province. Res.        Pap. NE-346. Upper Darby, PA: U.S. Department of Agriculture, Forest        Service, Northeastern Forest Experiment Station. 6 p.  [20005] 16.  Davidar, Priya; Morton, Eugene S. 1986. The relationship between fruit        crop sizes and fruit removal rates by birds. Ecology. 67(1): 262-265.        [20743] 17.  de Bruyn, Peter; Buckner, Edward. 1981. Prescribed fire on sloping        terrain in west Tennessee to maintain loblolly pine (Pinus taeda). In:        Barnett, James P., ed. Proceedings, 1st biennial southern silvicultural        research conference; 1980 November 6-7; Atlanta, GA. Gen. Tech. Rep.        SO-34. New Orleans, LA: U.S. Department of Agriculture, Forest Service,        Southern Forest Experiment Station: 67-69.  [12091] 18.  Della-Bianca, Lino; Johnson, Frank M. 1965. Effect of an intensive        cleaning on deer-browse production in the southern Appalachians. Journal        of Wildlife Management. 29(4): 729-733.  [16404] 19.  DeSelm, Hal R.; Clebsch, Edward E. C.; Rennie, John C. 1991. Effects of        27 years of prescribed fire on an oak forest and its soils in middle        Tennessee. In: Coleman, Sandra S.; Neary, Daniel G., compiler.        Proceedings, 6th biennial southern silvicultural research conference:        Vol. 1; 1990 October 30 - November 1; Memphis, TN. Gen. Tech. Rep.        SE-70. Asheville, NC: U.S. Department of Agriculture, Forest Service,        Southeastern Forest Experiment Station: 409-417.  [17488] 20.  Kaufman, H. P. 1942. A study of forest-wildlife problems. Annual        Progress Report: Project 9R. Federal Aid in Wildlife Restoration.        [Washington, DC]: [Publisher unknown]. [Unknown pages].  [24535] 21.  Devet, David D.; Hopkins, Melvin L. 1968. Response of wildlife habitat        to the prescribed burning program on the National Forests in South        Carolina. 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