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Changes in vegetation structure and diversity after grass-to-forest succession in a southern Appalachian watershed.

INTRODUCTION

Disturbance and subsequent successional development are the keys to understanding the regulation of biological diversity on ecological time scales (Petraitis et al., 1989; Huston, 1994). As Peet (1981) and others (see Pickett and White, 1985, for review) have shown, unique events in the development of forest stands, particularly at the onset, can produce effects that last for decades. The rate of recovery from a disturbance depends in large part on the characteristics of the disturbance. If the disturbance is severe (such as long-term agriculture that eliminates saplings and the seed pool) and is conducted over a large area (which diminishes seed rain potential) the result can be a very protracted recovery time (Runkle, 1985). In addition, differences in species life histories (such as dispersal rates, growth rates, mode of reproduction, lifespan and growth form) may be responsible for many of the successional patterns observed in forest development (Grime, 1979; Pickett, 1982; Busing and Clebsch, 1983; Keever, 1983; Leps, 1987). Individuals growing after a disturbance can be present at the time of disturbance as suppressed seedlings and saplings, as seeds buried in the soil or as seeds newly dispersed into the area. The interaction of life histories and assimilative capabilities of species with the size, frequency and persistence of disturbance will determine community recovery and overall diversity pattern (Pickett and White, 1985; Roberts and Gilliam, 1995).

Previous studies in forest ecosystems have found conflicting patterns of diversity (see Halpern and Spies, 1995; Meier et al., 1995; and Roberts and Gilliam, 1995 for reviews). Plant diversity may decrease in late succession, as the largest and most shade-tolerant functional types dominate, as their high leaf area reduces light availability, and as shade-intolerant functional types become suppressed (Huston, 1994). Therefore, different strata of vegetation can have very different patterns of diversity over the course of succession - an important consideration in the temperate forests of the eastern United States, where natural disturbance and past land use practices led to a preponderance of secondary forests (Marquis and Johnson, 1989).

Numerous experiments in the Coweeta Basin demonstrate the resilience of Southern Appalachian forests after large-scale disturbance; these experiments evaluated the structural and functional aspects of ecosystem recovery by measuring streamflow, stream nutrient concentrations, nutrient export, leaf area and biomass, tree density and basal area (Waide, 1988). Other experiments on the effects of clear-cutting in the Southern Appalachians addressed the silvicultural and ecosystem aspects of early forest regeneration (McGee and Hooper, 1970, 1975; Trimble, 1973; Leopold and Parker, 1985; Leopold et al., 1985; Boring et al., 1988). In this study, we report successional changes in species composition and plant diversity in a Southern Appalachian mixed-deciduous forest after a severe disturbance regime. The study site was a watershed that had been subjected to clear-cutting, 5 yr of grass cover, 2 yr of herbiciding and regrowth of woody species for 28 yr. Although this set of disturbances was the most severe in the Coweeta Basin since research began there in 1934, this disturbance regime is similar to abandoned agriculture and pastures that are common throughout much of the Southern Appalachians. Although the grass was not cut or grazed, the lime and fertilizer amendments with attendant high productivity and nutrient uptake by fescue make these practices similar to agricultural practices. The original objective was to test the effects of different vegetation types on evapotranspiration and on the quantity and timing of streamflow (Hibbert, 1969; Swank et al., 1988; Butt and Swank, 1992). The objective of this new study was to document how community structure, and plant species richness and diversity recover from severe and large scale disturbance.

METHODS

Study area. - Watershed 6 (WS6), is a 9.0 ha NW-facing catchment located in the Coweeta Basin, southwestern North Carolina, Lat 35 [degrees] 03 [minutes] N, Long 83 [degrees] 25 [minutes] W. Elevation ranges from 700 to 900 m, mean slope is 50% and mean annual precipitation is ca. 1800 mm. Mean annual temperature is 12.6 C and average temperature ranges from 6.7 C in the dormant season to 18.5 C in the growing season (Swift et al., 1988). Parent rocks of schist and gneiss have weathered to form deep soils (Hatcher, 1988). Three soil types occur across the watershed. Along the riparian corridor and where slopes are 30-90% at higher elevations the soil type is the Trimont gravelly loam, a fine-loamy, mixed mesic Humic Hapludults; where slopes are 8-50% at lower elevations the soil type is Saunook gravelly loam, stony, a fine-loamy, mixed, mesic Humic Hapludults. The dominant ridge soils are Evard-Cowee gravelly loam, a fine-loamy, oxidic/mixed, mesic Typic Hapludults.

History of disturbance. - Before 1842, the Coweeta Basin was occupied by the Cherokee Indians who practiced semiannual burning to control understory shrubs and weeds and to expose nuts and other mast in the autumn for wildlife (Douglass and Hoover, 1988). Between 1842 and 1900, European settlers continued the practice of light semiannual burning and grazing. A small sawmill operated near WS6 in 1912, and the stand was heavily culled until 1923 (Douglass and Hoover, 1988). In the early 1920s chestnut blight [Endothia parasitica (Murr.) P.] was first noted in the Coweeta Basin. About 30% of the basal area in the watershed was in Castanea dentata trees most of which were infected with the chestnut blight fungus by 1930 (Woods and Shanks, 1959).

In 1941, all woody vegetation was cut in a 5-m width corridor (1.06-ha area) above the stream to determine how riparian vegetation affects streamflow (Dunford and Fletcher, 1947; Hursh, 1951). By 1958, 17 yr later, this 1.06-ha area had 6501 stems [ha.sup.-1] but basal area was only 4.32 [m.sup.2] [ha.sup.-1]. In contrast, the portion of the watershed that was not cut in 1941 (remaining 8.0-ha area) had an average density of 5735 stems [ha.sup.-1] and average basal area of 20.21 [m.sup.2] [ha.sup.-1] in 1958. Because the riparian corridor had been cut before the grass conversion experiment, it was not included in further vegetation analyses.

In 1958, the entire watershed was clear-cut, merchantable timber was removed, and the residue was piled and burned. In 1959, surface soil was scarified and planted to Kentucky-31 fescue grass (Festuca octiflora Walter). In 1960, the watershed was treated with a onetime application of 1100 kg [ha.sup.-1] lime, 110 kg [ha.sup.-1] 30-10-0 NPK and 18.4 kg [ha.sup.-1] granular 60% potash. Between 1960 and 1965, Kalmia latifolia, Rhododendron maximum, and other hardwood sprouts were suppressed with spot applications of 2,4-D[(2,4-dichlorophenoxy) acetic acid] to maintain the watershed in grass cover (Hibbert, 1969). In 1965, the watershed was fertilized again. In 1967, the grass was herbicided with atrazine [2-chloro-(4-ethylamino)-6-9-isopropylamino)-S-trizine], paraquat [1,1-dimethyl-4,4-bipyridinium ion (dichloride salt)], and 2,4-D[(2,4-dichlorophenoxy) acetic acid] (Douglass et al., 1969), and then left undisturbed. The objectives of the conversion were to compare water use of grass versus hardwoods (Hibbert, 1969; Swank et al., 1988) and to determine how conversion to grass affects discharge characteristics (Burt and Swank, 1992).

Overstory sampling. - In 1958, a pretreatment strip inventory sampled 25% of the area with 10-m width strips approximately 40-m apart extending along a N 35 [degrees] E transect from the ridge-top to the stream channel. This sampling method resulted in a total of 27 unequal sized plots (ranging from 0.02 to 0.14 ha), excluding the riparian corridor. All woody stems [greater than or equal to]2.54 cm dbh were measured by species and separated into 2.54-cm diam classes. Median values multiplied by number of individuals per diameter class were used to calculate basal area.

In 1982, 26 0.02-ha plots were permanently marked continuously along five transects on a N 45 [degrees] E compass bearing from ridge-top to near stream, excluding the riparian corridor; and woody stems, [greater than or equal to]2.54 cm dbh, were measured and tagged. In 1995, diameters of all woody stems, [greater than or equal to]2.54 cm dbh, were remeasured to the nearest 0.1 cm in the 26 plots.

Two adjacent 70-yr-old forests (WS14 and WS18) undisturbed since 1923, were selected as references for the developing forest conditions of the 1-yr-old field in 1968, 15-yr-old forest in 1982, and 28-yr-old forest in 1995 of WS6. These adjacent forests were sampled in 1993 with 13, 0.08-ha permanent sample plots with similar aspect and elevation as WS6.

Understory sampling. - Regeneration was quantified by measuring diameter at stem base for all woody stems [less than]2.54 cm dbh and [greater than]1.0 m height in two 3 x 5-m plots at opposite corners of each 0.02-ha plot. Ground flora was sampled in each of the summer months (June through September) of 1968. All aboveground live vegetation was clipped from 22 randomly located 1.0-[m.sup.2] plots in WS6. Samples were separated by species, dried at 105 C for [greater than]24 h, and weighed. Since samples collected in early September showed peak biomass for the season, we used the data collected in this sample month to compare with data from following years.

In mid-to-late August of 1982 and 1995, all herbaceous species and woody vegetation [less than or equal to]1.0 m height were clipped in two randomly located 1.0-[m.sup.2] subplots within each permanent 0.02-ha plot in WS6. In 1993, two 4.0-[m.sup.2] subplots within each 0.08-ha permanent plot were sampled for plant density by species in the reference plots (WS14 and WS18) (Sankovski, 1994). Plant species nomenclature follows Radford et al., 1968.

Data analyses. - We used several indices - species richness, Shannon-Weiner's index of diversity (H[prime]) and Pielou's (1966) evenness index (J[prime]) - to evaluate the change in diversity during succession on WS6 and the current condition of WS6 in comparison with the 70-yr-old reference forests. Shannon-Weiner's index is a simple quantitative expression that incorporates both species richness and the evenness of species abundance. Because H[prime] alone fails to show the degree that each factor contributes to diversity, we calculated a separate measure of species evenness (J[prime]). Species diversity was calculated as: H[prime] = -[Sigma][p.sub.i]ln[p.sub.i], where [p.sub.i] = proportion of total abundance of species i, with abundance of woody species = stem density (stems [ha.sup.-1]) or basal area ([m.sup.2] [ha.sup.-1] and abundance of herbaceous species = density (plants [m.sup.-2]) or biomass (g [m.sup.-2]). Species evenness was calculated as: J[prime] = H[prime]/[H[prime].sub.max], where [H[prime].sub.max] = maximum level of diversity possible within a given community = ln(S). We used pairwise t-tests (Magurran, 1988) to examine the differences in H[prime] between WS6 for sampling years 1958, 1982 and 1995 and the reference plots sampled in 1993.

RESULTS

Overstory. - Before conversion to grass in 1958, Kalmia latifolia, Rhododendron maximum, and Quercus prinus were the three most abundant woody species in WS6; when combined, they occupied 53.0% of the IV and 31.3% of the basal area (Table 1). Their high density gave K. latifolia and R. maximum the highest IVs; in contrast, their basal areas were low. The most abundant species in 1958, based only on basal area, were Q. prinus, Q. coccinea, Acer rubrum, Carya spp. and Pinus rigida. Quercus species (prinus, coccinea, rubra, alba, velutina) occupied 28.4% of the IV and 49.2% of the basal area. In 1982, 15 yr after cessation of management, Q. prinus and P. rigida were minor species, and Quercus species abundance had declined dramatically to 1.3% of the IV and 1.0% of the basal area (Table 1). In 1995, Quercus species were 1.2% of the IV and 1.5% of the basal area. Although Q. coccinea ranked fourth in basal area (15.0% of total basal area) before conversion to grass, by 1982 it had disappeared from the overstory; whereas, Robinia pseudoacacia and Liriodendron tulipifera combined accounted for 71.6% of the IV and 83.9% of the basal area. By 1995 (28-yr-old forest), these two species accounted for 50.8% of the IV and 73.7% of the basal area. In 1958, Liriodendron tulipifera accounted for [less than]0.5% of the IV, but by 1982 (15 yr after cessation of management) its IV and frequency of occurrence was much higher. Acer rubrum increased in IV from 1982 to 1995; in 1995, its density was twofold higher and basal area was sixfold higher and it had exceeded the preconversion level of density and basal area.

From 1982 to 1995 in WS6, average mortality for all tree stems was 35.3% and average ingrowth was 33.6%. Robinia pseudoacacia average mortality was 72.7% with no ingrowth over the 13-yr period, Liriodendron tulipifera had 15.3% mortality and 19% ingrowth, and Acer rubrum had 17% mortality and 54.7% ingrowth (via recruitment into additional plots).

In the reference forests, Quercus species constituted 19.8% of the IV and 29.5% of the basal area. Quercus prinus had the highest relative basal area and ranked third in IV value in the reference plots (Table 1), compared to [less than]1.0% of the basal area and a ranking of 14 in IV for WS6. Quercus coccinea had disappeared from the overstory of WS6, yet it accounted for 7.3% of the basal area and was ranked eighth in IV in the reference plots. In the reference plots, Kalmia latifolia was the most important species with high relative density [TABULAR DATA FOR TABLE 1 OMITTED] producing a high IV (Table 1). In contrast, in WS6, 28 yr after the cessation of management, K. latifolia was ranked 13th based on relative basal area, and it tied for the 15th position with four other species based on frequency (Table 1).

The reference plots had significantly higher density-based H[prime] and basal area-based H[prime] than WS6 in any year ([ILLUSTRATION FOR FIGURE 1A OMITTED] and Table 2). However, density-based J[prime] was comparable [TABULAR DATA FOR TABLE 2 OMITTED] among time periods [ILLUSTRATION FOR FIGURE 1A OMITTED]. In WS6, density-based H[prime] was significantly higher in 1982 and 1995 than in 1958. However, basal area-based H[prime] significantly declined from 1958 to 1982, and then significantly increased in 1995 ([ILLUSTRATION FOR FIGURE 1B OMITTED] and Table 2).

Understory. - In 1995, increased regeneration was limited to only a few tree species in the understory of WS6. The most abundant saplings were Acer rubrum and Symplocos tinctoria. Liriodendron tulipifera and Quercus spp. saplings were rare. Pyrularia pubera and Kalmia latifolia were the most abundant shrubs in the [greater than]1.0 m height stratum. In the ground flora plots ([less than or equal to]1.0 m height), the average number of shrubs was 21,340 stems [ha.sup.-1], and the average number of trees was 11,150 seedlings [ha.sup.-1]. The most abundant shrubs were Rubus alleghaniensis with 11,530 stems [ha.sup.-1] and Gaylussacia ursina with 8080 stems [ha.sup.-1]. Acer rubrum was the most abundant tree species with 5000 seedlings [ha.sup.-1]; L. tulipifera and Prunus serotina each had 960 seedlings [ha.sup.-1], and Quercus rubra and Quercus coccinea combined had 960 seedlings [ha.sup.-1].

The ground flora subplots of the reference plots had 68,540 stems [ha.sup.-1] of shrubs and 16,680 seedlings [ha.sup.-1] of trees. Gaylussacia ursina was the most abundant shrub with 59,740 stems [ha.sup.-1]. The most abundant tree seedlings were Acer rubrum, Quercus rubra, and Liriodendron tulipifera with 8880, 3030 and 1120 seedlings [ha.sup.-1], respectively. All the Quercus species combined (rubra, prinus, velutina and coccinea) had 4150 seedlings [ha.sup.-1], fourfold higher than the 28-yr-old forest of WS6.

In the 1982 ground flora inventory, not all plants were identified to species - a category designated as "others" contained 1.02% of the total biomass, and plants of Solidago, Eupatorium and Aster were not identified to species. Thus, the low number of species present in 1982 may be attributed to the lumping of rare species rather than to a true decline (Table 3).

In 1968, WS6 had only 23 species with four (Erechtites hieracifolia, Phytolacca americana, Equisetum arvensis and Fescue octiflora) accounting for 92.3% of the biomass. Of these, only E octiflora remained in 1982, but it had decreased in frequency and relative biomass (Table 3), and by 1995, it was lower in biomass. Erechtites hieracifolia and Erigeron canadensis reappeared as minor species in 1995 with only 0.20% of the biomass. based on relative biomass, the ranking of ground flora species in 1995 was Eupatorium spp., Polystichum acrostichoides and Smilax spp. (Table 3). Other species that occurred frequently in relatively high biomass in 1995, but were not identified in 1968, were Rubus alleghaniensis, Dennstaedtia punctilobula and Clematis virginiana.

Unlike WS6, in the reference plots, Gaylussacia ursina, Acer rubrum, Galax aphylla and Thelypteris noveboracensis were the four most abundant species based on relative density (Table 4). [TABULAR DATA FOR TABLE 3 OMITTED] In WS6, Eupatorium spp. occurred in all 26 sample plots, and Polystichum acrostichoides and Rubus alleghaniensis occurred in 20 of the plots. Taxa that were similar between the reference watersheds and WS6 were Dioscorea villosa, Arisaema triphyllum, T. noveboracensis, Dennstaedtia punctilobula, Houstonia purpurea, Smilacina racemosa and Galium latifolia. WS6 had fewer species than the reference plots but average density was 3.6 times greater (Table 4).

DISCUSSION

Distribution of woody species. - The canopy of the 28-yr-old WS6 forest differed from that of the reference watersheds. Species richness was slightly lower, and basal area-based H[prime] was significantly lower. We attributed the initial decline in basal area-based H[prime] to the evenness of species distribution (J[prime]) - which declined from 1958 to 1982, and the subsequent increase to the corresponding increase in J[prime]. Thus, the changes in overstory diversity among years was driven by changes in dominance rather than changes in the number of overstory species. The reference forests had a large component of Quercus species and Tsuga canadensis along with Liriodendron tulipifera. In WS6, Quercus species were a minor component, T. canadensis was absent, and Robinia pseudoacacia and L. tulipifera were the dominant species in the first 28 yr of succession. Clebsch and Busing (1989) found that R. pseudoacacia and L. tulipifera dominated a 15-yr-old cove forest after abandonment from agriculture, but that R. pseudoacacia disappeared by the 42nd yr of development. Clebsch and Busing (1989) also compared an old-growth stand to an adjacent abandoned agricultural field that was dominated by L. tulipifera at age 48. They found that species richness peaked during midsuccession ([approximately equal to]50 yr). Density-based H[prime] was highest in the 48-yr-old stand, whereas biomass-based [TABULAR DATA FOR TABLE 4 OMITTED] H[prime] was highest in the old-growth stand. In our study, R. pseudoacacia declined in abundance from 1982 to 1995, but was still the dominant species 28 yr after cessation of management; whereas, L. tulipifera increased in abundance.

Using data from the Coweeta Basin, we compared the results from WS6 with two watersheds that had different patterns of cutting and succession: a treated S-facing watershed, which had a single clear-cut harvest followed by 17 yr of succession (Elliott et al., 1997); and an NE-facing watershed, which had two clear-cuts separated by 23 yr of unimpeded growth (Elliott and Swank, 1994). In the 17-yr-old once-clear-cut forest, relative basal area of Robinia pseudoacacia was 9.5% for cove-hardwoods, 21.3% for mixed-oak hardwoods, and 3.4% for hardwood-pine communities (Elliott et al., 1997). In WS6, relative basal area of R. pseudoacacia was 65.4% for the 15-yr-old forest and 25.7% for the 28-yr-old forest. In addition, Acer rubrum, a ubiquitous component of

Southern Appalachian forests that was abundant in WS6 before conversion to grass, regained its position in the canopy after cessation of management, and remained important in the 28-yr-old forest. In the once-clear-cut watershed, basal area-based H[prime] ranged from 1.76 to 2.57 depending on community type after 17 yr of forest development, whereas in WS6 basal area-based H[prime] was 1.30 after 15 yr, and only 1.75 after 28 yr of forest development. The twice-clear-cut watershed had higher diversity than WS6. Basal area-based H[prime] ranged from 2.31 to 2.61 in the 8 to 23 yr following the first clear-cut, and from 2.55 to 2.06 in the 7 to 29 yr following the second clear-cut (Elliott and Swank, 1994).

The recovery of WS6 following large-scale, severe disturbance, results partly from the life history traits of the species that colonized the watershed. A major difference between WS6 and the other nearby clear-cut watersheds in the Coweeta Basin is in the species mechanisms for sexual and vegetative reproduction. Both the once- and twice-clear-cut watersheds were allowed to regrow immediately after clear-cutting, making sprouting from cut stumps the primary mode of reproduction. However, in WS6 vegetative reproduction was only apparent for Robinia pseudoacacia. To keep the watershed in grass cover for 5 yr, stump sprouting was eliminated, and woody species were spot-herbicided. Following cessation of management, regeneration could only come from seeds that had survived in the soil for many years, from small, wind-dispersed seeds such as the winged-samaras of Liriodendron tulipifera and Acer rubrum, or species that could sprout from extensive, persistent root systems (for species like R. pseudoacacia). Large seeded species such as Quercus rubra and Q. coccinea were regenerating, but were in low numbers; and some species, including Q. prinus and Q. velutina had disappeared from the understory.

Following cessation of management, Robinia pseudoacacia quickly sprouted from roots to outperform other species for several years, similar to patterns that have been documented throughout the Southern Appalachians (Beck and McGee, 1974; McGee and Hooper, 1970, 1975; Clebsch and Busing, 1989). The dense stands eventually decrease in vigor, succumb to locust stem borers (Megacyllene robiniae), and decline (Hoffard and Anderson, 1982) leaving N-enriched soil and organic matter for exploitation by other species (Boring and Swank, 1984a). Robinia pseudoacacia is a dominant Southern Appalachian successional tree that symbiotically fixes N, grows rapidly and has a relatively short lifespan (Boring and Swank, 1984b). Although R. pseudoacacia regenerated quickly following cessation of management, it began to experience heavy stem borer mortality in 1979; by 1982, 21% of the R. pseudoacacia trees were dead, 18% were severely injured, and many of the remaining trees showed evidence of canopy decline. Since 1982, there has been no ingrowth and it is not found in the shrub stratum.

Liriodendron tulipifera increases in density following clear-cutting due to its prolific seedling establishment (Trimble, 1973). It is a rapidly growing, shade-intolerant, early successional species often found in pure stands on abandoned fields. Yet the species is long-lived, can achieve diameters in excess of 2 m, and can occupy sites for hundreds of years (Buckner and McCracken, 1978). Apsley (1987) demonstrated that Robinia pseudoacacia enhanced the growth of L. tulipifera in a 10-yr-old stand in the Coweeta Basin, presumably by substantively increasing nitrogen availability (Boring and Swank, 1984a). Other researchers report a large pulse in R. pseudoacacia mortality approximately 10-20 yr following clear-cutting (Della-Bianca, 1983; Leopold et al., 1985; Elliott et al., 1997). For these reasons, we predict that L. tulipifera will maintain its canopy dominance in WS6, whereas R. pseudoacacia will continue to decline in the absence of any further large-scale disturbance.

Understory. - Because of its heterogeneity of resources, the understory is typically the most diverse stratum in mature eastern deciduous forests (Huebner et al., 1995). Richness of the ground flora was much higher in the 28-yr-old forest than the 1-yr-old field of WS6. Much of this richness came from woody species colonizing the watershed. There were only four woody species in the sample plots in 1968 and five in 1982; however, that number had increased to 22 (nine shrubs, 13 trees) by 1995.

Recovery rates of woody species richness and cover were much faster in WS6 than in other studies of old-field abandonment (Myster and Pickett, 1990; Myster and Pickett, 1994; Inouye and Tilman, 1995), yet slower than in experimental clear-cut watersheds (Boring et al., 1981; Reiners, 1992). Inouye and Tilman (1995) found that species richness increases with field age and soil nitrogen, but woody species contributed [less than]15% cover even in the oldest fields (56-yr-old). In our study, woody species contributed [less than]3.0% to the total aboveground biomass in the 1st yr after cessation of management, 67.8% by the 3rd yr, and [greater than]99.0% in 1982 and 1995. In 1995 (28-yr since cessation of management), woody species contributed 6.6% of the density, 10.5% of the cover, and 15.6% of the biomass in the ground flora stratum alone. The rate of woody species recovery following disturbance depends largely on the previous land use practices, such as the number of years under agricultural practice and the extent of nutrient amendments. In WS6, the grass cover remained for only 5 yr, there was no grass utilization, and the site received large additions of lime and fertilizer. Nevertheless, woody species recovery was slower than that of a clear-cut and herbicided northern hardwood forest at Hubbard Brook (Reiners, 1992), where woody species contributed 53.6% of the aboveground biomass in the 1st yr following recovery and 86.7% by the 3rd yr. Although there are differences in climate, soils and vegetation composition between the Hubbard Brook watershed and Coweeta Basin's WS6, a major factor influencing the rate of recovery of woody species in WS6 was the impact of planting, herbiciding of woody species and maintaining grass cover for 5 yr.

Diversity may remain low even decades after logging because herbaceous plants of late-successional or mature forests colonize slowly, with some species needing a decade or more from seed to first flowering (Bierzychudek, 1982). In WS6, clear-cutting, 5 yr of grass cover, followed by herbiciding, increased the abundance of genera - such as Erechtites, Phytolacca and Erigeron, as well as early successional woody species - that tolerate open habitats. In contrast, shade-tolerant understory ferns and herbs such as Polysticum acrostichoides, Dennstaedtia punctilobula, Galium latifolium and Viola cucullata have only become more abundant as the forest matured.

Large-scale, severe disturbance decreased plant diversity and dramatically altered community structure in a small Southern Appalachian watershed. Although recovery of woody species richness and cover was faster than in other studies following old-field abandonment, it was slower than in experimental clear-cut watersheds. Twenty-eight yr since cessation of management, overstory diversity has begun to increase and shade-tolerant ferns and herbs are becoming more abundant. To address long-term effects, we need to know how species responses vary with changes in stand development, life-history characteristics, and disturbance severity and spatial scale. Comparative studies in different ecosystem types would provide insights into the relative importance of processes that influence diversity. These studies would help clarify the patterns and mechanisms that different ecosystems have in common as well as those that are unique.

Acknowledgments. - We thank Anthony Elkins and Sonya Holland for their assistance in field sampling. Dr. Paul Bolstad provided useful suggestions on this manuscript. This research was mainly supported by U.S. Forest Service, Southern Research Station and partly by the National Science Foundation's Long-Term Ecological Research Program.

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Author:Elliott, Katherine J.; Boring, Lindsay R.; Swank, Wayne T.
Publication:The American Midland Naturalist
Date:Oct 1, 1998
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