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Long-Term Effects of High Intensity Prescribed Fire on Vegetation Dynamics in the Wine Spring Creek Watershed, Western North Carolina, USA

Abstract

We examined the long-term effects of a prescribed fire in a southern Appalachian watershed in Nantahala National Forest, western North Carolina, USA. Fire was prescribed in 1995 on this site by forest managers to restore a degraded pine (Pinus spp.)-hardwood community, specifically to stimulate forage production, promote pine and oak (Quercus spp.) regeneration, and increase plant diversity. Before and after the prescribed fire, permanent plots were sampled across a south-facing hillslope, which corresponded to three community types: mesic, near-stream cove (riparian); dry, mixed-oak (mid-slope); and xeric, pine-hardwood (ridge). In an earlier paper, we reported the first two years of post-burn vegetation response from this prescribed burn. In our current study, we compared the pre-burn (1994) forest condition with 10 years post-burn (2005) vegetation measurements to determine the effects of fire on the mortality and regeneration of overstory trees, understory shrubs, and herbaceous-layer species. Overstory mortality was high immediately after the burn at the ridge location and ten years after the fire. Mortality of pitch pine (Pinus rigida Miller) (91.8 %) and hickory (Carya spp.) (77.5 %) reduced overstory basal area from 26.97 m2 ha−1 pre-burn to 18.86 m2 ha−1 post-burn in 1995 and to 9.13 m2 ha−1 in 2005. At the mid-slope and riparian locations, no significant overstory mortality occurred over time. Understory density was significantly higher 10 years after the burn (2005) than pre-burn, and basal area had returned to pre-burn levels. Density of mountain laurel (Kalmia latifolia L.), black huckleberry (Gaylussacia baccata [Wang.] K. Koch), and blueberry (Vaccinium spp.) had increased due to prolific sprouting. The prescribed fire had varying effects on diversity across the hillslope gradient over time. On the ridge, overstory diversity declined following the fire (H’basal area = 1.14 in 1994, H’basal area = 0.75 in 1995, and H’basal area = 0.80 in 2005). Diversity significantly increased in the herbaceous layer and remained higher than pre-burn conditions through 2005 (H’cover = 1.02 in 1994, H’cover = 1.97 in 1995, and H’cover = 2.25 in 2005). For the mid-slope and riparian positions, no change in diversity was observed in the overstory, understory or herbaceous layer.

Introduction

Prescribed burning is currently being used as a management tool to reduce fuel loads, improve wildlife habitat, and to restore ecosystem structure and function in the southern Appalachian forests of the USA that are managed by the Forest Service, the National Park Service, and The Nature Conservancy. Historically, fire was an integral part of the Appalachian forests and determined their natural structure and composition (Barden and Woods 1976, Harmon 1982, Buckner 1989, Van Lear and Waldrop 1989, DeVivo 1991, Brose et al. 2001, Brose and Waldrop 2006, Petersen and Drewa 2006). In particular, mixed pine-hardwood forest types occupying dry ridge sites were thought to be dependent on fire for their maintenance (Barden and Woods 1976, Barden 2000, Lafon et al. 2007). Fire suppression and the limited occurrence of natural fires in xeric pine-hardwood forests have promoted the dominance of hardwoods, and the pine component has been in decline for about three decades (Smith 1991, Vose et al. 1994, Elliott and Vose 2005). In addition, substantial drought-related insect populations (primarily southern pine beetle [Dendroctonus frontalis Zimmermann]) (Hoffmann and Anderson 1945, Smith 1991, Elliott et al. 1999a, Elliott and Vose 2005) and previous land use practices, such as high-grading, have contributed to further changes in these forests. The result is a significant increase in acreage of stands with a dense understory of mountain laurel (Kalmia latifolia L.), an evergreen ericaceous shrub, on upper, drier slopes. Competition with mountain laurel inhibits the reproduction and growth of both woody and herbaceous vegetation so that changes in species composition and stand structure are likely to persist without management intervention

The mixed-oak (Quercus spp.) stands that occupy mesic, sub-mesic, and dry forests at middle elevations are also undergoing considerable change. Oaks were a dominant feature of the southern Appalachians long before European settlement (Clark and Robinson 1993, Abrams 2005), and throughout the entire region various species of oak remain major components of many forest types (Nowacki and Abrams 1992, Stephenson et al. 1993). However, the decline in oak abundance across the eastern US has been documented in numerous studies (Oak et al. 2004, Abrams 2005, Guldin et al. 2006, Heitzman et al. 2007). These submesic to dry oak forests were established and historically maintained by a combination of natural and human-induced fires (Lorimer 1984, Abrams and Nowacki 1992). In the absence of fire, shade-tolerant species, such as red maple (Acer rubrum L.), that formerly were confined to the understory have become established and are recruiting into the overstory at unprecedented rates (Lorimer 1985, Crow 1988, Elliott et al. 1999b, Galbraith and Martin 2005, Rentch and Hicks 2005, Fei and Steiner 2007, Elliott and Swank 2008).

In the southern Appalachians, fire has been prescribed as a silvicultural treatment in pine-hardwood forests to restore diversity and productivity (Swift et al. 1993) and to promote regeneration of native pines and oaks (Vose et al. 1994, Vose et al. 1997). Fire can reduce the abundance of mountain laurel and delay its growth (Clinton et al. 1993), encourage oaks and various other tree species to sprout (Van Lear and Waldrop 1989), and provide a seedbed where native pines can germinate and become established (Elliott et al. 1999a, Waldrop and Brose 1999, Waldrop et al. 2000).

Much is known about short-term vegetation responses to fire in the southern and central Appalachians (Johnson 1985, Van Lear and Waldrop 1989, Van Lear and Watt 1993, Elliott et al. 1999 a, Welch et al. 2000, Van Lear et al. 2004, Elliott and Vose 2005, Signell et al. 2005), but few studies document longer-term responses (Blankenship and Arthur 2006). Long-term studies are necessary for evaluating and predicting the response of mixed-oak/pine communities following wildland fire.

In this study, we examined the longer-term effects of a single, dormant season fire in the Nantahala National Forest, western North Carolina, USA. In 1995, the fire was ignited across a south-facing slope, an area where fire had been excluded for over 70 years. The purpose of the burn was to create a mosaic of fire intensities to restore a pine-hardwood community, stimulate forage production, reduce the understory biomass of mountain laurel and shade-tolerant hardwood species, and promote pine and oak regeneration along the hillslope gradient. In earlier papers, we compared the first two years of responses to the pre-burn forest condition (Elliott et al. 1999 a, Vose et al. 1999). This current paper addresses the longer-term effects 10 years after a single, prescribed fire.

Methods

Study Area

The study area is located in the Nantahala National Forest in the southern Appalachian Mountains of western North Carolina (35°N latitude, 83°W longitude) and is part of the Wine Spring Creek Ecosystem Management Project (Swank et al. 1994). The Wine Spring Creek watershed is within the Blue Ridge Mountains District of the Blue Ridge physiographic province. The area has a southern aspect and elevations range from 1500 m to 1700 m with slopes ranging from 35 % to 60 %. The soil types along the upper slope and ridge are fine-loamy, mixed, mesic Typic Hapludults (Edneyville Series) and loamy, mixed, mesic Lithic Dystrochrepts (Cleveland Series); and the soils along the middle and lower slope positions are coarse-loamy to a loamy-skeletal, mixed, mesic Typic Haplumbrepts (Cullasaja Series) (Thomas 1996). Mean annual temperature is 10.4°C and mean annual precipitation is 1900 mm (Coweeta Hydrologic Laboratory, unpublished data).

A prescribed burn of approximately 300 ha was conducted in April 1995. The fire was ignited by helicopter at the bottom of the south facing slope near the stream. It created a mosaic of fire intensities across the hillslope, ranging from lightly burned (flame temperatures < 80°C) at the low slope to heavily burned (flame temperatures > 800°C) along upper slopes and ridges (Vose et al. 1999). Heat penetration into the soil also varied along the hillslope. On the ridge, a 45°C heat pulse penetrated 27.5 mm and a 59°C heat pulse penetrated 24.0 mm. On the mid-slope, a heat pulse penetrated 18.2 mm and 16.8 mm for 45°C and 59°C, respectively. On the lower slope, a heat pulse penetrated less than 0.6 mm and temperatures never exceeded 45°C (Vose et al. 1999). In the areas of highest fire intensity, along the ridge, a stand-replacing fire consumed understory vegetation and ignited the crowns (Vose et al. 1999).

Experimental Design

Before the prescribed burn, 32 plots were established along seven parallel transects that ran from the top of the ridge to the stream (Elliott et al. 1999 a). In July 1994, twelve 15 m × 15 m plots were sampled and an additional twenty 10 m × 10 m plots were sampled in March 1995 before the burn. After the burn, plots were sampled again in July of 1995, July 1996 (Elliott et al. 1999a), and July 2005 (10 years post-burn). Plot locations along transects corresponded to three community types: mesic, near-stream cove (riparian); dry, mixed-oak (mid-slope); and xeric, pine-hardwood (ridge). In 2005, only 25 of the original 32 plots could be located and re-measured (n = 13 ridge plots; n = 6 slope plots; and n = 6 riparian plots). These 25 plots were used for the statistical analyses to compare pre-burn (1994) and early responses (1995 and 1996) to 10 years post-burn (2005) vegetation responses to prescribed fire.

As with many other large scale fire studies, this study was pseudoreplicated (van Mantgem et al. 2001). Therefore, interpretation is based on before, after, and long-term burn treatment effects and limited to this particular forest site. However, case studies of large scale events still provide valuable information as long as they are interpreted appropriately (Turner et al. 1997, van Mantgem et al. 2001).

Overstory and Understory Sampling

Vegetation was measured by layer: the overstory layer included all trees ≥5.0 cm diameter at breast height (dbh, 1.37 m above ground); the understory layer included all woody stems <5.0 cm dbh and ≥1.0 cm basal diameter; and the herb-layer included woody stems <1.0 cm basal diameter and all herbaceous species. Woody stems with <1.0 cm basal diameter were counted as seedlings regardless of the mode of reproduction (i.e., seedling or sprout origin).

Diameter of all overstory trees was measured and recorded by species in every plot. For the original plots, the understory layer was measured and recorded by species in the entire 15 m × 15 m plot, with the exception of mountain laurel and flame azalea (Rhododendron calendulaceum [Michaux] Torrey). These were measured in a 3.75 m × 3.75 m subplot in the southwest corner of each plot. For the additional plots, the understory layer (including mountain laurel, great laurel [Rhododendron maximum L.] and flame azalea) was measured in a 3.0 m × 3.0 m subplot located in the southwest corner of each plot (Elliott et al. 1999 a).

Herbaceous Layer Sampling

Only six ridge plots were sampled for herbaceous layer species before the burn in 1994 and re-sampled post-burn in 1995 and 1996 (Elliott et al. 1999 a), and again in 2005. Cover of herbaceous layer species was estimated visually by cover classes in six 1.0 m2 quadrats placed in the corners and at the midpoint of the east and west sides of each plot (a total of 36 quadrats). The seven cover classes used were: R (0 % to 0.5 %), 1 (0.5 % to 1 %), 2 (>1 % to 3 %), 3 (>3 % to 15 %), 4 (>15 % to 33 %), 5 (>33 % to 66 %), and 6 (>66 %). In the analyses, midpoint values of each cover class were used to compare pre-burn and post-burn effects.

Tree seedling abundance was estimated for the 25 plots sampled before and after the burns is 1995, 1996, and again in 2005 after the prescribed burn. Tree seedlings were counted in each 1.0 m2 quadrat of the original plots and in the 3.0 m × 3.0 m subplots of the additional plots. Tree species nomenclature follows Kirkman et al. (2007) and nomenclature for all other flora follows Gleason and Cronquist (1991).

Data Analyses

We used several indices—species richness (S), Shannon-Weiner’s index of diversity (H’), and Pielou’s (1966) evenness index (J’)—to evaluate the change in vegetation diversity from pre-burn 1994 to post-burn 2005. Shannon-Weiner’s index is a simple quantitative expression that incorporates both species richness and the evenness of species abundance (Magurran 2004), and was calculated based on stem density (stems ha−1) or basal area (m2 ha−1) of woody species, and percent cover of herbaceous species. Separate statistical analyses were performed for each vegetative layer (i.e., overstory, understory, and herbaceous layer). Because the permanent plots were sampled over time, we used a mixed linear model with repeated measures (PROC MIXED, SAS 2002–2003, Cary, North Carolina, USA) to determine significant vegetation differences between years. We used the unstructured covariance option in the repeated statement because it produced the lowest AIC value. If the overall F-tests were significant (P < 0.05), then least squares means (LS-means, Tukey-Kramer adjusted t-statistic) tests were used to determine significant differences between years (Littell et al. 1996).

Results

Overstory

On the ridge, 10 year post-fire mortality of pitch pine (Pinus rígida) (92.7 %) and hickory (Carya spp.) (77.5 %) significantly reduced overstory density and basal area (Table 1). Before the prescribed fire (1994), pitch pine, chestnut oak (Quercus montana Willdenow), hickory, and scarlet oak (Quercus coccinea Munch.) were the most abundant overstory species, accounting for 72 % of the density and 78 % of the basal area (Table 2). Ten years after the fire, chestnut oak, red maple, service-berry (Amelanchier arborea [Michaux f.] Fernald), and sourwood (Oxydendrum arboreum [L.] De Candolle) were the most abundant, accounting for 70 % of the density and 49 % of the basal area. In addition, H’basal area declined the first year after burning but no difference was detected between pre-burn and 2005.

Table 1 Average overstorya density, basal area, and diversity based on density (H’density) and basal area (H’basal area) before the prescribed burn (1994), and the first (1995) and tenth (2005) growing seasons after the prescribed burn for the three communities (ridge, mid-slope, and riparian) at Wine Spring Creek, western North Carolina.

On the mid-slope and riparian positions, overstory density and basal area were not significantly different ten years after the burn compared to pre-burn conditions (Table 1). Red maple, blackgum (Nyssa sylvatica Marshall), and hickory remained the most abundant species (Table 2), with fewer scarlet oak and chestnut oak (Table 2). No differences in H’density, or H’basal area were detected for the mid-slope or riparian communities between pre-burn and 10 years post-burn (Table 1).

Table 2 Overstory speciesa density (stems ha−1) and basal area (m2 ha−1) before the prescribed burn (1994), and the first (1995) and tenth (2005) growing seasons after the burn for the three communities (ridge, mid-slope, and riparian) at Wine Spring Creek, western North Carolina.

Understory

The fire affected the understory vegetation layer on the ridge much more than on the mid-slope and riparian positions. Even though density and basal area were reduced the first year after burning on the ridge, by 2005 density was significantly higher and basal area had returned to the pre-burn level (Table 3). Before the burn, understory density and basal area were high on the ridge and mid-slope with mountain laurel contributing 73 % and 66 % of the density on the ridge and mid-slope, respectively (Table 3). On the ridge, by 2005, mountain laurel and other shrubs exceeded their pre-burn density level and total density of woody stems was significantly higher than before the burn (Table 3). On the mid-slope, mountain laurel and other shrubs returned to their pre-burn density. Density of tree species also returned to their pre-burn level by 2005 (Table 3). On average, understory tree density was twice as high in 2005 as it had been before the burn; however, this increase was not highly significant (ridge; 1994 vs. 2005, t = −2.37, P = 0.0955). On the ridge, chestnut oak and scarlet oak density remained high through 2005, while red oak and black oak (Quercus velutina Lamarck) had not returned to the understory (Table 4). Red oak did recruit into the mid-slope community, however, with 741 seedlings ha−1 in 2005 (Table 4).

Table 3 Average understorya density, basal area, and diversity based on density (H’density) and basal area (H’basal area) and species richness (S) before the prescribed burn (1994), and the first (1995), second (1996), and tenth (2005) growing seasons after the prescribed burn for the three communities (ridge, mid-slope, and riparian) at Wine Spring Creek, western North Carolina.
Table 4 Understorya species density (stems ha−1) and basal area (m2 ha−1) before the prescribed burn (1994), and the first (1995), second (1996), and tenth (2005) growing seasons after the burn for the three communities (ridge, mid-slope, and riparian) at Wine Spring Creek, western North Carolina.

For the riparian community, density and basal area were not significantly different between pre-burn and post-burn (Table 3). We did not detect a significant change in any of the measures of diversity (i.e., S, H’density or H’basal area) over time (Table 3).

Tree Seedling Regeneration

On the ridge, total tree seedling (woody stems <1.0 cm basal diameter) density was not different between years (Figure 1). Nonetheless, the number of seedlings increased for some species, while others decreased. Red maple consistently recruited over time with nearly 4000 and more than 8000 seedlings ha−1 on the ridge and mid-slope, respectively (Figure 1). Scarlet oak, chestnut oak, and red oak seedlings recruited on the ridge the first and second growing seasons after the burn, but their recruitment diminished by 2005 (Figure 1). Pitch pine seedling numbers also increased on the ridge the first growing season after the burn; however, its numbers returned to the pre-burn level by 1996, and no new seedling recruitment was recorded in 2005 (Figure 1).

Figure 1
figure1

Tree seedling densities before the prescribed burn (1994) and the first (1995), second (1996), and tenth (2005) growing seasons after the burn: a) ridge, pine/hardwood community, b) mid-slope, mixed-oak community, and c) riparian, cove-hardwood community. Species codes: ACERUB = Acer rubrum; AMEARB = Amelanchier arborea; Carya = Carya spp.; HALCAR = Halesia carolina; OXYARB = Oxydendron arboreum; PRUSER = Prunus serotina; QUECOC= Quercus coccinea; QUEMON = Quercus montana; QUERUB = Quercus rubra; QUEVEL = Quercus velutina; ROBPSE = Robinia pseudoacacia; SASALB = Sassafras albidum; PINRIG = Pinus rigida. Species nomenclature and authorities follow Kirkman et al. (2007). Total number of seedlings have standard error bars with different letters to denote significant differences (P < 0.05) based on repeated measures analysis of variance (PROC MIXED 2002–2003), followed by a Tukey-Kramer adjusted t-test.

On the mid-slope and riparian, total number of tree seedlings significantly increased between 1994 and 2005. Red maple and service-berry contributed the largest number of seedlings to total recruitment in 2005, with more than 8000 seedlings ha−1 combined (Figure 1).

Herbaceous Layer

On the ridge, percent cover decreased the first summer after the burn, returned to pre-burn levels in the second year, and remained high through 2005 (Table 5). The H’cover increased the first growing season after the burn and remained high through 2005, whereas S per plot (number of species per 1.0 m2) increased the first growing season then returned to the pre-burn level. Number of species per site increased after the fire, and many more herbaceous species (SH) were present 10 years after the fire than before the burn (Table 5).

Table 5 Herb-layer cover, diversity (H’cover), and species richness (S) and average cover by growth form before the prescribed burn (1994), and the first (1995), second (1996), and tenth (2005) growing seasons after the prescribed burn for the ridge community at Wine Spring Creek, western North Carolina.

The percent cover of growth forms also changed after the burn. Percent cover of deciduous shrubs, such as blueberry, black huckleberry, flame azalea, and sweet pepperwood (Clethra acuminata Michaux) increased after the burn and remained higher than the pre-burn condition through 2005. Percent cover of graminoids increased by 1996, and then they were no longer significantly different than the pre-burn level by 2005 (Table 5). Evergreen shrubs, primarily mountain laurel, were initially reduced after burning, while deciduous shrubs and trees increased in percent cover (Table 5). Non-woody species (herbs, grasses, and vines) also increased. Before burning, non-woody species accounted for only 2.5 % of the cover; by 2005, non-woody species accounted for 11.8 % of the cover.

Discussion

Numerous researchers have advocated using prescribed fires to restore native pine or mixed pine-hardwood forests in the eastern US (Dey and Hartman 2005, Elliott and Vose 2005, Van Lear et al. 2005, Albrecht and McCarthy 2006, Boerner et al. 2006, McCarthy and Brown 2006, Mitchell et al. 2006, Andre et al. 2007, Lafon et al. 2007).

Altered pine-hardwood communities are common across the southern Appalachian region (Van Lear and Johnson 1983, Nicholas and White 1984, Smith 1991, Swift et al. 1993, Clinton et al. 1993), and the area of altered stands has increased since the last southern pine beetle epidemic (1998 to 2002) (Elliott and Vose 2005), which induced substantial pine mortality. Altered stands are characterized by heavy mortality of native yellow pines (pitch pine, Table Mountain pine [Pinus pungens Lambert], and shortleaf pine [Pinus echinata Miller]), often with additional oak mortality, and a dense understory layer of ericaceous shrubs (e.g., mountain laurel).

The rationale for this prescribed fire was to restore the pine-hardwood forest, and we hypothesized that fire would reduce mountain laurel and fire-intolerant hardwoods (e.g., red maple, blackgum, and sourwood), stimulate wildlife forage production (i.e., grasses, herbs, forbs, and berries), increase herbaceous layer diversity, and stimulate pine and oak regeneration along the hillslope gradient. Our earlier paper reported that overstory mortality was the heaviest on the ridge and was related to fire intensity (Elliott et al. 1999 a), with 31 % tree mortality the first summer and no additional overstory mortality the second year after the fire. This observation was consistent with wildfire effects in a pine-hardwood forest in West Virginia where overstory mortality was 20 % after the first year and 40 % after the second year (Groeschl et al. 1992). Even though we did not observe additional mortality the second year, by 10 years after fire on our study area, additional mortality occurred. Density was 54 % lower and basal area was 66 % lower than the pre-burn condition, and even lower than the first two years after the burn. This level of fire severity and concurrent tree mortality had a substantial impact on species composition and diversity.

On the ridge, overstory H’ decreased after the burn due to the decline in species richness (S) rather than a change in evenness (J’) of species distribution. Five species, Carolina silverbell (Halesia carolina L.), blackgum, white oak, red oak, and eastern hemlock (Tsuga canadensis [L.] Carriere), were no longer present in the overstory ten years after the burn. All were minor components of the ridge community before the burn. However, only white oak had seedlings and understory recruitment in 2005, suggesting that four of the five species may not regain their position in the overstory. For the riparian location, where fire severity was light (Vose et al. 1999), no changes in overstory density, basal area, or diversity were recorded.

Other studies have reported understory dominance by shade-tolerant red maple, which in the absence of fire eventually may replace oaks (Christensen 1977, Abrams 2005). In the southern Appalachians, an increase in abundance of red maple over the last two decades has been reported (Elliott et al. 1999 b), and the species has become dominant, occurring across a wide range of elevation and environmental conditions (Elliott and Swank 2008). In our study, red maple, a dominant species on the ridge before the burn, suffered heavier mortality than any other hardwood overstory species (Elliott et al. 1999 a), and it was also substantially reduced in the understory layer. However, by 2005, it had again recruited into the understory and overstory, and it continues to provide new seedlings across the hillslope. Conversely, chestnut oak and scarlet oak had less overstory mortality. Chestnut oak increased in importance and both oak species increased in density in the understory and herbaceous layer after the burn.

On the ridge, the increase in understory density and basal area of scarlet oak, chestnut oak, sourwood, black locust (Robinia pseudoacacia L.), and sassafras (Sassafras albidum [Nuttall] Nees) saplings after the burn corresponded to the substantial initial decrease in mountain laurel (Elliott et al. 1999 a). It is possible that the fire reduced the abundance of mountain laurel and red maple long enough for oaks to overtop the evergreen shrub and successfully recruit and grow into the overstory.

The mortality and regeneration of oak saplings varied with species and intensity of the burn across the hillslope. For example, white oak, black oak, and red oak saplings suffered heavy mortality, and they have not regained their numbers in the understory layer on the ridge where the fire was most intense. In contrast, scarlet oak and chestnut oak suffered heavy mortality in the overstory (Elliott et al. 1999 a). However, scarlet oak and chestnut oak seedling recruitment on the ridge was high in the first two years and, by the second year after the burn, understory density of these oaks was higher than before burning. Ten years after the prescribed fire, oak seedling numbers were low, but their numbers had more than doubled in the understory, suggesting that seedlings had successfully grown into this stratum.

The reduction of mountain laurel in the understory was sufficient to allow regeneration of oaks on the ridge and mid-slope, but the establishment of pitch pine was less successful. On our site, many mountain laurel clones survived the fire and these clones sprouted and doubled their numbers in the understory stratum ten years after the burn. Mountain laurel is a vigorous sprouter that produces many stems (McGinty 1972), but the growth of these stems is slower than that of many woody seedlings (Hooper 1969, McGee et al. 1995). Clinton et al. (1993) found that even after high intensity burning, mountain laurel reasserts its influence on microsite conditions at the forest floor within a few years and reduces the number of tree stems reaching the understory. However, the early reduction in mountain laurel abundance can allow successful establishment of native pines if pine seeds germinate, seedlings survive, and seedling growth is fast enough to overtop mountain laurel (Clinton et al. 1993). In our study, successful pine establishment was not the case due to low seedling survival (Elliott et al. 1999 a).

Our results indicate that regeneration and re-establishment of pitch pine may not occur at Wine Spring Creek without further management. In an earlier study on this burn site, Elliott et al. (1999 a) found high numbers of pine germinants the first growing season after the fire, followed by a significant decrease in pine seedlings in the second year. Ten years after the burn, we found no new pine seedlings, and pine saplings in the understory were fewer than before the prescribed fire. Elliott et al. (1999 a) attributed the poor pine seedling success to three factors: 1) residual overstory basal area was too high the first year after the burn for shade-intolerant pines to survive; 2) burning consumed little of the humus layer (Vose et al. 1999) and roots of pine germinants probably did not penetrate to mineral soil; and 3) precipitation in early fall was well below the long-term average. Thus, most of the new germinants of pitch pine were not able to survive through the first year and succeed into the understory.

On the ridge where fire was most intense (Vose et al. 1999), total herbaceous layer cover decreased the first summer after the burn, and then returned to pre-burn levels by 2005. Because mountain laurel cover was substantially reduced immediately after the fire, H’ increased with the recruitment of numerous herbaceous species. Ten years after the burn, deciduous shrubs and forbs continued to have higher cover than evergreen species (e.g., mountain laurel) in the herbaceous layer even though mountain laurel density had increased in the understory. Deciduous shrubs such as blueberry and black huckleberry, and grasses such as switchgrass (Panicum spp.) and little bluestem (Schizachyrium scoparius [Michaux] Nash), which increased in number after the fire, were still present even ten years later.

Several authors have found that the herbaceous layer tends to be more diverse after moderate- to high-intensity fire (Arthur et al. 1998, Clinton and Vose 2000, Hutchinson and Sutherland 2000, Clendenin and Ross 2001, Waldrop et al. 2008) partly due to removal of the litter layer, increased nutrient cycling rates, and increased light levels. In contrast, dormant season, low-intensity fire may have little to no effect on the herbaceous layer (McGee et al. 1995, Kuddes-Fischer and Arthur 2002, Franklin et al. 2003, Dolan and Parker 2004, Elliott and Vose 2005, Hutchinson et al. 2005).

Conclusions

Many studies in the eastern US have attributed community composition after a fire to the sprouting ability of dominant species, the failure of subordinate species to increase in numbers, and the failure of invasive species to persist (Abrahamson 1984, Schmalzer and Hinkle 1992, Matlack et al. 1993, McGee et al. 1995, Signell et al. 2005). In our study, all woody species sprouted, but increases in sprout densities varied among species. Oaks, hickory, black locust and sassafras, subordinate species in the understory before the burn, increased in numbers. Mountain laurel, the dominant species before the burn, initially decreased in the understory, but sprouted prolifically and returned to its pre-burn density and basal area levels ten years after the fire. We found that burning stimulated production of berries (black huckleberry, blackberry [Rubus spp.], and blueberry) and grasses, which are important sources of forage for wildlife, and other researchers have reported similar findings (Langdon 1981, Ducey et al. 1996, Keyser et al. 1996, Van Lear et al. 2004).

The effect of intense fire on oak regeneration has received less attention despite the fact that intense fires have produced the most dramatic results (Ward and Stephens 1989, Nowacki et al. 1992). We found that even ten years after a single event, oaks have increased their numbers in the understory, and the herbaceous layer is more diverse with a concomitant increase in non-woody growth forms.

The combination of high overstory mortality and low recruitment of pine species indicates that a single intense burn on the ridge location was not successful in restoring the pine component of this degraded pine-hardwood community. The longer term measurements were especially important in support of these observations because pitch pine regeneration was high (2381 seedlings ha−1 and 342 saplings ha−1) immediately after the burn and many overstory pines were still alive (425 trees ha−1) two years post-fire. Ten years after the burn, we found no new pine seedlings and fewer pine in the understory (82 saplings ha−1) and overstory (51 trees ha−1) than before the prescribed fire.

Other researchers have suggested that ridge-top pine systems, particularly Table Mountain pine, do not require high intensity (or stand replacement) fires to regenerate (Waldrop et al. 2003, Brose and Waldrop 2006). For example, Brose and Waldrop (2006) reported that ridge-top pine systems historically had frequent low intensity fires with episodic high intensity burns. Frequent, low intensity prescribed burns could reduce fire-sensitive species and slowly reduce highly flammable fuels (i.e., pine needles and twigs), while maintaining pine and oak in the overstory.

Literature Cited

  1. Abrahamson, W.G. 1984. Post-fire recovery of Florida Lake Wales Ridge vegetation. American Journal of Botany 71: 9–21.

    Article  Google Scholar 

  2. Abrams, M.D. 2005. Prescribing fire in eastern oak forests: is time running out? Northern Journal of Applied Forestry 22: 190–196.

    Google Scholar 

  3. Abrams, M.D., and G.J. Nowacki. 1992. Historical variation in fire, oak recruitment, and post-logging accelerated succession in central Pennsylvania. Bulletin of the Torrey Botanical Club 119: 19–28.

    Article  Google Scholar 

  4. Albrecht, M.A., and B.C. McCarthy. 2006. Effects of prescribed fire and thinning on tree recruitment patterns in central hardwood forests. Forest Ecology and Management 226: 88–103.

    Article  Google Scholar 

  5. Andre, J., M. Morales, and M. Anderson. 2007. Restoring the interior Ozark Highlands. Fire Management Today 67: 20–23.

    Google Scholar 

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

    Article  Google Scholar 

  7. Barden, L.S., and F.W. Woods. 1976. Effects of fire on pine and pine-hardwood forests in the southern Appalachians. Forest Science 22: 399–403.

    Google Scholar 

  8. Barden, L.S. 2000. Population maintenance of Pinus pungens Lam. (Table Mountain pine) after a century without fire. Natural Areas Journal 20: 227–233.

    Google Scholar 

  9. Blankenship, B.A., and M.A. Arthur. 2006. Stand structure over 9 years in burned and fire-excluded oak stands on the Cumberland Plateau, Kentucky. Forest Ecology and Management 225: 134–145.

    Article  Google Scholar 

  10. Boerner, R.E.J., T.A. Waldrop, and V.B. Shelburne. 2006. Wildfire mitigation strategies affect soil enzyme activity and soil organic carbon in loblolly pine (Pinus taeda) forests. Canadian Journal of Forest Research 26: 3148–3154.

    Article  Google Scholar 

  11. Brose, P.H., T. Schuler, D. Van Lear, and J. Berst. 2001. Bringing fire back, the changing regimes of the Appalachian mixed-oak forests. Journal of Forestry 99: 30–35.

    Google Scholar 

  12. Brose, P.H., and T.A. Waldrop. 2006. Fire and the origin of Table Mountain pine-pitch pine communities in the southern Appalachian Mountains, USA. Canadian Journal of Forest Research 36: 710–718.

    Article  Google Scholar 

  13. Buckner, E.R. 1989. Evolution of forest types in the southeast. Pages 27–33 in: T.A. Waldrop, editor. Proceedings of pine-hardwood mixtures: a symposium on management and ecology of the type. USDA Forest Service General Technical Report SE-58, Asheville, North Carolina, USA.

  14. Certini, G. 2005. Effects of fire on properties of forest soils: a review. Oecologia 143: 1–10.

    Article  Google Scholar 

  15. Christensen, N.L. 1977. Changes in structure, pattern and diversity associated with climax forest maturation in Piedmont, North Carolina. American Midland Naturalist 97: 176–188.

    Article  Google Scholar 

  16. Clark, J.S., and J. Robinson. 1993. Paleoecology of fire. Pages 193–214 in: P.J. Crutzen and J.G. Goldammer, editors. Fire in the environment: the ecological, atmospheric, and climatic importance of vegetation fires. John Wiley and Sons, New York, New York, USA.

    Google Scholar 

  17. Clendenin, M., and W. G. Ross. 2001. Effects of cool season prescribed fire on understory vegetation in a mixed pine hardwood forest of east Texas. Texas Journal of Science 53: 65–78.

    Google Scholar 

  18. Clinton, B.D., J.M. Vose, and W.T. Swank. 1993. Site preparation burning to improve southern Appalachian pine-hardwood stands: vegetation composition and diversity of 13-year-old stands. Canadian Journal of Forest Research 23: 2271–2277.

    Article  Google Scholar 

  19. Clinton, B.D., and J.M. Vose. 2000. Plant succession and community restoration following felling and burning in the southern Appalachians. Proceedings of the Tall Timbers Fire Ecology Conference 21: 22–29.

    Google Scholar 

  20. Crow, T.T. 1988. Reproductive mode and mechanisms for self-replacement of northern red oak (Quercus rubra)—a review. Forest Science 34: 19–40.

    Google Scholar 

  21. DeVivo, M.S. 1991. Indian use of fire and land clearance in the southern Appalachians. Pages 306–312 in: S.C. Nodvin and T.A. Waldrop, editors. Fire and the Environment: Ecological and Cultural Perspectives. USDA Forest Service General Technical Report SE-69, Asheville, North Carolina, USA.

  22. Dey, D.C., and G. Hartman. 2005. Returning fire to Ozark Highland forest ecosystems: effects on advance regeneration. Forest Ecology and Management 217: 37–53.

    Article  Google Scholar 

  23. Dolan, B.J., and G.R. Parker. 2004. Understory response to disturbance: an investigation of prescribed burning and understory removal treatments. Pages 285–291 in: M.A. Spetich, editor. Upland oak ecology symposium: history, current conditions, and sustainability. USDA Forest Service General Technical Report SRS-73, Asheville, North Carolina, USA.

  24. Ducey, M.J., W.K. Moser, and P.M.S. Ashton. 1996. Effect of fire intensity on understory composition and diversity in a Kalmia-dominated oak forest, New England, USA. Vegetation 123: 81–90.

    Article  Google Scholar 

  25. Dumas, S., H.S. Neufeld, and M.C. Fisk. 2007. Fire in a thermic oak-pine forest in Linville Gorge Wilderness Area, North Carolina: importance of the shrub layer to ecosystem response. Castanea 72: 92–104.

    Article  Google Scholar 

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

    Article  Google Scholar 

  27. Elliott, K.J., J.M. Vose, W.T. Swank, and P.V. Bolstad. 1999b. Long-term patterns in vegetation-site relationships in a Southern Appalachian forest. Journal of the Torrey Botanical Society 126: 320–334.

    Article  Google Scholar 

  28. Elliott, K.J., and J.M. Vose. 2005. Effects of understory prescribed burning on shortleaf pine (Pinus enchinata Mill.)/mixed hardwood forests. Journal of the Torrey Botanical Society 132: 236–251.

    Article  Google Scholar 

  29. Elliott, K.J., and W.T. Swank. 2008. Long-term changes in forest composition and diversity following early logging (1919–1923) and the decline of American chestnut (Castanea dentata (Marshall) Borkh). Plant Ecology 197: 155–172.

    Article  Google Scholar 

  30. Fei, S., and K.C. Steiner. 2007. Evidence for increasing red maple abundance in the eastern United States. Forest Science 53: 473–477.

    Google Scholar 

  31. Franklin, S.B., P.A. Robertson, and J.S. Fralish. 2003. Prescribed burning effects on upland Quercus forest structure and function. Forest Ecology and Management 184: 315–335.

    Article  Google Scholar 

  32. Galbraith, S.L., and W.H. Martin. 2005. Three decades of overstory and species change in a mixed mesophytic forest in eastern Kentucky. Castanea 70: 115–128.

    Article  Google Scholar 

  33. Gleason, H.A., and A. Cronquist. 1991. Manual of vascular plants of northeastern United States and adjacent Canada, second edition. The New York Botanical Garden, Bronx, New York, New York, USA.

    Book  Google Scholar 

  34. Groeschl, D.A., J.E. Johnson, and D.W. Smith. 1992. Early vegetative response to wild fire in a table mountain-pitch pine forest. International Journal of Wildland Fire 2: 177–184.

    Article  Google Scholar 

  35. Guldin, J.M., E. Poole, E. Heitsman, J. Kagrick, and R.M. Muzika. 2006. Ground truth assessments of forests affected by oak decline and red oak borer in the Interior Highlands of Arkansas, Oklahoma, and Missouri—preliminary results for overstory analysis. Pages 415–419 in: K.F. Connor, editor. Proceedings of the 13th Biennial Southern Silvicultural Research Conference. USDA Forest Service General Technical Report SRS-92, Asheville, North Carolina, USA.

  36. Harmon, M.E. 1982. Fire history of the westernmost portion of Great Smoky Mountains National Park. Bulletin of the Torrey Botanical Club 109: 74–79.

    Article  Google Scholar 

  37. Heitzman, E., A. Grell, M. Spetich, and D. Starkey. 2007. Changes in forest structure associated with oak decline in severely impacted areas of northern Arkansas. Southern Journal of Applied Forestry 31: 17–22.

    Google Scholar 

  38. Hoffman, C.H., and R.F. Anderson. 1945. Effect of southern pine beetle on timber losses and natural restocking. Journal of Forestry 43: 436–439.

    Google Scholar 

  39. Hooper, R.M. 1969. Prescribed burning for laurel and rhododendron control in the southern Appalachians. USDA Forest Service Research Note SE-116, Asheville, North Carolina, USA.

  40. Hutchinson, T.F., and S. Sutherland. 2000. Fire and understory vegetation: a large-scale study in Ohio and a search for general response patterns in central hardwood forests. Pages 64–74 in: D.A. Yaussy, compiler. Proceedings: Workshop on Fire, People, and the Central Hardwoods Landscape. USDA Forest Service General Technical Report NE-274, Durham, New Hampshire, USA.

  41. Hutchinson, T.F., B.E.J. Boerner, S. Sutherland, E.K. Sutherland, M. Ortt, and L.R. Iverson. 2005. Prescribed fire effects on the herbaceous layer of mixed-oak forests. Canadian Journal of Forest Research 35: 877–890.

    Article  Google Scholar 

  42. Johnson, P.S. 1985. Regenerating oaks in the lake states. Pages 98–109 in: J.E. Johnson, editor. Proceedings, Challenges in Oak Management and Utilization. Cooperative Extension Service, University of Wisconsin-Extension, Madison, USA.

    Google Scholar 

  43. Keyser, P.D., P. Brose, D. Van Lear, and K.M. Burtner. 1996. Enhancing oak regeneration with fire in shelterwood stands: preliminary trials. Transactions of the 61st North American Wildland and Natural Resource Conference: 215–219.

  44. Kirkman, L.K., C.L. Brown, and D.J. Leopold. 2007. Native trees of the southeast. Timber Press, Portland, Oregon, USA.

    Google Scholar 

  45. Kuddes-Fischer, L.M., and M.A. Arthur. 2002. Response of understory vegetation and tree regeneration to a single prescribed fire in oak-pine forests. Natural Areas Journal 22: 43–52.

    Google Scholar 

  46. Lafon, C.W., J.D. Waldron, D.M. Cairns, M.D. Tchakerian, R.N. Coulson, and K.D. Klepzig. 2007. Modeling the effects of fire on the long-term dynamics and restoration of yellow pine and oak forests in the southern Appalachian Mountains. Restoration Ecology 15: 400–411.

    Article  Google Scholar 

  47. Langdon, O.G. 1981. Some effects of prescribed fire on understory vegetation in loblolly pine stands. Pages 143–153 in: Proceedings, Prescribed Fire and Wildfire in Southern Forests. Clemson University, South Carolina, USA.

    Google Scholar 

  48. Lorimer, C.G. 1984. Development of the red maple understory in northeastern oak forests. Forest Science 30: 3–22.

    Google Scholar 

  49. Lorimer, C.G. 1985. The role of fire in perpetuation of oak forests. Pages 8–25 in: J.E. John, editor. Challenges in oak management and utilization. Cooperative Extension Service, University of Wisconsin, Madison, USA.

    Google Scholar 

  50. Magurran, A.E. 2004. Measuring biological diversity. Blackwells, Oxford, United Kingdom.

    Google Scholar 

  51. Matlack, G.R., D.J. Gibson, and R.E. Good. 1993. Regeneration of the shrub Gaylussacia baccata and associated species after low-intensity fire in an Atlantic coastal plain forest. American Journal of Botany 80: 158–173.

    Article  Google Scholar 

  52. McCarthy D.R., and K.J. Brown. 2006. Soil respiration response to topography, canopy cover, and prescribed burning in an oak-hickory forest in southeastern Ohio. Forest Ecology and Management 237: 94–102.

    Article  Google Scholar 

  53. McGee G.G., D.J. Leopold, and R.D. Nyland. 1995. Understory response to spring-time prescribed fire in two New York transition oak forests. Forest Ecology and Management 76: 149–168.

    Article  Google Scholar 

  54. McGinty, D.T. 1972. The ecological roles of Kalmia latifolia L. and Rhododendron maximum L. in the hardwood forest at Coweeta. Thesis, University of Georgia, Athens, USA.

    Google Scholar 

  55. Mitchell, R.J., J.K Hiers, J.J. O’Brien, S.B Jack, and R.T. Engstrom. 2006. Silviculture that sustains: the nexus between silviculture, frequent prescribed fire and conservation of biodiversity in longleaf pine forests of the southeastern United States. Canadian Journal of Forest Research 36: 2724–2736.

    Article  Google Scholar 

  56. Nicholas, N.S., and P.S. White. 1984. The effect of southern pine beetle on fuel loading in yellow pine forest of the Great Smoky Mountains National Park. US Department of the Interior National Park Service. Research/Resource Management Report SER-73, Atlanta, Georgia, USA.

    Google Scholar 

  57. Nowacki G.J., and M.D. Abrams. 1992. Community, edaphic, and historical analysis of mixed oak forests of the Ridge and Valley province in central Pennsylvania. Canadian Journal of Forest Research 22: 790–800.

    Article  Google Scholar 

  58. Oak, S.W., J.R. Steinman, D.A. Starkey, and E.K. Yockey. 2004. Assessing oak decline incidence and distribution in the southern US using forest inventory and analysis data. Pages 236–242 in: M.A. Spetich, editor. Upland Oak Ecology Symposium: History, Current Conditions, and Sustainability. USDA Forest Service General Technical Report SRS-73, Asheville, North Carolina, USA.

  59. Petersen, S.M., and P.B. Drewa. 2006. Did lightning-initiated growing season fires characterize oak-dominated ecosystems of southern Ohio? Journal of the Torrey Botanical Society 133: 217–224.

    Article  Google Scholar 

  60. Pielou, E.C. 1966. The measurement of diversity in different types of biological collections. Journal of Theoretical Biology 13: 131–144.

    Article  Google Scholar 

  61. Rentch, J.S., and R.R. Hicks. 2005. Changes in presettlement forest composition for five areas in the central hardwood forest. Natural Areas Journal 25: 228–238.

    Google Scholar 

  62. Schmalzer PA, and C.R. Hinkle. 1992. Recovery of oak-saw palmetto scrub after fire. Castanea 57: 158–173.

    Google Scholar 

  63. Signell, S.A., M.D. Abrams, J.C. Hovis, and S.W. Henry. 2005. Impact of multiple fires on stand structure and tree regeneration in central Appalachian oak forests. Forest Ecology and Management 218: 146–158.

    Article  Google Scholar 

  64. Smith, R.N. 1991. Species composition, stand structure, and woody detrital dynamics associated with pine mortality in the southern Appalachians. Thesis, University of Georgia, Athens, USA.

    Google Scholar 

  65. Stephenson, L.L., A.N. Ash, and D.F. Stauffer. 1993. Appalachian oak forests. Pages 305–338 in: W.H. Martin, S.G. Boyce, and A.C. Echternacht, editors. Biodiversity of the southeastern United States, upland terrestrial communities. John Wiley and Sons, New York, New York, USA.

    Google Scholar 

  66. Swank, W.T., S.G. McNulty, L.W. Swift, Jr. 1994. Opportunities for forest hydrology applications to ecosystem management. Pages 19–29 in: T. Ohta, Y. Fukushima, and M. Suzuki, editors. Proceedings of the International Symposium on Forest Hydrology. International Union of Forestry Research Organization, Tokyo, Japan.

    Google Scholar 

  67. Swift, L.W., K.J. Elliott, R.D. Ottmar, and R.E. Vihnanek. 1993. Site preparation burning to improve southern Appalachian pine-hardwood stands: fire characteristics and soil erosion, moisture, and temperature. Canadian Journal of Forest Research 23: 2242–2254.

    Article  Google Scholar 

  68. Thomas, D.J. 1996. Soil survey of Macon County, North Carolina. USDA Natural Resources Conservation Service, Washington, D.C., USA.

    Google Scholar 

  69. Turner, M.G., W.H. Romme, R.H. Gardner, and W.W. Hargrove. 1997. Effects of fire size and pattern on early succession in Yellowstone National Park. Ecological Monographs 67: 411–433.

    Article  Google Scholar 

  70. Van Mantgem, P., and W.M. Schwartz. 2001. Monitoring fire effects of managed burns and wildfire: coming to terms with pseudoreplication. Natural Areas Journal 21: 266–273.

    Google Scholar 

  71. Van Lear D.H., and V.J. Johnson. 1983. Effects of prescribed burning in the southern Appalachian and upper Piedmont forest: a review. Department of Forestry, Clemson University, Bulletin 36, Clemson, South Carolina, USA.

    Google Scholar 

  72. Van Lear, D.H., and T.A Waldrop. 1989. History, use, and effects of fire in the Appalachians. USDA Forest Service General Technical Report SE-54, Asheville, North Carolina, USA.

  73. Van Lear, D.H., and J.M. Watt. 1993. The role of fire in oak regeneration. Pages 66–78 in: D.L. Loftis and C.E. McGee, editors. Oak regeneration: serious problems practical recommendations. USDA Forest Service General Technical Report SE-84, Ashville, North Carolina, USA.

  74. Van Lear, D.H., K.R. Russell, D.E. Moorman, and D.B. Vandermast. 2004. Initial vegetation response to prescribed fire in some oak-hickory forests of the South Carolina Piedmont. Natural Areas Journal 24: 216–222.

    Google Scholar 

  75. Van Lear, D.H., W.D. Carroll, P.R. Kapeluck, and R. Johnson. 2005. History and restoration of the longleaf pine-grassland ecosystem: implications for species at risk. Forest Ecology and Management 211: 150–165.

    Article  Google Scholar 

  76. Vose, J.M., W.T. Swank, and B.D. Clinton. 1994. Fire, drought, and forest management influences on pine/hardwood ecosystems in the southern Appalachians. Pages 232–238 in: Proceedings of the 12th Conference on Fire and Forest Meteorology. Society of American Foresters, Bethesda, Maryland, USA.

    Google Scholar 

  77. Vose, J.M., W.T. Swank, B.D. Clinton, R.L. Hendrick, and A.E. Major. 1997. Using fire to restore pine/hardwood ecosystems in the southern Appalachians of North Carolina. Pages 149–154 in: Proceedings of Fire Effects on Rare and Endangered Species and Habitats. International Association of Wildland Fire, Fairfield, Washington, USA.

    Google Scholar 

  78. Vose, J.M., W.T. Swank, B.D. Clinton, J.D. Knoepp, and L.W. Swift, Jr. 1999. Using prescribed fire to restore southern Appalachian pine-hardwood ecosystems: effects on mass, carbon, and nutrients. Forest Ecology and Management 114: 215–226.

    Article  Google Scholar 

  79. Waldrop, T.A., and P.H. Brose. 1999. A comparison of fire intensity levels for stand replacement of Table Mountain pine (Pinus pungens Lamb.). Forest Ecology and Management 113: 155–166.

    Article  Google Scholar 

  80. Waldrop, T.A., N.T. Welch, P.H. Brose, K.J. Elliott, H.H. Mohr, E.A. Gray, and F.H Ellis. 2000. Current research on restoring ridgetop pine communities with stand replacement fire. Pages 103–109 in: D.A. Yaussey, editor. Proceedings: Workshop on Fire, People, and the Central Hardwood Landscape. US Department of Agriculture Forest Service General Technical Report NRS-274.

  81. Waldrop, T.A., P.H. Brose, N.T. Welch, H.H. Mohr, E.A. Gray, F.H. Tainter, and L.E. Ellis. 2003. Are crown fires necessary for Table Mountain pine? Pages 157–163 in: K.E.M. Galley, R.C. Klinger, and N.G Sugibara, editors. Fire Conference 2000: The First National Congress on Fire Ecology, Prevention, and Management. Miscellaneous Publication No. 13. Tall Timbers Research Station, Tallahassee, Florida, USA.

    Google Scholar 

  82. Waldrop, T.A., D. Yaussy, R.J. Phillips, T.A. Hutchinson, L. Brudnak, and R.A.J. Boerner. 2008. Fuel reduction treatments affect vegetation structure of hardwood forests in western North Carolina and southern Ohio, USA. Forest Ecology and Management 255: 3117–3129.

    Article  Google Scholar 

  83. Ward, J.S., and G.R. Stephens. 1989. Long-term effects of a 1932 surface fire on stand structure in a Connecticut mixed-hardwoods forest. Pages 267–273 in: G. Rink and C.A. Budelsky, editors. Proceedings of the 7th Central Hardwood Forest Conference. USDA General Technical Report NC-132, St. Paul, Minnesota, USA.

  84. Welch, N.T., T.A. Waldrop, and E.R. Buckner. 2000. Response of southern Appalachian Table Mountain pine (Pinus pungens) and pitch pine (P. rigida) stands to prescribed burning. Forest Ecology and Management 136: 185–197.

    Article  Google Scholar 

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Acknowledgements

The authors thank Patsy Clinton, Neal Muldoon, Duane Foster, Sonya Holland, and Tony Elkins for their assistance in field sampling. Drs. Tara Keyser and Charles Lafon and two anonymous reviewers provided valuable comments on this manuscript. This research was supported by USDA Forest Service, Southern Research Station, as a contribution to the Wine Spring Creek Ecosystem Management Project.

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Elliott, K.J., Vose, J.M. & Hendrick, R.L. Long-Term Effects of High Intensity Prescribed Fire on Vegetation Dynamics in the Wine Spring Creek Watershed, Western North Carolina, USA. fire ecol 5, 66–85 (2009). https://doi.org/10.4996/fireecology.0502066

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Keywords

  • Carya spp.
  • diversity
  • herbaceous flora
  • Kalmia latifolia
  • mortality
  • pine-oak heath
  • restoration
  • Pinus rigida
  • Quercus spp.