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International Journal of Forestry Research
Volume 2014 (2014), Article ID 179415, 11 pages
Developing a Topographic Model to Predict the Northern Hardwood Forest Type within Carolina Northern Flying Squirrel (Glaucomys sabrinus coloratus) Recovery Areas of the Southern Appalachians
1Department of Geography, Texas A&M University, College Station, TX 77840, USA
2Geospatial and Environmental Analysis Program, Virginia Polytechnic Institute and State University, Blacksburg, VA 24061, USA
3Department of Geography, Virginia Polytechnic Institute and State University, Blacksburg, VA 24060, USA
4Department of Fish and Wildlife Conservation, Virginia Cooperative Fish and Wildlife Research Unit, U.S. Geological Survey, Blacksburg, VA 24061, USA
5Department of Forest Resources and Environmental Conservation, Virginia Polytechnic Institute and State University, Blacksburg, VA 24061, USA
Received 12 May 2014; Revised 14 July 2014; Accepted 18 July 2014; Published 28 August 2014
Academic Editor: Piermaria Corona
Copyright © 2014 Andrew Evans et al. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.
The northern hardwood forest type is an important habitat component for the endangered Carolina northern flying squirrel (CNFS; Glaucomys sabrinus coloratus) for den sites and corridor habitats between boreo-montane conifer patches foraging areas. Our study related terrain data to presence of northern hardwood forest type in the recovery areas of CNFS in the southern Appalachian Mountains of western North Carolina, eastern Tennessee, and southwestern Virginia. We recorded overstory species composition and terrain variables at 338 points, to construct a robust, spatially predictive model. Terrain variables analyzed included elevation, aspect, slope gradient, site curvature, and topographic exposure. We used an information-theoretic approach to assess seven models based on associations noted in existing literature as well as an inclusive global model. Our results indicate that, on a regional scale, elevation, aspect, and topographic exposure index (TEI) are significant predictors of the presence of the northern hardwood forest type in the southern Appalachians. Our elevation + TEI model was the best approximating model (the lowest AICc score) for predicting northern hardwood forest type correctly classifying approximately 78% of our sample points. We then used these data to create region-wide predictive maps of the distribution of the northern hardwood forest type within CNFS recovery areas.
1.1. Environmental Setting
The Blue Ridge portion of the southern Appalachians, extending from northern Georgia to central Virginia , has been labeled a “biodiversity hotspot” due to its assemblage of unique ecosystems and number of imperiled species that occur therein [2, 3]. Natural and anthropogenic disturbance history has significantly altered the landscape and continues to impact the habitat of endemic species such as the endangered Carolina Northern flying squirrel (CNFS, Glaucomys sabrinus coloratus), a Pleistocene relict that uses the montane northern hardwood and red spruce (Picea rubens)-Fraser fir (Abies fraseri) forests for denning sites and foraging areas [4–6].
In the southern Appalachians, high elevation forest communities above 1200 m have been subjected to varying degrees of disturbance over the last 200 years. Disturbance to these areas began with Native Americans and early European pioneers clearing land for high-elevation pasture and then large-scale timber harvesting to exploit vast forest resources during the industrial logging period around the turn of the 20th century [5, 7]. The extent and type of harvests during this time were important determinants for shaping the present high-elevation forests. In mid- to high-elevations, wildfires or intentional burning following logging of northern hardwoods favored regeneration of helophytic tree species, such as oak (Quercus spp.), particularly, northern red oak (Quercus rubra) . Conversely, in disturbed areas where red spruce-Fraser fir were cut and burned, stump sprouting and wind dispersed seeds allowed northern hardwood species to regenerate, thereby increasing the acreage of mixed northern hardwood-red spruce stands in formerly pure conifer forests . Currently, some high elevation oak stands appear to be in a transition state, moving back towards a northern hardwood forest dominated by mesic species such as maples (Acer spp.) and yellow birch (Betula alleghaniensis). This transition is occurring in a gap-phase disturbance-response condition, in the absence of fire that might otherwise favor establishment and release of oak advance regeneration. More recent perturbations include the introduction of the balsam woody adelgid (Adelges piceae), causing significant mortality of Fraser fir at the upper elevation limits of northern hardwood distribution, and the beech bark disease on American beech (Fagus grandifolia) throughout [1, 9]. Loss of mature Fraser fir and American beech can lead to the formation of forest canopy gaps that allows the woody shrubs such as blackberry (Rubus spp.) to capture the site, keeping successional processes arrested . Additionally, the southern Appalachians are known to be an area of high atmospheric acid deposition and impacts on high elevation forest health have been posited by some researchers [11–13].
Two sciurid species, the endangered CNFS and the common southern flying squirrel (SFS; Glaucomys volans), have been impacted by these past and ongoing forest changes. Both species den in cavities commonly found in older, mature deciduous trees. All CNFS are limited to isolated high-elevation areas along the Appalachian crest in western North Carolina, eastern Tennessee, and southwestern Virginia, where nine “populations” are believed to exist [4, 14, 15]. Previous studies of CNFS have indicated that red spruce-Fraser fir forests serve as foraging areas attributed in part to the presumed higher abundance of mycorrhizal fungi that make up a significant portion of CNFS diet and serve as drey (twig or leaf nest) sites on a limited basis [4, 16–18]. The northern hardwood species of these second growth forests, most commonly yellow birch (Betula alleghaniensis) or American beech (Fagus grandifolia), provide nesting sites for CNFS in the form of large hollows and cavities as well as food cache sites, latrines, and natal sites [4, 19, 20]. Weigl  and Meyer et al.  found that these sites also provide substantial ground cover and closed canopies that provide a degree of protection from predators as well as quantities of wet, decaying wood that support the truffles, lichens, and beech nuts that make up a large portion of CNFS diet. Additionally, northern hardwoods can be relatively poor habitat for the competing southern flying squirrel and can serve has habitat corridors linking red spruce-Fraser fir patches that may constitute the preferred foraging habitat .
However, northern hardwoods, particularly those in close proximity to oak stands with hard mast production, provide the SFS a high-energy food source. This food source has allowed the more austral SFS to overcome an otherwise thermally difficult environment and increase in abundance and local distribution at high elevations. Despite their smaller size, SFS are more aggressive than CNFS in den-site competition when the two species are synoptic, often displacing CNFS locally [5, 19, 22–24]. Moreover, SFS are chronic hosts of an intestinal nematode (Strongyloides robustus) that is often lethal to CNFS and that may have contributed further to CNFS reductions [6, 19, 25–27]. Northern hardwoods with substantial ground cover, large amounts of coarse woody debris, lichens, and closed canopies can provide some suitable foraging habitat for CNFS [6, 21] or serve as habitat corridors, particularly in close proximity to mixed or completely conifer-dominated stands [5, 28]. Additionally, in the absence of oak, northern hardwoods can be relatively poor habitat for SFS . As a requirement for CNFS recovery, an improved understanding of the distribution of northern hardwoods within designated CNFS recovery areas (Figure 1) is necessary for habitat delineation and identification of possible habitat management strategies to enhance and increase existing CNFS populations and local distributions .
1.2. Predictive Habitat Modeling
Mapping the distribution of deciduous forest types over large areas and in complex terrain is an important yet challenging task. Data from extensive vegetation inventories such as the US Forest Service Forest Inventory and Analysis program  and Carolina Vegetation Survey  are generally too coarse for accurate delineation of forest or habitat types at a management scale. Land cover mapping from aerial photography and satellite imagery can sufficiently discriminate between coniferous and deciduous forest cover but have generally not been an effective approach in distinguishing among the many deciduous forest types that dominate most southern Appalachian landscapes (e.g., discerning oak-dominated systems from northern hardwoods). Since extensive field sampling within each recovery area for the presence of CNFS is not possible, predictive models based on relationships between biophysical gradients and species distributions may provide an effective and needed approach for this management concern [31, 32].
In forested mountain landscapes, where topography controls or influences many biophysical characteristics, such as microclimate, incident solar radiation, soil moisture, and organic matter accumulation, modeling terrain attributes within a geographic information system (GIS) can be effective for delineating vegetation community patterns [1, 33–35]. Topographic characteristics that are often directly correlated with environmental gradients of interest can be accurately and efficiently modeled for large geographic areas using widely available digital elevation data and spatial analysis software . Nonetheless, previous studies using GIS-based terrain analysis to predict ecological types in the southern Appalachians have been relatively limited in geographic scope [7, 15, 36]. Simon et al.  used topographic variables in addition to geological and soil fertility data as a first approximation to classify ecological zones of the southern Appalachians with GIS outputs achieving 81 and 85 percent accuracy for the northern hardwood forest type in their northern and southern zones. However, the lack of distinction between predicted northern hardwood forests and high-elevation oak forests limits management utility. Furthermore, a more precise model of the northern red oak forest types, northern hardwood forests, and their ecotone would allow forest managers to more appropriately use prescribed burning to accomplish burning goals to favor oak where it is biologically appropriate without harming fire-sensitive northern hardwood or red spruce-Fraser fir regeneration. Lastly, a predictive model would provide a baseline condition for predicting the impact of climate change in the southern Appalachians to high elevation forest types such as northern hardwoods that are presumed to be a risk for decline.
The objectives of our study were to define the northern hardwood forest type in western North Carolina, adjacent portions of eastern Tennessee, and southwestern Virginia and to determine if the geographic distribution of northern hardwood forest types can be accurately determined from digital terrain modeling in and adjacent to CNFS recovery areas. To meet the objectives, we used a decision tree approach for initial classification based on similar stand composition and species abundance within those stands as used in previous studies [1, 33, 37]. We examined presence or absence of northern hardwoods at high elevations in the region using an information-theoretic approach . We hypothesized, based on previous studies, that elevation, aspect, slope, curvature, and an index of topographic exposure would contribute to the predictive model [7, 34, 39–41].
2.1. Study Areas
During the summer of 2012 and January 2013, we sampled vegetation and terrain characteristics at 338 points over 113 three-point belt transects across 11 study areas in western North Carolina, adjacent portions of eastern Tennessee, and southwestern Virginia within the Blue Ridge physiographic province (Figure 1). Nine sites were within North Carolina and/or portions of Tennessee along the crest of the southern Appalachians or in the Grayson Highlands area of southwestern Virginia that contained known populations of CNFS [6, 16, 42]. Additionally, we sampled two, more disjunct high-elevation areas in North Carolina with northern hardwood forests where CNFS have not been documented—the Standing Indian and Wayah Bald massifs. All sample points fell within the Blue Ridge Parkway National Park (BRPNP), Pisgah, Nantahala, Cherokee, or Jefferson national forests or on lands owned by the Eastern Band of Cherokee Indians. On average, these areas receive in excess of 200 centimeters of precipitation annually, distributed relatively evenly throughout the year (often occurring as snow and ice during the winter months). Temperatures are widely variable throughout the year due to the effects of elevation and aspect, with means of approximately 2.2°C in January and approximately 23°C in July [1, 33, 43]. Typically, the first frost occurs in early October and the last frost in early May, with 130 frost-free days on average (NOAA, National Climatic Data, 2012, http://www.ncdc.noaa.gov/cdo-web/datasets). Soils in the study area are acidic and frigid. Depending on the amount of emergent rock, soils often display deep organic layers [17, 39, 44].
Regionally, Simon et al.  and Ulrey  characterized southern Appalachians northern hardwoods as those forests dominated by American beech, yellow birch, red maple (Acer rubrum), sugar maple (Acer saccharum), black cherry (Prunus serotina), and yellow buckeye (Aesculus octandra). This ecological group was then divided into 4 different subgroups: boulder fields, beech gaps and slopes, rich coves, and typic subtype northern hardwood [1, 36]. The boulder field subgroup has a canopy that is dominated by yellow birch, whereas the beech gap and slopes are almost exclusively American beech [1, 7, 36, 45, 46]. Rich coves are composed of all of the listed species with no single dominant species and may also have mesophytic species such as basswood (Tilia americana), white ash (Fraxinus americana), silverbell (Halesia carolina), and eastern hemlock (Tsuga canadensis) [1, 36]. The typical northern hardwood subgroup is dominated by yellow birch, American beech, yellow buckeye, and sugar maple with northern red oak or red spruce individuals occasionally present but rarely dominant in the stand composition [1, 7, 36, 45]. The high elevation red oak forest type also occurs frequently at this elevation range but is typically found on more xeric and exposed landforms (southerly aspects and ridge tops below the red spruce-Fraser fir zone). The oak type is more fire tolerant than the northern hardwood forest. At higher elevations in the study area, forests increasingly are dominated by red spruce and Fraser fir, although northern hardwood species are often present until elevations exceed 1800 m [1, 7, 36, 45]. Although there are some old-growth northern hardwood stands in the Great Smoky Mountains National Park, virtually all of the area we examined and that is extant on the landscape can be considered mature, second growth that originated after logging in the early 20th century [45, 47–49].
Using a method to validate DEM-based models similar to the approach of Odom and McNab , we used ESRI’s ArcMap  to randomly select sampling points in clipped US Geological Survey (USGS) DEMs downloaded from the National Elevation Dataset (NED) [51, 52]. These sampling points served as center points on 200 m belt transects with sampling points placed at 0 m, 100 m, and 200 m. This was done in order to maximize the topographic effects on the data based on our previous knowledge of the study area terrain. For accessibility, we generated study points that were within 1000 m of the Blue Ridge Parkway or US Forest Service (USFS) roads or established hiking trails. An excess of points was originally generated to allow for the elimination of points in the field that occurred in nonforested areas (e.g., grassy balds or ericaceous heath communities) or in areas where sampling was prohibited by the National Park Service (NPS) or USFS.
The number of points we established per study area was proportional to the total area above 1219.2.2 m in each. Sampling rates ranged between 0.2% for the larger mountain ranges and 3% on the smaller massifs. Our sampling points in 8 of the 11 study areas met the following criteria: elevation >1219.2 m, within a designated CNFS recovery area, and reasonably accessible. The remaining 3 study areas included one area without documented CNFS populations but met our elevation criteria, and northern hardwood forest species were known to be present there. The lower elevation limit of 1219.2 m was based on the lowest recorded elevation of CNFS capture regionally  and also approximates where mid-elevation forest types transition to high-elevation types in the southern Appalachians [45, 53].
We used a mapping grade Trimble GeoXT GPS unit (the use of any trade, product, or firm names does not imply endorsement by the US government) with submeter accuracy to navigate to the randomly generated study points that were generated from the DEMs. At each sampling point, we tallied the total number of stems for each tree species using a 10-factor basal area prism to identify dominant overstory species and made a visual determination of forest type. We noted dominant understory woody species to aid in classifying sample locations as northern hardwood or other forest types. We also looked for any evidence of past forest disturbance such as cut stumps, old logging roads/skidder trails, or abandoned railroad grades which may have influenced stand development. Our forest type categories included northern hardwood (yellow birch, American beech, sugar maple, mountain maple (Acer spicatum), basswood, and yellow buckeye), red spruce-Fraser fir, high elevation northern red oak (dominated by northern red oak with an element of American beech), and montane pine (composed mostly of table mountain pine (Pinus pungens) with pitch pine (Pinus rigida) present at some locations). A decision tree encompassing these definitions and descriptions for forest types was used for continuity throughout our study duration; we acknowledged that some species overlap may occur between forest types due to the large variation in terrain conditions and geographic extent of the study area [1, 7, 34, 36, 45, 54].
We classified each study point as ridgeline, shoulder, side slope, or cove and further characterized each point by its vertical position on the slope (low, medium, or high) to describe each point's location and topographic position in relation to the surrounding landscape . We collected elevation, slope gradient, and aspect measurements at each study point in the field using GPS, a clinometer, and a compass, respectively, following methods described by McNab et al. . Aspect was measured in the direction of the steepest downward slope and we recorded slope gradient from the sampling point to a point approximately 15 m away in the same direction.
2.2. Deriving Terrain Variables
We downloaded USGS-produced 1/3 arc-second (10 meter) digital elevation models [51, 52] for each study area and derived 5 terrain variables (elevation, slope gradient, aspect, topographic exposure index, and slope curvature). Slope gradient was computed using the 4-cell method in DEM Surface Tools  and aspect was calculated using ArcGIS Spatial Analyst and then transformed using a sin transform. Topographic exposure index (TEI) was derived by subtracting the average elevation of an area (defined as a circular area with radius equal to 1000 m) surrounding each cell in the DEM from the elevation at each cell. Cells with relatively high TEI values (approximately >50) represent exposed peaks and ridges, while low values (approximately <−50) represent sheltered landforms such as coves and lower slopes. The Raster Calculator tool in ArcGIS Spatial Analyst was used to derive TEI. We derived curvature values using the algorithm identified by Moore et al.  as a way to describe hydrological catchment areas whereby DEM Surface tools multiply the curvature values by negative 1 and then by 100 to maintain consistency with the values calculated by ArcGIS . Once these terrain surfaces were calculated for all study areas, we overlaid a vector point file of sample locations and extracted terrain values for each sample point.
2.3. Statistical Analysis
We created a series of six overarching a priori model categories to examine presence or absence of the northern hardwood forest type based on previous research findings reporting the effects of topography on regional forest types plus a global model. In addition to topographic effects, we included our northing coordinate for each sample point as a measure of latitude to examine the change in south to north elevation clines for northern hardwood presence. The model categories we constructed were based on inclusion of the following variables: (1) Elevation , (2) Elevation + TEI , (3) Elevation + Aspect , (4) Elevation + Curvature [34, 58], (5) Slope gradient + TEI , (6) Elevation + Aspect + Slope gradient , and (7) Global using all parameters.
We used correlation analysis to examine multicollinearity and redundancy relationships among variables and eliminated those variables with a correlation coefficient greater than 0.8, proceeding with the variable believed to be most beneficial to analysis . We then used the forest type as a categorical response and the derived terrain variables and a latitudinal gradient as predictors in a multinomial regression using the statistical software  and the neural network package . In addition to the main effects, all interactions among variables, as well as quadratic effects of individual variables, were examined to allow for examination of a nonlinear relationship between a predictor variable and a response [62, 63]. The multinomial regression technique uses a set of binomial comparisons to classify data as one of our three possible outcomes. The resulting equations are based on the target or reference group (northern hardwood) versus one of the other possible outcomes (northern red oak or spruce-fir). The result is a probability for each possible outcome for each data point. We then classified the data points to one of three forest types that corresponded to the highest probability. We used Akaike information criteria corrected for small sample sizes (AICc) to avoid overfitting of the model to the dataset . We ranked all of the models based on their respective AICc scores and considered the model with the lowest AICc score the best approximating . To further examine performance of our best approximating model, we used a bootstrap procedure to compute an overall correct classification rate as well as model specificity and sensitivity to correctly predict the northern hardwood forest type. We then took the best performing model and created a predictive map using the study area terrain rasters in the statistical software package  that executed the model on a cell by cell basis and classified each as one of the three forest types. We then wrote these predicted cell classifications to georectified tiff image and exported it to ArcGIS for visual inspection.
3.1. Model Selection and Prediction Accuracy
The 338 sites we sampled encompassed a wide range of terrain conditions (Table 1); 179 were characterized as the northern hardwood forest type and the remaining 153 sites were composed of the high elevation northern red oak forest type () and the red spruce-Fraser fir forest type (). The montane pine community () was dropped from the analysis due to the low rate of sampling. The northern hardwood forest type was found most often in sheltered areas at higher elevations than either the high elevation northern red oak forest type or montane pine communities but was consistently found at lower elevations than the red spruce-Fraser fir forest type.
Ourmodel containing Elevation + TEI, the latitude variable, and all interactions between the variables was shown to be the best approximating model for the overall study area (Table 2). Elevation + TEI indicated that the predicted occurrence of the northern hardwood forest type was negatively correlated with elevation and TEI when compared to the northern red oak forest type, but positively correlated when compared to the spruce-fir forest type (Table 3). Of all of the terrain variables we examined, the elevation variable was significant () across all of the models. Our elevation + TEI model had an overall accuracy rate of 67% for all forest types but was significantly better at predicting our target forest type (northern hardwood) with an 80% accuracy rate (see Table 4). We then created a predictive map for our study using this equation (Figure 2). Our predictive map was overlaid with existing forestry data for post hoc visual analysis of misclassified points. Visual inspection showed that a large portion of the misclassified points occurred near the edges and areas where our predicted forest types overlapped with other forest types from existing forestry data sets. This likely indicates that many of the misclassified points were ecotone areas with similar probability values in more than one of our forest types.
Our use of GIS to delineate northern hardwood forests in the southern Appalachians gives managers in the region a tool to better understand the distribution and composition of high-elevation forests important for the management and recovery of CNFS as well as other species restricted to high elevation forests. Previous studies have indicated that using digital terrain analysis within a GIS, most physiographic regions can be modeled with some degree of accuracy in the southern Appalachians [7, 34, 65, 66]. Our models show that a perceptible relationship exists between the northern hardwood forest type and some of the variables we examined. Our Elevation + TEI model was the best model for the study area as a whole.
Our best model, Elevation + TEI, supports the current assertion that elevation plays a key role, as does the level of “shelteredness” of a point for determining the presence of the northern hardwood forest type [15, 36, 37, 67, 68]. The significance of the quadratic effects of the elevation variable clearly suggests that this is not a linear relationship but is influenced by other attributes of a specific site such as TEI. Others in the region also have indicated the role of an elevational gradient in combination with other site factors on stand development in the southern Appalachians [1, 36, 44, 69, 70].
Our results also show that there was significant overlap in the range of several of the terrain variables we examined between the northern hardwood forest type and the adjacent red spruce-Fraser fir, high elevation northern red oak, and montane pine community. This can be attributed to the northern hardwood forest type having a higher mean elevation than the northern red oak forest type regionally but a lower mean elevation than the red spruce-Fraser fir forest type (Table 1). Additionally, the overlap in the other terrain variables is likely due to the wide variation in terrain occupied by all the forest types examined. It also supports our hypothesis and that of others that as elevation increases, aspect plays a smaller role in determination of forest type in montane systems . Our Elevation + TEI model appears to follow the trend of northern hardwoods occupying more sheltered areas below ridgelines and away from exposed shoulder areas as based on field observations of others [1, 36]. Our model accuracy was congruent with accuracy rates for other vegetation models in the study area, which range from less than 50%  to 86% . Inclusion of additional variables such as a soil related variable or factoring in disturbance history, that is, past fire history, would have likely increased our model’s accuracy and merit further examination.
The variance in significance among predictors between the models on the overall study area also shows the complexity of the effects of latitude, terrain, site quality, and disturbance patterns on stand composition in the southern Appalachians. Terrain, site quality, and disturbance patterns are directly related to stand development regionally. However, past exploitative logging  and other disturbances such as conversion to pastoral system lead to burning and clearing of large areas of forest with subsequent nonanalog successional trajectories that disrupted some of the predictable association patterns in the southern Appalachians over the past 100+ years [7, 44, 47, 72].
The acreage of the northern hardwood forest type in the southern Appalachians is likely to increase as this forest type continues to reoccupy areas previously occupied by oak communities. Fire suppression that began in the 1940’s has allowed for conditions to favor mesophytic species commonly associated with the northern hardwood forest type such as American beech, yellow birch, and maples to increase in abundance in the advance regeneration pool [8, 73]. In the absence of disturbance such as fire and significant canopy removal, the high elevation northern red oak forests may become restricted to the more xeric or exposed mid-elevation slopes regionally, thereby allowing for expansion of the northern hardwoods overall .
Conversely, both climate change and atmospheric deposition continue to threaten the red spruce-Fraser fir forests of the southern Appalachians likely resulting in the northern hardwood forest type expanding as temperature and environmental conditions shift [41, 74, 75]. How potential replacement of these conifer stands by northern hardwoods will impact CNFS is not fully known. Still, our predictive maps in combination with additional variables such as proximity to red spruce-Fraser fir forests could help prioritize where to conduct conservation or management activities to support habitat conditions favorable to CNFS and unfavorable to SFS. For example, applications of our map showing the locations of the northern hardwoods would allow land managers to better identify areas to avoid prescribed burning (used to promote or maintain oak stands) or identify areas to “release” understory red spruce as management actions favoring CNFS [5, 23, 28, 76]. Conversely, incongruence in our map of predicted northern hardwood absence and actual presence shows managers where application of prescribed burning to restore or promote oak would be more or less appropriate.
These models could have significant implications in management practices when used in combination with known areas of red spruce and Fraser fir. A more specific habitat management and conservation plan could be developed for CNFS with available resources channeled to a more focused area. It also increases the likelihood that this species may occupy a larger portion of the landscape than previously suspected and raises the possibility of the existence of a larger population of this species and that recovery efforts may be more successful than previously thought. However with the current threats to the high elevation ecosystems, it will be crucial to continue to gather onsite data for much of this area. Further analysis and inclusion of additional variables would be needed to increase the predictive power of the models examined due to the influence of the variability of points occupied by the northern hardwood forest type. Using a combination of existing forestry data and land cover data from satellite imagery analysis, our predictive map of northern hardwoods could be used for a second step of pruning our incorrect classifications. As such, the combination of predicted northern hardwood distribution and existing land cover data will make it possible for managers to identify and put into practice management policies that will help conserve and improve areas such as recovery areas for CNFS as well as other stewardship goals.
Conflict of Interests
The authors declare that there is no conflict of interests regarding the publication of this paper.
Funding for this study was provided by the US Geological Survey, Cooperative Research Unit Program, the Eastern band of Cherokee Indians, and the Department of Geography at Virginia Tech’s Sidman Poole Foundation Trust. Additional logistic support was provided by the US Forest Service Southern Research Station, Bent Creek Experimental Forest. The authors thank M. Duncan for field assistance and H. McNab for assistance with study design and field methodologies.
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