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Woody species composition following a wildfire in the Dugger Mountain Wilderness, Talladega National Forest, al.

ABSTRACT

A point-centered quarter survey was conducted within the Dugger Mountain Wilderness in the Talladega National Forest eighteen months after a March 2007 wildfire to determine tree and sapling species composition. In the tree stratum, dominant species were Quercus prinus, Pinus echinata, Pinus virginiana, Quercus velutina, and Oxydendrum arboreum. The summed importance value of Quercus species in the tree stratum was 53.99. Dominant species in the sapling stratum included Acer rubrum, Nyssa sylvatica, and Prunus alabamensis. The importance value of sapling A. rubrum (23.62) and N. sylvatica (25.73) exceeded that of all oaks combined (16.26). A. rubrum, N. sylvatica, and P. alabamensis were observed to be prolific sprouters following the fire. Unless a pre-Colonial fire regime is restored with the possibility of more intense fires, the high importance value of A. rubrum and N sylvatica in the sapling stratum may prevail over Quercus species resulting in an overstory dominated by shade-tolerant species with low fire resistance. Due to restrictions on management mandated by the Wilderness Act of 1964, it is not likely that fires of the needed intensity to maintain the current Quercus dominated overstory will be possible.

INTRODUCTION

Lightning-caused and Native American set fires historically were a major force in shaping ecosystems of the eastern US (Van Lear and Waldrop 1989, Frost 1998, Abrams 2006). Frequent, low intensity fires created conditions favorable for the establishment and dominance of Quercus (Abrams 2000, Van Lear et al. 2000) and other fire tolerant species (Wade et al. 2000). Quercus species have an ecological advantage under a regime of frequent fires due to their thick bark, sprouting ability, and resistance to decay when damaged (Lorimer 1985). In addition, fire reduces soil moisture that would favor mesophytic species, prepares a seedbed by reducing litter thickness, and reduces competition from fire-intolerant species (Barnes and Van Lear 1998, Darley-Hill and Johnson 1981, Van Lear and Watt 1993).

Since the early 1900's, the understory of Quercus dominated forests has been invaded by shade-tolerant later successional species, such as Acer rubrum (Abrams 2000), that may eventually replace Quercus dominance in the overstory (Abrams 2000, Lorimer 1985, McGee 1984, Wade et all 2000). A. rubrum and other mesophytic species can become so dense that the shade reduces Quercus seedling and forb abundance. The long-term effect is a reduction in species richness as fire adapted species are replaced by more fire-sensitive species (Nowacki and Abrams 2008). Thus, fire exclusion can be a major disruption in Quercus dominated ecosystems (Packard 1993). When fire does return to fire suppressed sites, the mesophytic species are often top-killed but resprout and may dominate the site (Wade et al. 2000). Such is the case in Tennessee where repeated low intensity fires reduced A. rubrum seedling density, but the surviving A. rubrum grew at a faster rate than the Quercus seedlings present (Green et at 2010).

The absence of fire in the Dugger Mountain Wilderness could result in unnatural conditions such as the intrusion of mesophytic species into the landscape (Lorimer 1985, McGee 1984, Wade et at 2000), but the use of prescribed fire could result in a less self-willed landscape (Parsons et at 1986) in violation of the Wilderness Act. According to section 2 (a) of the Wilderness Act of 1964, designated Wilderness Areas are to be untrammeled by humans and retain a primeval character that is protected and managed to preserve its natural conditions. The human imprint should be substantially unnoticeable (Hendee et at 1990). The use of prescribed fire in wilderness areas managed by the Forest Service is permitted to reduce fuel loadings but not to restore natural processes (Parsons et at 1986). This study sought to assess the species composition of saplings and trees following a wildfire in the Dugger Mountain Wilderness to determine post-fire regeneration and the potential future overstory.

MATERIALS AND METHODS

The study area was within the Dugger Mountain Wilderness located on the Shoal Creek Ranger District of the Talladega National Forest, Calhoun County, Alabama. This area is in the Southern Ridge and Valley Section and is characterized by low mountains with steep slopes and shallow excessively drained soils. The elevation ranges from 244 to 640 meters above sea level (Soil Conservation Service 1958). A low intensity human caused wildfire burned 267 hectares in the northern end of the wilderness area from February 27-March 4 2007. The surface fire with 0.5 to 1.8m flame lengths consumed primarily hardwood leaf litter and downed hardwood and pine trees.

In September of 2008, 18 months following the fire, a point-center quarter survey (Cottam and Curtis 1956) of trees and saplings was conducted on a 200 X 200 meter grid throughout the burned area. At each point, four quarters were established (northeast, southeast, northwest, southwest). Within each quarter, the diameter at breast height (dbh) and distance to the center of each sapling and tree closest to the center point were measured Saplings were defined as manifesting woody sterns at least 1.4 m tall but less than 11.4 cm dbh. Woody stems greater than 11.4 cm dbh were considered trees. The tree density, basal area, relative frequency, relative density, relative basal area, importance value, and density were calculated for each species in the tree and sapling strata. A pine plantation established before the creation of the wilderness area was excluded from sampling.

Calculations were performed utilizing with the following formulae:

Frequency = number of points containing a species

Relative frequency = frequency/sum of frequencies for all species * 100

Density = number of sterns per species

Relative density = density/total number of sterns * 100

Basal area = sum of dbh by species/2 * [pi]

Relative basal area = basal area per species/sum of basal area * 100

Importance value = Relative frequency + relative density + relative basal area/3

Area of tree coverage = [[(total distance for all species/number of stems)/2].sup.2] * [pi]

Total stems/ha = 10,000m/area of tree coverage

Stems/ha by species = total stems/ha * relative density

RESULTS

In the tree stratum, dominant species based on importance values were Quercus prinus, Pinus echinata, P. virginiana, and Oxydendrum arboreum (Table 1). Q. prinus dominated in terms of importance value and density (Table 1). The importance value of Quercus species summed to 53.99, while the importance value sum for Pinus species was only 22.30, half that of Q. prinus (44.23) alone (Table 1). Acer rubrum and Nyssa sylvatica had importance values of 3.81 and 2.97, respectively.
Table 1. Relative frequency, relative density, relative abundance,
importance value, basal area, and density of trees following a
wildfire in the Dugger Mountain Wilderness, Talladega National
Forest, Alabama.

Tree Species  Relative   Relative  Relative   Importance    Density
                                                Density     (stems/ha)
              Frequency  Density   Abundance    Value

Acer rubrum        5.44      4.56       1.42        3.81       21.12

Carya alba         0.68      0.42       0.09        0.40        1.92

Carya glabra       4.76      5.39       3.79        4.65       24.96

Carya              2.04      2.49       1.81        2.11       11.52
pallida

Cornus             1.36      0.83       0.20        0.80        3.84
florida

Liriodendron       0.68      0.42       0.25        0.45        1.92
tulipifera

Nyssa              4.08      2.90       1.97        2.97       13.44
sylvatica

Oxydendrum         9.52      8.30       2.95        6.93       38.40
arboreum

Pinus             10.88     10.37       8.51        9.92       48.00
echinata

Pinus taeda        4.08      2.90       2.64         321       13.44

Pinus              9.52      9.54       8.45        9.17       44.16
virginiana

Prunus             2.04      1.24       0.34        1.21        5.76
alabamensis

Quercus            0.68      0.42       0.64        0.58        1.92
coccinea

Quercus            2.04      1.55       0.42        1.38        7.68
marilandica

Quercus           31.97     41.08      59.62       44.23      190.08
prinus

Quercus            0.68      0.42       1.55        0.88        1.92
rubra

Quercus            2.72      1.66       0.74        1.71        7.68
stellata

Quercus            6.12      4.98       4.53        5.21       23.04
velutina

Vaccinium          0.68      0.42       0.08        0.39        1.92
arboreum

Tree Species  Basal Area
              ([m.sup.2]
                 /ha)

Acer rubrum      0.08403

Carya alba       0.00664

Carya glabra     0.14977

Carya            0.07088
pallida

Cornus           0.01403
florida

Liriodendron     0.02113
tulipifera

Nyssa            0.07639
sylvatica

Oxydendrum       0.16943
arboreum

Pinus            0.30793
echinata

Pinus taeda      0.09179

Pinus            0.29504
virginiana

Prunus           0.02196
alabamensis

Quercus          0.01802
coccinea

Quercus          0.02880
marilandica

Quercus          1.56035
prinus

Quercus          0.02805
rubra

Quercus          0.03794
stellata

Quercus          0.16066
velutina

Vaccinium        0.00639
arboreum


Dominant species in the sapling stratum included Acer rubrum, Nyssa sylvatica, and Prunus alabamensis (Table 2). A. rubrum and N. sylvatica both exceeded 20% of relative frequency, density, and abundance. Combined the importance value of A. rubrum and N. sylvatica was 49.35 and the density was 53.46%. Even when the importance values of Quercus saplings was summed (16.26), it did not exceed that of Acer rubrum or Nyssa sylvatica (Table 2). When considering just saplings [less than or equal to] 2.54 cm in diameter at breast height, Q. prinus was the fourth most abundant species following A. rubrum, N. sylvatica, and P. alabamensis (Table 3).
Table 2. Relative frequency, relative density, relative abundance,
importance value, basal area, and density of saplings following a
wildfire in the Dugger Mountain Wilderness, Talladega National
Forest, Alabama

Sapling       Relative  Relative  Relative  Importance  Density
species

Acer rubrum      23.46     26.44     20.95       23.62  160.18

Carya glabra      1.24      0.77      2.21        1.41    4.64

Carya             1.85      0.77      1.27        1.30    4.64
pallida

Cornus            5.56      4.21      7.60        5.79   25.54
florida

Liquidambar       0.62      0.38      0.01        0.34    2.32
styraciflua

Liriodendron      0.62      0.38      0.08        0.36    2.32
tulipifera

Nyssa            22.84     27.20     27.14       25.73  164.83
sylvatica

Oxydendrum        5.56      3.84      3.24        4.21   23.22
arboreum

Pinus             1.23      1.15      1.89        1.42    6.97
echinata

Pinus             0.62      0.38      0.99        0.66    2.32
palustris

Pinus             0.62      0.38      0.93        0.64    2.32
virginiana

Prunus           14.82     13.80     14.14       14.25   83.57
alabamensis

Primus            1.85      1.50      0.22        1.07    6.96
serotina

Quercus           1.23      1.15      0.88        1.09    6.96
marilandica

Quercus           9.88      9.58     10.59       10.01   58.04
prinus

Quercus           1.85      1.53      3.73        2.37    9.29
stellata

Quercus           3.09      3.45      1.84        2.79   20.90
velutina

Rhus              0.62      0.38      0.01        0.34    2.32
copallinum

Sassafras         0.62      1.15      1.51        1.09    6.97
albidum

Vaccinium         1.85      1.92      0.78        1.52   11.61
arboreum

Sapling        Basal
species         Area

Acer rubrum   0.10099

Carya glabra  0.00839

Carya         0.00501
pallida

Cornus        0.03481
florida

Liquidambar   0.00038
styraciflua

Liriodendron  0.00113
tulipifera

Nyssa         0.13899
sylvatica

Oxydendrum    0.01565
arboreum

Pinus         0.00902
echinata

Pinus         0.00401
palustris

Pinus         0.00388
virginiana

Prunus        0.06437
alabamensis

Primus        0.00276
serotina

Quercus       0.00576
marilandica

Quercus       0.04746
prinus

Quercus       0.01440
stellata

Quercus       0.00889
velutina

Rhus          0.00038
copallinum

Sassafras     0.00589
albidum

Vaccinium     0.00738
arboreum

Table 3. Stems/ha for saplings [less than or equal to] 2.54 cm dbh
following a wildfire in the Dugger Mountain Wilderness, Talladega
National Forest, Alabama

Sapling Species          Density (Stems/ha)

Acer rubrum                          106.79

Carya pallida                          2.32

Cornus florida                         2.32

Liquidambar styraciflua                2.32

Liriodendron tulipifera                2.32

Nyssa sylvatica                       78.93

Oxydendrum arboreum                   16.25

Pinus echinata                         2.32

Prunus alabamensis                    55.72

Prunus serotina                       18.57

Quercus marilandica                    2.32

Quercus prinus                        34.82

Quercus stellata                       2.32

Quercus velutina                       6.96

Rhus copallinum                        2.32

Sassafras albidum                      4.64

Vaccinium arboreum                     6.96


DISCUSSION

The species dominating the sapling stratum, Acer rubrum, Nyssa sylvatica, and Prunus alabamensis, have low fire resistance but are prolific sprouters following fires (Hare 1965, Walters and Yawney 1990, Boyer 1990). A. rubrum has some characteristics of early successional species, such as rapid invasion of disturbed sites, and characteristics of late successional species, such as high tolerance of low light conditions in the understory (Abrams 1998). The reduction of fire frequency in the 20th century permitted A. rubrum to expand from moist areas with low fire frequency to dominate the understory of much of the current Quercus forests (Abrams 2006).

Acer rubrum (Scheiner et al. 1988, Walters and Yawney 1990, Elliott et al. 1999, Green et al. 2010) and Quercus prinus (Elliott et al. 1999) have been shown to increase in abundance following fires due to vigorous sprouting. In the Dugger Mountain Wilderness, Q. prinus saplings ([less than or equal to] 2.54 cm dbh) were relatively dense post-fire but were well below the density of A. rubrum, N. sylvatica, and P. alabamensis (Table 3). In Tennessee, Green et aL (2010) found that low intensity fires reduced A. rubrum seedling survival compared to unburned areas, but the low intensity fires did not provide a successional advantage for Q. prinus seedlings. The Q. prinus and A. rubrum seedling survival levels were nearly equal (Green et aL 2010). The single low intensity fire in the Dugger Mountain Wilderness may even cause increased sprouting of non-oak species (Arthur et aL 1998).

Although A. rubrum and N. sylvatica did not dominate the tree stratum (Table 1), their dominance in the sapling stratum indicates that the future forest without significant disturbances such as fire is likely to be dominated by these species (Arthur et al 1998). A. rubrum and N. sylvatica are prolific sprouters following low intensity fires, and low intensity fires may select for A. rubrum (Green et al 2010). If more shade-tolerant species become established, the understory microenvironment becomes cooler and moister (Nowacki and Abrams 2008) making the application of prescribed fires of acceptable intensity to favor Quercus species more difficult. Green et al. (2010) and Alexander et al. (2008) recommend more intense fires or mechanical canopy removal mixed with low intensity fire to reduce the canopy cover. This will reduce the density of A. rubrum and allow Quercus species with a mid-shade tolerance to receive the light necessary to compete.

Even if a pre-Colonial fire regime is restored to the Dugger Mountain Wilderness, a decline in Quercus species and increases in species with low fire tolerance and high shade tolerance are likely. More intense prescribed fire are not likely in a wilderness area where mechanized equipment is not permitted and mechanical treatment to reduce overstory density would be a violation of the Wilderness Act (Hendee et al. 1990). Thus, the forest within the wilderness area will likely proceed to a mesophytic species dominated forest.

ACKNOWLEDGEMENTS

This research was supported by a grant from the USDA Forest Service.

LITERATURE CITED

Marc D. Abrams. 1998. The Red Maple Paradox. BioScience 48: 355-364.

Abrams, M. 2000. Fire and the Ecological History of Oak Forests in the Eastern United States. In: D. A. Yaussy [comp], Proceedings: workshop on fire, people, and the central hardwoods landscape, 46-55. USDA Forest Service GTR NE-274.

Abrams, Marc D. 2006. Ecological and ecophysiological attributes and responses to fire in eastern oak forests. In: M.B. Dickinson [ed.], 2006. Fire in eastern oak forests: delivering science to land managers, proceedings of a conference, 74-89. USDA Forest Service GTR NRS-P-1.

Alexander, H.D., Arthur, M.A., Loftis, D.L., Green, S.R., 2008. Survival and growth of upland oak and co-occurring competitor seedlings following single and repeated prescribed fires. Forest Ecology and Management 256:1021-1030

Arthur, M.A., R.D. Paratley, and B.A. Blankenship. 1998. Single and repeated fires affect survival and reproduction of woody and herbaceous species in an oak-pine forest. Journal of the Torrey Botanical Society 125: 225-236.

Barnes, T.A. and D.H. Van Lear. 1998. Prescribed fire effects on hardwood advanced regeneration in mixed hardwood stands. Southern Journal of Applied Forestry 22: 138-142.

Boyer, W.D. 1990. Growing-season burns for control of hardwoods in longleaf pine stands. USDA Forest Service RP SO-256. 7 p.

Cottam, G. and J.T. Curtis. 1956. The use of distance measures in phytosociological sampling. Ecology 37: 451-460.

Darley-Hill, S. and W. C. Johnson. 1981. Acorn dispersal by the blue jay (Cyanocitta cristata). Oecologia 50: 231-232.

Elliott, K.J., R.L. Hendrick, A.E. Major, J.M. Vose, and W.T. Swank. 1999. Vegetation dynamics after a prescribed fire in the southern Appalachians. Forest Ecology and Management 114: 199-213.

Frost, C. 1998. Presettlement fire frequency regimes of the United States: a first approximation In T.L. Pruden and L.A. Brennan [eds.], 20th Tall Timbers Fire Ecology Conference: Fire in ecosystem management: shifting the paradigm from suppression to prescription, 70-81. Tall Timbers Research, Inc., Tallahassee, FL.

Green, S.R., M.A. Arthur, and B.A. Blankenship. 2010. Oak and red maple seedling survival and growth following periodic prescribed fire on xeric ridgetops on the Cumberland Plateau. Forest Ecology and Management 259:2256-2266

Hare, R.C. 1965. Contribution of bark to fire resistance of southern trees. Journal of Forestry 63: 248-251.

Hendee, J.C., G.H. Stankey, R.C. Lucas. 1990. Wilderness Management. North American Press, Golden, CO. 546 pp.

Lorimer, C.G. 1985. The role of fire in the perpetuation of oak forests. In J.E. Johnson [ed.], Proceedings: Challenges in oak management and utilization, 8-25. University of Wisconsin Cooperative Extension Service, Madison, WI.

McGee, C.E. 1984. Heavy mortality and succession in a virgin mixed mesophytic forest. USDA Forest Service RS SO-209. 7 p.

Nowacki, G.J. and M.D. Abrams. 2008. The Demise of Fire and "Mesophication" of Forests in the Eastern United States. BioScience 58: 124-138.

Packard, S. 1993. Restoring Oak Ecosystems. Restoration and Management Notes. 11: 5-16.

Parsons, D.J. D.M. Graber, J.K. Agtt, and J. W. Van Wagmndonk. 1986. Natural fire management in national parks. Environmental Management 10: 21-24.

Scheiner, S.M., T.L. Sharik, M.R. Roberts, and R. Vande Kopple. 1988. Tree density and modes of tree recruitment in a Michigan pine-hardwood forest after clear-cutting and burning. Canadian Field Naturalist 102: 634-638.

Soil Conservation Service. 1958. Soil survey of Calhoun County, Alabama. USDA Soil Conservation Service.

Van Lear, D.H. and T.A. Waldrop. 1989. History, uses, and effects of fire in the Appalachians. USDA Forest Service GTR SE-54. 20 p.

Van Lear, D.H. and J.M. Waft. 1993. The role of fire in oak regeneration. In D. Loftis and C.E. McGee [eds.], Oak regeneration: serious problems, practical recommendations, 1992 symposium proceedings, 66-78. USDA Forest Service GTR SE-84.

Van Lear, D.H., P.H. Brose, and P.D. Keyser. 2000. Using prescribed fire to regenerate oaks. In D.A. Yaussy [ed.], Proceedings: workshop on fire, people, and the central hardwoods landscape, 97-102. USDA Forest Service GTR NE-274.

Wade, D.D., B.L. Brock, P.H. Brose, J.B. Grace, G.A. Hoch, W. A. Patterson III. 2000. In K.K. Brown and J.K. Smith [eds.], Wildland fire in ecosystems: effects of fire on flora, 53-98. USDA Forest Service GTR RMRS-GTR-42, vol 2.

Walters, R.S. and H.W. Yawney. 1990. Acer rubrum L. red maple. In R.M. Burns and B.H. Honkala [eds.], Silvics of North America. Vol. 2. Hardwoods, 60-69. USDA Agricultural Handbook 654. Washington, DC.

Robert E. Carter and Grant C. Cobb

Department of Biology, Jacksonville State University, 700 Pelham Road North, Jacksonville, AL 36265

Correspondence Robert Carter (rcarter@jsu.edu)
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Publication:Journal of the Alabama Academy of Science
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Geographic Code:1U6AL
Date:Jan 1, 2012
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