- freely available
Forests 2012, 3(3), 591-604; doi:10.3390/f3030591
Abstract: The objectives of this study were to (1) characterize tree-based spatial patterning of soil properties and understory vegetation in frequently burned (“reference state”) and fire-suppressed longleaf pine forests; and (2) determine how restoration treatments affected patterning. To attain these objectives, we used an experimental manipulation of management types implemented 15 years ago in Florida. We randomly located six mature longleaf pine trees in one reference and four restoration treatments (i.e., burn, control, herbicide, and mechanical), for a total of 36 trees. In addition to the original treatments and as part of a monitoring program, all plots were subjected to several prescribed fires during these 15 years. Under each tree, we sampled mineral soil and understory vegetation at 1 m, 2 m, 3 m and 4 m (vegetation only) away from the tree. At these sites, soil carbon and nitrogen were higher near the trunk while graminoids, forbs and saw palmetto covers showed an opposite trend. Our results confirmed that longleaf pine trees affect the spatial patterning of soil and understory vegetation, and this patterning was mostly limited to the restoration sites. We suggest frequent burning as a probable cause for a lack of spatial structure in the “reference state”. We attribute the presence of spatial patterning in the restoration sites to accumulation of organic materials near the base of mature trees.
Individual trees in woodland and forest ecosystem can create chemical and physical gradients that affect the spatial patterning of soil properties [1,2,3]. Trees can create gradients in soil moisture [4,5,6], temperature [7,8], texture , carbon (C) and nutrient accumulation and turnover [10,11,12], understory species composition through spatially distinct effects via litter accumulation [1,12,13], stemflow and throughfall [14,15], light and precipitation interception [16,17,18] and root distribution [8,19].
Southeastern longleaf pine woodlands are one of the most endangered ecosystems in the United States due to decreased fire frequency and conversion of woodlands to agroforestry and agriculture [20,21]. These ecosystems were historically described as open, fire-maintained woodlands with a sparse but species-rich understory . Frequently burned (i.e., fire frequency of 1–12 years) longleaf pine woodlands have very little organic matter on the ground, with the exception of a more substantial accumulation of litter and woody debris under the canopy of individual pines [21,22]. The most xeric sites—termed pine sandhills—tend to have very low organic matter accumulation  and open understory . Modern fire suppression from forest management or agriculture, however, has led to hardwood encroachment, the development of a woody mid-story  and altered cover and composition of understory vegetation [23,26,27,28]. Without fire, litter from pines and hardwoods can accumulate as deep as 25 cm, especially near the bases of large trees . In savanna-type forests, levels of soil organic matter and nutrients are generally higher below the tree canopy [4,29]. In contrast, in other woodland ecosystems, the absence of fire tends to homogenize the distribution of soil organic matter and nutrients [30,31,32]. It is unknown whether longleaf pine woodlands exhibit strong tree-level spatial patterning of soil nutrients and understory vegetation when burned frequently or whether fire-suppression and woody encroachment alter spatial patterning.
Active management to restore the native community structure of longleaf pine woodlands has been underway in parts of the Southeast and often consists of hardwood removal by mechanical or chemical treatments and/or the re-introduction of frequent fire [33,34]. Re-introduction of fire to long-unburned stands (i.e., unburned for more than ~10 years) can reduce the hardwood component in the mid-story and facilitate the re-establishment of native forbs and graminoids in the understory [23,28,35,36]. Herbicide and mechanical treatments, by contrast, are more effective in removing the hardwood mid-story than in improving groundcover species richness [23,28]. Little is known, however, about the effects of any of these restoration treatments on the spatial patterning of soil biogeochemistry and understory vegetation.
In this study, we characterized the spatial variability of soil biogeochemistry and understory vegetation in relation to individual longleaf pine trees in reference stands and a 15 year-old experimental manipulation of restoration treatments on Eglin Air Force Base (EAFB), Florida, USA. In 1994, the Longleaf Pine Restoration Project (LPRP) was established in fire-suppressed longleaf pine sandhills on base lands to explore the effects of restoration treatments on community composition and soil processes . Prior to the LPRP project, these fire-suppressed forest stands remained unburned for more than 20 years and were also subjected to some logging activities. Experimental treatments applied in 1994 included three hardwood reduction techniques (spring burning, herbicide application and mechanical (i.e., chainsaw felling and girdling)) and a control (continued fire-suppression). However, it should be noted that all plots (including controls) were subjected to several prescribed fires during the last 15 years as part of EAFB natural resources management. Reference sites (i.e., the target for restoration) where fires still occurred at a relatively high frequency (i.e., fire frequency of <8 years) were selected at the time of the initial experimental application and have been concurrently monitored. Fifteen years later, we revisited the LPRP and reference plots to determine whether the spatial patterning of soil processes and vegetation had been affected by the treatments. Our goals were to (1) characterize tree-based spatial patterning of soil characteristics and understory vegetation in the reference sites and restoration treatments; and (2) determine whether restoration treatments differed in their ability to restore spatial patterning to that seen in reference stands.
2. Experimental Section
2.1. Study Sites
Our study was conducted in longleaf pine forests at EAFB (30°29’00” N; 86°31’52” W), which is located on the panhandle of Florida, USA. This area was previously managed as the Choctawhatchee National Forest and was transferred to the Air Force in 1940. Soils of the study sites were typic Quartzipsamments of the Lakeland series with mean depth to water table of 200 cm . The climate of the area is subtropical, with warm, humid summers and mild winters. Mean annual temperature is 19.8 °C, with a mean annual precipitation of 1580 mm, most of which falls from June to September . Study sites were 52–85 m above sea level, and all sites had the minimal topography typical of sandhills . EAFB sandhills fall under Xeric Sand Barrens and Uplands of the Eastern Gulf Coastal Plain classification by Peet . Vegetation was dominated by a longleaf pine overstory with a mid-story of various deciduous oaks, e.g., Quercus laevis Walter, Q. margaretta Ashe, Q. incana Bartram, Q. germinata Small.
2.2. Sampling Design
Five treatment blocks were established in 1994. Each block was composed of four 900 m × 900 m plots with each plot representing one hardwood removal treatment (burn, mechanical, herbicide, and control). Six reference plots were also established in the site area. Reference plots were chosen based on “expert opinion” for the desired state for the natural ecosystem [24,40]. Each treatment was carried out only once but were under the EAFB natural resource management program, and all plots were subjected to a number of prescribed burns and wildfires between 1994 and 2009. During these 15 years, reference, burn, control, herbicide and mechanical plots were burned 9, 4, 3, 5 and 4 times respectively. All plots were burned between January and April 2009 prior to this study.
In August 2009, due to time and military mission constraints, we selected only one block of restoration treatments (consisting of four plots, one for each four restoration treatments) and one block for the reference (consisting of two plots), and we randomly located six mature longleaf trees in each plot (i.e., 6 plots × 6 tree/plot). Under each tree, we removed the litter and organic layers and sampled mineral soil (0 to 20 cm) at 1m (near the trunk), 2m, and 3m (outside the tree crown) away from the tree, at three directions (0, 120, 240°) and bulked samples by distance from the tree. At each sampling location, a 0 to 20 cm depth volumetric soil sample was taken with a 2.5 cm diameter soil core. For this study we concentrated on the 0–20 cm depth because it is the area with the highest density of fine roots [41,42]. Soil samples were kept on ice for transport back to University of Florida and kept at 4 °C for <1 week before processing.
In July 2011, we revisited the plots and the same 36 longleaf pine trees for a survey of the groundcover vegetation. Four 1 m line transects were placed perpendicular to each of the same three directions (i.e., 0°, 120°, and 240°) from the trees at 1 m, 2 m, 3 m and 4 m for a total of 12 line transects per tree. Using the line-intercept method [43,44], percent cover was estimated as a proportion of the line covered by each vegetation category to the total length of the line <1 m high. Vegetation was classified by eight categories: wiregrass (Aristida stricta Michx.), other graminoids, legumes, other forbs, saw palmetto (Serenoa repens W. Bartram), pines, other woody species, and moss. Graminoids were defined as any grass or sedge except wiregrass. Woody species were defined as any groundcover vegetation with a woody stem except saw palmetto or pines (<1m high). Cover classes were estimated for each of the eight vegetation categories crossing the plane of the line transect at <1 m high: 0 = 0%; 1–5 = 3%; 6–10 = 8%; 11–15 = 13%; 16–25 = 21%; 25–50 = 38%; 51–75 = 68%; 75–95 = 85%; and 95–100 = 98%. Cover classes were assigned at the line transect level. To minimize error in cover estimation, a meter stick was used for the line transect so that the percent cover would equal the total cm of vegetation crossing the plane of the line transect. Due to the vertically stratified nature of the vegetation, it was possible to have total cover of all vegetation categories exceed 100%.
2.3. Soil Analysis
Soils were homogenized by passing through a < 2 mm sieve and roots, twigs, and green vegetation were removed by hand. From each soil sample, a sub-sample was used to determine gravimetric moisture content, total soil C and N, initial inorganic nitrogen (NO3−-N and NH4+-N), and initial basal respiration. Soil basal respiration and inorganic nitrogen (NO3−-N and NH4+-N) were also measured after a 6-week aerobic laboratory incubation at field moisture and 25 °C. Soil samples were adjusted with additional water during the incubation to maintain field moisture.
Total soil C and N were measured on subsamples of initial soil cores using a Costech ECS 4010 Elemental Analyzer (Costech Analytical Technologies, Inc., Valencia, CA, USA) and calculated on a dry soil mass (%) and volume basis (e.g., g m−2).
To determine basal respiration, we placed one specimen cup filled with approx. 30 g fresh weight soil into one 1 L Mason jar. We measured CO2 production from the samples by sealing the Mason jars and measuring CO2 accumulation in the headspace over a 96-h period. Air samples (10 mL) were taken from the jar headspace at time 0 and at 96 h by syringe through a septum in the Mason jar lid, and injected into a Li-Cor 6252 CO2 analyzer fitted with a calibrated injection port (Li-Cor, Nebraska, USA). Carbon flux rate was determined at the beginning of the incubation, after one week and after six weeks. Carbon dioxide production was expressed as μg C gdw−1 h−1.
To determine N mineralization, soil samples were analyzed for initial and final pools of inorganic N (NO3−-N and NH4+-N) by extracting approximately 10 g of field moist soil with 50 mL of 2.0 M KCL . The solutions were shaken for 1 h and left to sit in an air-conditioned room (approx. 23 °C) for 18–24 h and then filtered using a Whatman (GF/A) filter under vacuum. Ammonium and NO3− concentrations in extracts were determined colorimetrically using an Astoria-Pacific colorimetric autoanalyzer (Astoria, Oregon, USA). Net rates of nitrification and N mineralization for the incubation period (i.e., six weeks) were calculated from the differences in initial and final inorganic N pools divided by the incubation time. All initial N pools and N rates were calculated on a dry soil mass basis (e.g., µg N gdw−1) and volume basis (e.g., g N m−2).
2.4. Statistical Analysis
To determine linearity between soil and vegetation characteristics and distance, we first fit regression lines separately for each treatment. To compare the regression lines, we used ANCOVA, with treatment as the categorical variable and distance as the continuous variable [46,47,48]. If an ANCOVA has a significant interaction between treatment and distance, it will indicate that the slope (i.e., distance) of the soil or vegetation variable analyzed differs for different treatments. Multiple comparisons of means were also performed with the Tukey’s HSD post hoc test (see Table S1). All results are reported as significant when p < 0.05. All statistical analyses were computed using R 2.14.2 [49,50].
3.1. Soil Nutrients
In the herbicide plot, soil bulk density was positively related to distance (Table 1; Figure 1; Table S2). In contrast, our results show that C and N concentrations were negatively related to distance from the tree. These relationships were linear (i.e., nonzero slope) and similar (i.e., same slope) in the burn, control, herbicide and mechanical plots. In the burn and mechanical plots, soil C and N pools decreased with distance from the tree, while the CN ratio showed the same trend for the control plot only. These spatial patterns were, however, generally weak as distance never accounted for more than 25% of the variation. Additionally, C and N concentrations and pools were consistently lower in the reference than in the herbicide plot while soil bulk density showed greater values in the reference compare to the burn plot (Table S1).
|Responses variables||Distance||Treatment||D × T|
|Soil characteristics||Bulk Density (g cm−3)||5.7||0.019||2.7||0.034||1.2||0.285|
|Moisture Content (%)||0.8||0.387||1.1||0.379||0.1||0.988|
|C (%)||22.8||< 0.001||4.9||0.001||0.9||0.492|
|N (%)||16.4||< 0.001||9.2||< 0.001||0.6||0.692|
|C pool (g m−2)||12.4||< 0.001||3.9||0.005||0.8||0.538|
|Soil characteristics||N pool (g m−2)||5.9||0.017||6.4||< 0.001||0.8||0.571|
|NH4 (g N gdw−1)||0.4||0.562||1.2||0.324||2.0||0.105|
|NO3 (g N gdw−1)||0.5||0.463||3.0||0.022||0.7||0.571|
|NH4 (g m−2)||0.1||0.906||1.0||0.425||2.4||0.059|
|NO3 (g m−2)||1.9||0.172||2.4||0.054||0.7||0.572|
|Nitrification (g N gdw−1 d−1)||0.1||0.719||2.6||0.041||4.3||0.003|
|Mineralization (g N gdw−1 d−1)||0.1||0.858||2.1||0.087||1.1||0.356|
|Nitrification (g N m−2 d−1)||0.1||0.834||2.6||0.038||4.1||0.004|
|Mineralization (g N m−2 d−1)||0.0||0.959||2.1||0.098||1.1||0.356|
|Initial C flux rate (µg C gdw−1 h−1)||0.8||0.361||0.6||0.641||0.3||0.897|
|6-week C flux rate (µg C gdw−1 h−1)||0.9||0.352||1.1||0.353||1.3||0.268|
|Plant functional groups||Graminoids (%)||3.5||0.062||1.0||0.417||0.7||0.561|
|Forbs (%)||4.5||0.035||5.5||< 0.001||0.7||0.571|
|Woody species (%)||3.7||0.057||8.0||< 0.001||2.4||0.054|
|Saw palmetto (%)||4.7||0.003||5.5||< 0.001||0.9||0.468|
3.2. Nitrogen and Carbon Mineralization Rates
In the case of nitrification rates (mass and volume basis), the interaction between distance and treatment was significant, with a greater increase of the slope in the control plot (Table 1; Figure 2). On the other hand, we found no difference of spatial pattern or difference between treatments for inorganic N (Table 1; Figure 2; Tables S1 and S2). Additionally, we did not detect distance or treatment effects for C flux rates (data not shown).
3.3. Understory Vegetation
We observed a linear relationship between plant functional group and distance from the trunk in reference and restoration plots (Table 1; Figure 3; Table S2). Graminoids, forbs and saw palmetto all increased with distance from the trunk but only in the reference, herbicide and reference plots respectively. Additionally, woody species cover showed a different spatial pattern in the control and reference plots, with a steeper rate of decrease with distance from the trunk (Figure 3). Finally, forbs cover was lower in the reference than the burn plot; woody species almost absent in the herbicide plot; and saw palmetto cover reaching 5% only in the herbicide plot (see Table S1).
In this study, we found evidence of spatial patterning associated with individual longleaf pine trees in the soils and vegetation of xeric pine sandhills, but this patterning was mostly limited to the restoration sites. Overall, total surface soil C, N, and CN ratio all decreased with distance from the tree, while soil bulk density increased. Graminoids, forbs, and saw palmetto also showed a distinctive spatial pattern, with covers increasing with distance from the tree. These effects were primarily driven by the reference and herbicide plots. In the reference and control plots, only woody understory cover showed significant spatial patterning, with more cover closer to the trees (i.e., decreasing slope).
Mean soil characteristics also differed between the reference and restored sites. For instance, soil C and N was consistently lower in the reference plots. One factor that may contribute to the lack of spatial structure and lower soil C and N concentrations in the reference treatment may be more frequent burning. The reference treatment was subjected to nine burns since the initiation of the LPRP project in 1994 (1994–2009), plus three additional fires prior to this project (1971–1994). In contrast, only four burns have been recorded in the restoration treatments over this time period, all occurring after 1994. In the absence of fire (or longer fire interval), pine litter and woody debris accumulation, in addition to hardwood establishment, may have led to the development of spatial gradients through higher inputs of organic matter near trees. Reintroduction of fire at a frequency of once every 4 years was apparently not enough to return soil N levels to historic conditions (i.e., 0.018%–0.027%) .
4.1. Soil Gradient
Our results suggest that longleaf pine trees play a role in the spatial patterning of soil C and N concentrations, at least where long-term fire frequency is low. In the experimental plots, C and N concentrations were higher near the trunk where litter accumulation and forest floor depth are generally greater [19,51,52]. Indeed, Varner et al.  reported that without fire, litter from pines and hardwoods could accumulate as deep as 25 cm near the trunk of large trees. Burning of accumulated organic materials results in losses of C and N via volatilization, but also as an input, through ash, of soil C and N via leaching into the mineral soil .
Surprisingly, we found no evidence of this spatial structure in the reference plots. We suspect that the higher number of fires (i.e., fire frequency of ~3 years over the last 38 years) that occurred during several years prevented these accumulations of organic matter near the trunks. In addition, it may be that reference and restoration plots had pre-existing differences that were independent of fire history. We concentrated this study on one “reference state” and therefore we cannot generalize this conclusion to all “reference states”. It may be that reference and restoration plots cover different ranges in state variation. For EAFB only, Rodgers and Provencher  described at least two distinct sandhill associations: burned-wiregrass (this study) and burned-bluestem. Peet  described additional longleaf pine associations, largely determined by edaphic variation and soil disturbance histories. Although soil texture did not differ between the reference and restoration plots , it may be that fine scale heterogeneity in other, unmeasured soil characteristics differed between these areas. In addition to soil characteristics, tree density and basal area may also vary among these “reference states” and may vary between our reference and restoration treatments, and this variation could be linked to recent history. It may also be that spatial structure in “reference states” with more savanna characteristics, such as low tree density and low canopy cover, differs from those with more similarities to woodlands (higher tree density, higher canopy cover).
Similarly, we found no clear evidence of spatial patterns of extractable inorganic N. The only exception was high nitrification rates in inter-canopy gaps, which only occurred in the control treatment that was burned only three times in 38 years (i.e., fire frequency of ~12 years). Higher net nitrification rates may indicate nitrogen available in excess of microbial demand and may reflect higher quality organic matter inputs from hardwoods .
4.2. Vegetation Gradients
In addition to affecting spatial patterns of soil nutrients, pine trees also had a small effect on the spatial patterning of understory vegetation. The effect varied but when the analysis was divided by functional groups, we detected an effect for graminoids and saw palmetto that was driven by the reference plots’ trend towards increasing cover with distance from trees. For forbs, this same effect was also present but only in the herbicide treatment. These results may be attributed to better habitat conditions such as understory light availability following fuel and hardwood midstory reduction  or may reflect differences in available soil resources.
In contrast to the three other functional groups, the woody plants showed a different spatial structure, particularly for the reference and control plots. Surprisingly, woody cover was greater near the trees. Although, it remains unclear why repeated fires did not create a similar spatial structure for these plants.
Our study showed that longleaf pine trees did have an affect on the spatial patterning of soil and understory vegetation, but were most pronounced in the restoration sites. This result could be explained by frequent burning in the “reference state”, and pre-existing differences between the reference and restorations sites. In addition, it is also possible that other longleaf pine stands with different disturbances histories or site characteristics (e.g., tree density, canopy cover) will express a different spatial structure of soil and understory vegetation.
The authors are thankful to Amanda Steen from the Joseph W. Jones Ecological Center and Brett Williams from Jackson Guard at EAFB for field assistance. We also thank Jenny Schafer, Jennie Demarco, Grace Crummer, and Julia Reiskind for laboratory assistance and Doria Gordon for valuable assistance. We are also grateful to four referees and Laura Schreeg for comments on earlier drafts of this manuscript. This research was supported by the Strategic Environmental Research and Development Program (Grant # 09 SI01-001).
Conflict of Interest
The authors declare no conflict of interest.
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