Biomass for bioenergy is debated for its potential synergies or tradeoffs with other provisioning and regulating ecosystem services (ESS). This biomass may originate from different production systems and may be purposefully grown or obtained from residues. Increased concerns globally about the sustainable production of biomass for bioenergy has resulted in numerous certification schemes focusing on best management practices, mostly operating at the plot/field scale. In this study, we compare the ESS of two watersheds in the southeastern US. We show the ESS tradeoffs and synergies of plantation forestry, i.e., pine poles, and agricultural production, i.e., wheat straw and corn stover, with the counterfactual natural or semi-natural forest in both watersheds. The plantation forestry showed less distinct tradeoffs than did corn and wheat production, i.e., for carbon storage, P and sediment retention, groundwater recharge, and biodiversity. Using indicators of landscape composition and configuration, we showed that landscape planning can affect the overall ESS supply and can partly determine if locally set environmental thresholds are being met. Indicators on landscape composition, configuration and naturalness explained more than 30% of the variation in ESS supply. Landscape elements such as largely connected forest patches or more complex agricultural patches, e.g., mosaics with shrub and grassland patches, may enhance ESS supply in both of the bioenergy production systems. If tradeoffs between biomass production and other ESS are not addressed by landscape planning, it may be reasonable to include rules in certification schemes that require, e.g., the connectivity of natural or semi-natural forest patches in plantation forestry or semi-natural landscape elements in agricultural production systems. Integrating indicators on landscape configuration and composition into certification schemes is particularly relevant considering that certification schemes are governance tools used to ensure comparable sustainability standards for biomass produced in countries with variable or absent legal frameworks for landscape planning.
Citation: Meyer MA, Chand T, Priess JA (2015) Comparing Bioenergy Production Sites in the Southeastern US Regarding Ecosystem Service Supply and Demand. PLoS ONE 10(3): e0116336. https://doi.org/10.1371/journal.pone.0116336
Academic Editor: Runguo Zang, Chinese Academy of Forestry, CHINA
Received: October 2, 2014; Accepted: December 8, 2014; Published: March 13, 2015
Copyright: © 2015 Meyer et al. This is an open access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited
Data Availability: All relevant data are within the paper and its Supporting Information files.
Funding: This work was partly funded by the European Union FP7 project SECTOR (Production of Solid Sustainable Energy Carriers by Means of Torrefaction), grant agreement number 282826, https://sector-project.eu/, and the Higher Education Commission Pakistan in cooperation with the German Academic Exchange Service (DAAD), http://www.hec.gov.pk/. The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist.
Research in the context of bioenergy and ecosystem services (ESS), the perceived human benefits from ecological systems , often focuses on largely debated 1st generation liquid biofuel feedstocks such as maize in the US, sugarcane or soybeans in Brazil, or rapeseed in Europe . Some papers address scenarios with a shift to 2nd generation liquid biofuel feedstocks, such as grasses or other perennial bioenergy feedstocks [3,4]. Research in this area only partly reflects the fact that only 3% of the global bioenergy supply was obtained from dedicated energy crops in 2008. More than 80% of the global bioenergy supply originates from forest biomass . With respect to modern solid bioenergy carriers, wood pellets have experienced an increased global trade volume, accounting for 120 PJ (∼660 Mt) of the total global solid bioenergy carrier trade of 300 PJ (∼1640 Mt) as of 2010 . For trade between EU and non-EU countries in 2010, the wood pellet trade volume of 45 PJ (∼250 Mt) is comparable to those of biodiesel and bioethanol .
Increasing forest biomass use and trade may also affect the supply of other ESS, e.g., carbon storage or groundwater recharge [8,9], or create environmental impacts exceeding the capacity of regulating ESS; e.g., increasing biomass may affect sediment retention due to increased plantation forestry . The expansion of bioenergy production is limited by and competing with the demand for land for other bio-based commodities (food, feed and fiber) . In that respect, a current draft of new sustainability requirements of the EU Renewable Energy Directive (RED) emphasizes the consideration and quantification of tradeoffs of feedstock production for liquid, gaseous and solid bioenergy and other ESS, such as carbon storage or sediment retention . Further research in this context may examine the ability to avoid negative impacts, such as the effects on erosion, carbon storage or biodiversity [2,7,13].
Existing studies on ESS supply typically model a single case study area with a mostly heterogeneous or contrasting land use/land cover composition and partly model synergies and tradeoffs in ESS supply, e.g., [14,15]. Rather homogenous and more intensively managed land use/land cover systems for ESS supply, e.g., systems specialized in forest plantations or agriculture, may require more significant tradeoffs regarding other ESS compared to heterogeneous production systems for biomass. For example, they are more likely to exceed critical environmental thresholds such as erosion control, water purification or recreation due to underrepresented natural or semi-natural vegetation [16,17]. Increased landscape heterogeneity helps to ensure a balanced supply of biodiversity and regulates ESS, such as the higher nutrient retention efficiency of riparian buffer zones in agricultural landscapes . Larger quantities of bioenergy feedstocks may generate economies of scale for processing and logistics , contributing to more homogenous landscapes. Considering that different biomass provision options may become even more important in the near future, we analyze ESS supply both in forest plantations and agricultural systems, which may be used interchangeably. For example, agricultural residues, such as cereal straw or corn stover, currently amount to 4% of the global bioenergy supply . In the US, cereal straw and corn stover comprise 97% of the estimated available agricultural residues in the US (2011) . Using residues contributes to reducing or completely avoiding the food versus fuel conflict compared with dedicated energy crops . Direct land use change (LUC) is when biomass production replaces other crops, forests or natural grasslands. Indirect land use change (iLUC) is the clearing of land not specifically for biomass but to meet the demands for other commodities, such as food and fiber, and may occur not only nearby but also in different parts of the region or even different parts of the world .
A wide range of factors may influence ESS supply, such as environmental conditions, including the topography, soil characteristics and climate. In contrast, land management may affect ESS supply [23–25]. In the context of bioenergy production, certification schemes are used as a governance tool to ensure sustainable production. They focus on indicators and prescribed management practices mostly applicable at the plot scale [26,27]. However, certification schemes rarely require indicators at the regional or landscape scale in the context of both bioenergy  and agricultural products  and payment schemes for ESS . At the landscape/regional scale, i.e., the typical scale of landscape planning, the influence of landscape composition and configuration has been argued [30,31] and exemplarily demonstrated for single ESS, i.e., soil protection and retention  and biodiversity .
In this paper, we first assess ESS supply in subtropical watersheds mostly used for (i) forest plantations, Pinus spp., and (ii) agricultural production as bioenergy sourcing regions in the southeastern US. Following [17,34], we expect that the tradeoffs between forest plantations and natural or semi-natural forest as a counterfactual are smaller than between corn and wheat production and natural or semi-natural forest. The remnants of the existing forests reflect the potential natural vegetation in both watersheds . Second, we hypothesize that not only environmental or management factors at the plot scale but also landscape composition and configuration and naturalness assessed at the landscape scale influence ESS supply and biodiversity. Third, we assume that these landscape factors play a role in whether socially accepted environmental thresholds, e.g., water quality, are met within the two contrasting case studies. For example, the connectivity or dominance of patches of natural land cover, which may serve a buffering function, strengthens nutrient or sediment retention.
Materials and Methods
The decline in pulpwood demand in the pulp and paper industry released capacities of existing pine plantations for wood pellets in the southeastern US . The 2008/09 recession and decline of the housing market released round wood from the timber market for solid bioenergy production . A large share of up to 80 PJ (∼440 Mt) of the produced pellets is expected to be exported to the EU by 2020 [6,7]. The Big Satilla and Little Satilla watersheds, addressed as the Satilla watershed throughout the paper, are representative examples of such pine plantation production systems in a humid subtropical climate. The Satilla watershed includes an area of 8,760 km² (hereof: 28% forest plantations in 2006, see Fig. 1) and is located in southeast Georgia, US.
For agricultural residues as an alternative feedstock option, the Mississippi Delta in humid subtropical western Mississippi, US is one of the major agricultural production areas in the subtropical southeastern US due to its alluvial fertile soils. The commodities include corn and wheat , with the area producing 68% of the winter wheat and 79% of the corn in Mississippi in 2013 . A common practice for residues is to burn them completely onsite. Alternatively, a certain share of residues may be used for bioenergy without negatively affecting the nutrient and carbon balances . The Big Sunflower watershed covers 8,170 km² (hereof: 80% agricultural land (four percentage points corn and winter wheat production) in 2006), which represents most of the Mississippi Delta. The Big Sunflower River is a major river in the Yazoo River basin; the latter is a tributary of the Mississippi river.
We model ESS supply for 2006, for which land cover information differentiating between natural and semi-natural forest and plantation forestry is available. Climatically, the precipitation in 2006 in the Big Sunflower watershed (1276.9 mm, SD: 31.0 mm) was 7% lower than the normal climate conditions for the period from 1981 to 2010 ; the precipitation in the Satilla watershed (950.7 mm, SD: 63. 9 mm) was 22% lower than the normal climate conditions. The minimum and maximum average temperatures in 2006 in the Big Sunflower watershed (Tmin: 11.9°C, SD: 0.3°C, Tmax: 24.2°C, SD: 0.5°C) and in the Satilla watershed (Tmin: 11.9°C, SD: 0.3°C, Tmax: 26.4°C, SD: 0.2°C) deviated less than 1 degree Celsius from the normal climate conditions for the period from 1981 to 2010 .
ESS are classified as provisioning, regulating and cultural ecosystem services . We identified the following potentially affected provisioning and regulating ESS based on the existing literature on environmental impacts and ESS for bioenergy [13,27,42–44] and in general [14,18,24,45,46]: carbon storage, nutrient retention, sediment retention, and groundwater recharge. In addition, we assess the impact on biodiversity, which may be a recreational ESS in itself but largely supports the supply of other ESS [47,48]. We focus on phosphorous (P) retention because (i) the nutrient retention efficiency is higher than that for nitrogen, (ii) agricultural sources are responsible for approximately 80% of the P input in the Gulf of Mexico, and (iii) P has been underestimated in its contribution to the eutrophication of the Gulf of Mexico for the Big Sunflower watershed region .
Sustainable production of bioenergy will only be possible if a feedstock is available without major negative direct and indirect impacts on ESS and biodiversity. In contrast to the plantation forestry system with alternative uses of timber, e.g., as construction wood, corn stover and wheat straw have no competing use but are burnt onsite in the Mississippi Delta and are therefore unlikely to cause iLUC risks. Therefore, residue use for bioenergy may save GHG emissions, which are not covered in the ESS assessment. We calculate the amount of sustainably available agricultural residues, i.e., from corn and winter wheat, based on 2006 production data , on ranges of sustainable harvest residue removal rates [39,49,50], and average CO2 and CH4 emission factors for onsite burning practices for agricultural residues in the US .
The amount of carbon stored was modeled with InVEST (Integrated Valuation of Environmental Services and Tradeoffs) [52,53] by refining standard assumptions for aboveground [54–57], belowground [14,55,56,58], soil [54,57–60] and dead organic carbon [14,57,60] for the land use/land cover data for 2006 [61,62].
The amount of retained P was modeled with InVEST. The model estimates P export and retention to surface water bodies based on the land use/land cover specific P input and retention capacity as well as the water yield. The major spatial inputs are the land use/land cover data for 2006 [61,62], a digital elevation model (DEM) , annual precipitation data for 2006 , and the long-term annual average reference evapotranspiration  as well as the depth to any root restrictive layer and the available water holding capacity (AWC) from the Soil Survey Geographic (SSURGO) database . We modified the InVEST default assumptions for evapotranspiration coefficients [66,67], rooting depth [68–72], P export rates and P retention efficiencies [73–75]. We validated the modeled P export against the corresponding phosphorous concentration measurements of the stations Little Satilla near Offerman (USGS 02227500), Satilla River at Atkinson (USGS 2228000) and Big Sunflower River at Sunflower (USGS 07288500).
The amount of retained sediment was modeled with InVEST. The model estimates the sediment retention and export based on the modeled soil loss from the universal soil loss equation (USLE) [76,77], i.e., sheet erosion, and the land use/land cover specific sediment removal efficiencies. The same land use/land cover and DEM datasets used for modeling P retention were used. We obtained the k factor (soil erodibility) from the SSURGO database . We calculated the r factor (rainfall erosivity) based on the following formula : where I30 is the maximum rainfall intensity in 30 minutes obtained from . We refined the required cover and management factor C [77,80–85] and the support practice factor P [80,82,84,86]. We validated the model outcome against the suspended sediment concentration for the same stations as for P export.
The net infiltration was modeled with the soil-water balance model (SWB) from the USGS [87,88]. We simulated the groundwater recharge on a daily basis with the Thornthwaite-Mater evapotranspiration calculation method. We used the same land use/land cover, DEM and AWC datasets as when modeling P retention. The hydrologic soil groups were obtained from the SSURGO database . The daily average temperature and precipitation data were obtained for the Waycross 4 NE (USC00099186) (Satilla watershed) and Cleveland (USC00221738) (Big Sunflower watershed) stations . We validated the results with a spatially explicit study on groundwater recharge, a modeled average for the period from 1951 to 1980, for the conterminous US with a resolution of one km  and with two other studies [91,92] with more recent indicative ranges of groundwater recharge for larger regions including the targeted watersheds.
- Natural or semi-natural forest (counterfactual)
- Plantation forestry (only the Satilla watershed)
- Corn and winter wheat (only the Big Sunflower watershed)
- Agricultural land (other)
We calculated the arithmetic mean ESS supply for these major land use/land cover classes and normalized them to the maximum value in each ESS category for each watershed. We conducted this analysis to assess the differences between targeted land use/land cover classes. In addition, the paired Pearson correlation coefficients between the ESS, selected from the list of methods in Mouchet et al. , were calculated for the entire watershed with the statistical software package R  to assess general ESS and biodiversity trade-offs in current production systems specialized in plantation forestry and agriculture respectively.
Because we considered two significantly different land use systems, it was reasonable to have a counterfactual, which served as a baseline to compare several alternatives of natural or semi-natural forest. This approach is recommended to test the suitability of bioenergy feedstock production options in the local hydrological context  or for biodiversity .
Indicators at the plot and landscape scale that potentially explain variation in ecosystem service supply
In this study, we tested indicators of landscape composition, configuration and naturalness for their influence on ESS supply in both watersheds (see Table 1). Therefore, we calculated the landscape composition and configuration indicators in a moving window approach for a buffer of 300 m, which was ten times the minimum pixel size . At the plot scale, potential explanatory variables of topography and soil properties were used to set the explanatory value of landscape scale variables in the context of other groups of variables driving ESS supply (see Table 1). Landscape composition was defined as the quantity, and landscape configuration was defined as the relevant shape or form of different land use/land cover classes [89,102]. Landscape naturalness was defined as the degree of human influence or impact on a natural system . In addition to the selected explanatory variables used by others for landscape naturalness, we rated the land use intensity partly based on Brockerhoff et al.  as follows: urban (5), agricultural land (4), plantation forestry (3), open water (2) and primary or secondary natural vegetation (1). We calculated landscape metrics using Fragstats 4.1  and R  based on the land use/land cover classes indicated in the following formula and the data source in Table 1. We modified the urbanity indicator from Wrbka et al. : where U is urban, A is agricultural land, P is plantation forestry, F is forestry, SG is shrub and grassland, W is open water, and B is barren land.
We applied a redundancy analysis (RDA) to identify explanatory values of plot and landscape factors on the variability of ESS supply in the selected case study regions. We chose the RDA because it allows us to (i) estimate the impact of the explanatory variable on ESS supply and vertebrate species richness simultaneously. A more complex alternative, machine learning methods, e.g., boosted regression trees, may only be applied to one response variable . (ii) RDA allows to control for multicollinearity among explanatory variables [95,105]. To consider nonlinear relationships between explanatory variables, we tested also the second degree terms of the potential explanatory variables as recommended by Borcard et al. . We reduced the number of explanatory variables based on the permutation of p-values (p<0.05; 1000 permutations per step) as described by Blanchet et al. , which is used instead of the Akaike information criterion (AIC) to select explanatory variables. We used the former method as it delimits the type I error and provides reliable results for non-orthogonal and non-independent explanatory variables . We partitioned the variation into the following groups: plot indicators (topography and soil properties), indicators on landscape composition, landscape configuration and naturalness. To test for spatial autocorrelation, we added the latitudinal and longitudinal coordinates and their interaction as an additional group .
Sites of sufficient and insufficient ecosystem service supply
Villa et al.  argued that the benefits from ESS to society are particularly relevant if thresholds or target values, e.g., regarding drinking water quality or good ecological status, are closely met or exceeded. Therefore, we use these thresholds, if available, to distinguish sites of sufficient and insufficient ESS supply. If thresholds are set following representative stakeholder consultation, it may be assumed that they reflect the demand for regulating ESS. In the context of bioenergy, it has been shown that common tools for assessing environmental sustainability, i.e., certification schemes, largely miss such thresholds .
The thresholds must be identified at the impact scale of the beneficiaries of ESS, which is the global scale for carbon storage as a factor influencing the global climate. By contrast, the regional or watershed level is relevant for P and sediment retention and groundwater recharge . Typically, P and sediment loading thresholds are set as the Total Maximum Daily Loadings for most of the surface water pollutant and are translated to land-based thresholds, e.g., sediment yields/soil erosion rates and P export rates, as indicated in Table 2. Because sediment loadings do not have thresholds in the Satilla watershed as a minor environmental concern, we did not include sediment export as an indicator for identifying sites of sufficient and insufficient ESS supply in the Satilla watershed.
Carbon storage of the current land use/land cover was compared with potential natural vegetation , following West et al. , i.e., sites of sufficient ESS supply are those with a gain in carbon storage for the current land use/land cover toward potential natural vegetation. Such a conservative classification of sites of sufficient and insufficient carbon storage should avoid that the conversion of naturally high carbon stocked land cover types, such as native forests, is viewed as beneficial.
In contrast to the investigated regulating ESS, P and sediment retention, groundwater recharge is an ESS that requires longer time scales to be generated. Therefore, land use activities may have longer lag phases before the consequences become apparent. Groundwater resources are declining due to human groundwater abstraction at both study sites [110–112]. Therefore, higher recharge rates are beneficial. Biodiversity may support other ESS or may be an ESS itself, as discussed in the materials and methods section. Biodiversity as a cultural ESS is highly subjective and strongly varies between stakeholder groups, i.e., among farmers, nature conservation activists, other citizens , species or species groups . Facing these limitations, we use the arithmetic mean for both groundwater recharge and biodiversity as the indicative threshold between sufficient and insufficient supply, i.e., assuming that a higher supply is more beneficial.
To explain differences between sites of sufficient and insufficient ESS supply as defined in the materials and methods section, we followed Qiu and Turner  and set beneficial sites to one and non-beneficial sites to zero and applied a binomial logistic regression model. We conducted a binomial logistic regression in addition to the RDA since it (i) reflects the case of ESS supply and biodiversity supply relevant in practice, i.e., above and below a threshold or target value and (ii) allows to identify the direction of the impact, i.e., positive or negative on ESS supply. (iii) It is computationally more feasible for larger datasets as in this study than machine learning techniques, e.g., boosted regression trees, and (iv) commonly used in ESS research . We focused on maximizing the bundle of relevant ESS instead of a single ESS. Maximizing bundles of ESS, particularly if regulating services are included, is more likely to ensure the stability of ESS supply, e.g., during sudden changes in environmental conditions. Maximized bundles may also avoid strong tradeoffs toward maximizing single ESS . We removed non-significant explanatory (p<0.05) variables in a backward stepwise manner based on the AIC. Next, variables with variance inflation factors >10 were removed to reduce multicollinearity. The significance of the final model was tested against a null model using a likelihood ratio test. We used the same indicators as those for the RDA to differentiate between sites of sufficient and insufficient ESS supply.
Ecosystem service supply in the Satilla and Big Sunflower watersheds
Examining the plantation forestry system (Satilla watershed) (left) and the agricultural production system (Big Sunflower watershed) (right); c.f. Fig. 2A, E, F, J, K, and O., we observed that carbon storage and vertebrate diversity were much higher in the Satilla watershed. In contrast, groundwater recharge and sediment retention were mostly higher in the Big Sunflower watershed; c.f. Fig. 2C, D, H, I, M, and N. P retention was only slightly higher but varied more in the Big Sunflower watershed. If burning was avoided, the potential GHG emission would be reduced by up to 34,000 t for winter wheat and 130,000 t for corn (CO2-equivalents (2006); see Table 3.
Mapped P and Sediment retention are plotted with breaks at 0.1, 1, 10 and 100 for better visualization.
The modeled annual P export rates explained approximately 90% of the average P concentrations from the empirical data (Fig. 3A). The modeled sediment export rates explained between 78 and 90% of the total suspended solid concentration (Fig. 3B). The modeled groundwater recharge rates for both watersheds were in the range of the existing studies, as shown in Fig. 3C, D.
Tradeoffs of ecosystem service supply
In the Satilla watershed, plantation forestry had a slightly lower mean carbon storage and vertebrate diversity than did natural- or semi-natural forests and the counterfactual; c.f. Fig. 4B, C. The plantation forestry had a higher vertebrate diversity and carbon storage than did the agricultural land and watershed average; c.f. Fig. 4A, D. By contrast, groundwater recharge was higher for plantation forestry than for forests. The P and sediment retention were negligible compared with agricultural land and the watershed average for both plantation forestry and forests. A paired correlation analysis for a sample of 10,000 pixels from all land use/land cover classes showed a high positive correlation between carbon storage and vertebrate diversity (S1 Fig.). A high negative correlation between groundwater recharge and both vertebrate diversity and carbon storage can be observed.
The highest arithmetic mean value for each ESS category is used maximum to scale the radar charts for the Satilla (a-d) and Big Sunflower watersheds (e-h) separately.
In the Big Sunflower watershed, corn and wheat production had a significantly lower mean carbon storage, vertebrate diversity and P retention than did forests (Fig. 4F, G). By contrast, the sediment retention and groundwater recharge were higher for corn and wheat production than for forests. A paired correlation analysis for a sample of 10,000 pixels from all land use/land cover classes showed a high positive correlation between carbon storage and vertebrate diversity (S2 Fig.). A lower negative correlation between groundwater recharge and both vertebrate diversity and carbon storage can be observed.
The influence of topography and soil properties, landscape composition, configuration and naturalness on ecosystem service supply
p<0.01 and values <0 are not shown; the indicated values display the variance captured by the indicator groups on landscape composition, naturalness, landscape configuration, topography and soil parameters selected from Table 1; the indicators were selected based on permutation p-values; the variance is captured as adjusted R² for single (non-overlapping areas) and combined categories (overlapping areas).
The RDA without geographic information for the Satilla watershed (Fig. 5A) as a plantation forestry system showed that the landscape naturalness, i.e., the land use gradient and the hemeroby index (human impact), only explained 10%, and if combined with other indicator groups, a further 20% of the variation in the ESS supply was explained. Landscape composition only explained 4%, and if combined with other indicator groups, 18% of variation in the ESS supply was explained. The selected indicators are the largest patch index for agricultural land and shrub- and grassland. The landscape configuration explained less than 1%, and if combined with other indicator groups, 10% of the variation was explained. The selected indicators are the effective mesh size of shrub- and grassland and water bodies as well as the landscape shape index of forest, plantation forestry and agricultural land. The topography and soil factors explained 4%, and if combined with other indicator groups, 14%.
The RDA without geographic information (Fig. 5B) for the Big Sunflower watershed as an agricultural system showed that the landscape naturalness, i.e., the land use gradient, explained 23%, and if combined with other groups, a further 49% of the variation in the ESS supply was explained. The landscape composition explained 2%, and if combined with other groups, explained a further 48%. The selected indicators are the largest patch index for agricultural land, urban land and water, the edge density for forest and for other land use/land cover categories as well as the Shannon’s diversity of land use/land cover. The landscape configuration and other indicator groups explained 52% of the variation. The selected indicators are the effective mesh size for forest and the landscape shape index for agricultural land. Topography and soil factors were of minor importance.
Plot and landscape characteristics to distinguish sites of sufficient and insufficient ESS supply
In total, 0.2% of the area of the Big Sunflower watershed had sufficient ESS supply, and 0.9% had insufficient ESS supply. The results for the overall area are shown in the previous section. Corn and wheat production, i.e., 4% of the area of the Big Sunflower watershed, accounted for 1% of the sites of sufficient ESS supply and 5% of the sites of insufficient ESS supply. The major landscape scale factors that promoted sufficient ESS supply were a higher effective mesh size of forests, a higher landscape shape index for agricultural land and a higher edge density of shrub, grassland and water bodies (Table 4). By contrast, a higher land use intensity, a higher edge density of forests and higher landscape shape indices for urban land promoted insufficient ESS supply at the landscape scale. A higher share of corn and wheat production slightly favored insufficient ESS supply. At the plot scale, the higher slope may be associated with insufficient ESS supply.
In total, 0.1% of the area of the Satilla watershed showed sufficient ESS supply, and 0.6% showed insufficient ESS supply. The plantation forestry, i.e., 28% of the area of the Satilla watershed in 2006, accounted for 19% of the sites of sufficient ESS supply and for 1.6% of the sites of insufficient ESS supply. The major landscape scale factors that were favorable for a sufficient ESS supply were a higher edge density as well as a high largest patch index of forest and plantation forestry (S1 Table). At the plot scale, a higher available water holding capacity and a higher depth to water table were beneficial. In contrast, a higher landscape shape index of forests, a greater land use intensity, a higher share of wetlands and a higher largest patch index of agricultural land promoted insufficient ESS supply at the landscape scale.
The likelihood ratio tests showed a significant difference when compared to a null model for the Big Sunflower watershed (χ2 = 20440, df = 18, p<2.2e-16) and the Satilla (χ2 = 35944, df = 22, p<2.2e-16) (the set of explanatory variables shown in Table 4 and S1 Table had a significant explanatory value when compared against the model without explanatory variables).
Ecosystem service supply synergies and tradeoffs
The higher carbon storage and biodiversity in the Satilla watershed may be related to the higher resemblance of plantation forestry to natural or semi-natural forest, see . Higher P and sediment retention in the Big Sunflower watershed are attributable to the higher P application and bare soil in agricultural production systems, resulting in a higher demand for related regulating services, see Fig. 3A, B. The higher rate of groundwater decline in the Big Sunflower watershed  hints at a stronger mismatch of groundwater abstraction and recharge compared with the Satilla watershed.
Generally, tradeoffs for agricultural production systems have been shown in other studies, e.g., [14,15,116,117], but not for plantation forestry or for the intensive feedstock production systems evaluated in this study. Overall, the plantation forestry deviates less from the counterfactual natural or semi-natural forest than from agricultural production systems such as corn and wheat; thus, we conclude that the plantation forestry system is preferable for the modeled ESS bundle and biodiversity.
Advantages and constraints of the ecosystem service modeling scheme
We achieved the models’ purpose of providing a broad picture of water quality  and of assessing annual groundwater recharge rates . For such application, we achieved a reasonably good validity (Fig. 3); our results are comparable with those of Qiu and Turner  and Terrado et al. . In addition, simple tools such as InVEST are more likely to be an option for practitioners for regional scale assessments , e.g., for bioenergy, agricultural or forestry production systems, compared to significantly more complex and resource-intensive models such as the Soil-Water Assessment Tool (SWAT) . For example, InVEST may be used in data scarce situations without monthly or daily precipitation data, the latter required by SWAT for nutrient and sediment modeling. Therefore, this study design is suitable for regions with high or low data availability, which will facilitate comparable analyses for bioenergy production systems around the world to compare ESS supply and biodiversity, e.g., within this study. However, tools such as InVEST or SWB do not support simulation studies requiring numerous runs to find Pareto optimal solutions of ESS supply, e.g., , or biodiversity, e.g., .
Considering only the higher biomass yield of pine plantations and the lower yields from corn stover and cereal straw , the smaller tradeoffs of pine plantations may be seen as preferable than agricultural biomass at first glance. Bennett and Balvanera  similarly argued that the tradeoffs of provisioning ESS should be minimized to ensure a balanced ESS supply. Focusing on the yield, i.e., for bioenergy, and the environmental side may disregard the social side of the “food, energy and environment trilemma” . This trilemma may be solved if (i) there are no competing uses of wheat straw or corn stover [21,39] and (ii) if both corn stover and wheat straw are produced regardless; the identified ESS tradeoffs with forests do not exclusively need to be attributed to a potentially used residual biomass.
Benefits of avoided and potential further competition for biomass
Due to the missing competing uses for the agricultural residues in the Mississippi Delta, their potential use for bioenergy instead of burning may create synergies. For example, (i) negative impacts on soil structure, local microbiology, the water holding capacity of soil and soil fertility from burning could be avoided [123,124], and (ii) we could reduce GHG emissions or at least generate energy as an additional use. However, the actual sustainable residue removal rates and GHG emissions depend on the local environmental conditions, e.g., soil organic carbon or water availability and conversion and use aspects, e.g., the harvesting technique, transportation and the type of energy carrier. Therefore, further studies may integrate results from this study into life-cycle assessments to compare these iLUC free bioenergy feedstocks with a fossil fuel energy carrier. For the plantation forestry system, future research may investigate (i) the global production pattern changes due to the decline of the pulp and paper industry in the southeastern US to identify potential indirect impacts, such as iLUC, and (ii) the ESS supply and tradeoffs of current and future pulp and paper exporting regions of the world that partly substitute production capacities in the southeastern US and that may be of interest; e.g., Eucalyptus plantations in Brazil or some parts of sub-Saharan Africa may reveal other economic, social or environmental issues.
Factors explaining the variance of ecosystem service supply
We confirmed the hypothesis of Frank et al.  that the degree of naturalness of the landscape affects ESS supply. Wrbka et al.  previously demonstrated this relation for the human appropriation of net primary productivity, e.g., biomass use. The impact of landscape composition and configuration on ESS supply was only slightly less important, as proposed by Syrbe and Walz  and Frank et al. , e.g., the largest patch index, the effective mesh size or the landscape shape index in both watersheds. For example, in the Satilla watershed, the substantial influence of the largest patch index of agricultural land and of the effective mesh size of shrub and grassland habitats have shown that not only the existence but also the location and connection of shrub and grassland patches are important for ESS supply. Further influential factors related to the climate are not considered in this study because both case studies are in the same humid subtropical climate zone according to Koppen-Geiger ; however, this may be reasonable for case studies with climatic gradients, e.g., , or when comparing case studies in different climate zones, e.g., a humid subtropical climate compared with a semi-arid tropical climate.
Thresholds and local demand for ecosystem services
To link ESS supply to the local demand, we related the actual supply to locally set environmental thresholds when available for sediment and P concentrations in surface waters, as in Terrado et al. . Considering local preferences may more likely allow us to determine whether ESS provide a human benefit. However, this consideration is not regularly performed in ESS modeling, see, e.g., [3,15]. Such socially accepted environmental thresholds for groundwater recharge or biodiversity.
When comparing the sites above and below thresholds, the plantation forestry contributed to sufficient ESS supply. In the Big Sunflower watershed, ESS supply may be enhanced by a higher complexity of agricultural patches. It simultaneously requires combining agricultural land with, e.g., shrub and grassland or forest patches rather than urban land, as shown by the negative impact of increasing land use intensity. This is supported by the beneficial effect of an increase in size and number of shrub and grassland patches. It is indirectly shown by the beneficial effect of a higher edge density and a higher effective mesh size of forest patches. In the Satilla watershed, it may be beneficial to increase the size and connectivity of forest patches. By contrast, it does not seem beneficial to enhance the complexity of forest patches. This may be explained by the fact that more complex forest patches have a larger share of non-forest land use, e.g., pine plantations, agricultural or urban land. These results are in line with the results of the tradeoff analysis showing the higher supply of carbon storage and biodiversity toward plantation forestry. However, a higher dominance of agricultural land decreases ESS supply, whereas plantation forestry still increases ESS supply. Future research should assess the relevance of landscape composition and configuration and naturalness of the landscape in other solid biomass production systems in other parts of the world.
In practice, the rules of certification schemes or the rules set by local authorities in landscape planning should include rules on landscape composition and configuration. It may be reasonable to consider an additional assessment of ESS supply at the landscape scale in improved certification schemes, e.g., for bioenergy. An assessment at the plot scale of the individual feedstock producer seems incomplete. Even if the assessment would go beyond the management practices, the local environmental factors, topography and soil parameters explained only a small share of the variation in ESS supply. For example, preserving or creating a landscape mosaic may better balance the supply of ESS beyond the bioenergy feedstock in the production region. One concrete option could be a higher number of connected forest patches as buffer strips alongside rivers in the Big Sunflower watershed or other natural vegetation, such as grassland in agricultural watersheds . For the Satilla river, we may see forested buffer strips in Fig. 1, which are required in Georgia’s Mountain and River Corridor Protection Act . Another strategy to reduce the intensity of agricultural production could be 2nd generation bioenergy feedstocks, such as perennial bioenergy grasses or short rotation coppice species. Such bioenergy-providing species may provide both biomass and higher ESS (sediment and nutrient retention) and biodiversity, c.f. [4,31].
Potential future use of indicators on landscape structure
We suggest including indicators of landscape structure to ensure a harmonized level of sustainability in certification schemes, which is particularly relevant if the biomass is largely traded, e.g., wood pellets in the form of pine plantations in the southeast US; they should also be subjected to legal frameworks, which are currently absent or variable, for landscape planning. For a broader application in sustainability assessments beyond bioenergy, the impact of landscape structure on ESS supply should be tested in other agricultural or forest production systems.
S1 Fig. Paired correlation analysis of ESS supply in the Satilla watershed (p<0.001 (***); p<0.01 (**), p<0.05 (*)).
S2 Fig. Paired correlation analysis of ESS supply in the Big Sunflower watershed (p<0.001 (***); p<0.01 (**), p<0.05 (*)).
S1 Table. Factors characterizing sufficient and insufficient ESS supply in the Satilla watershed (backward logistic regression).
A positive value for the standardized β indicates that an explanatory variable is contributing to sufficient ESS supply; a negative value for the standardized β indicates that an explanatory variable is contributing to insufficient ESS supply.
The authors would like to thank Charlotte Main for partial literature review and data preparation. The authors thank Ralf Seppelt, Daniel Doktor, and the reviewers for helpful comments on earlier drafts of this manuscript.
Conceived and designed the experiments: MAM TC JAP. Performed the experiments: MAM. Analyzed the data: MAM. Wrote the paper: MAM TC. Contributed to revisions of the manuscript: JAP.
- 1. MEA Board, editor (2005) Ecosystems and human well-being: current state and trends: findings of the condition and trends working group. Washington, DC: Island Press.
- 2. Gasparatos A, Stromberg P, Takeuchi K (2011) Biofuels, ecosystem services and human wellbeing: Putting biofuels in the ecosystem services narrative. Agriculture, Ecosystems & Environment 142: 111–128.
- 3. Meehan TD, Gratton C, Diehl E, Hunt ND, Mooney DF, et al. (2013) Ecosystem-Service Tradeoffs Associated with Switching from Annual to Perennial Energy Crops in Riparian Zones of the US Midwest. PLoS ONE 8: e80093. pmid:24223215
- 4. Werling BP, Dickson TL, Isaacs R, Gaines H, Gratton C, et al. (2014) Perennial grasslands enhance biodiversity and multiple ecosystem services in bioenergy landscapes. Proceedings of the National Academy of Sciences.
- 5. Chum H, Faaij A, Moreira J, Berndes G, Dhamija P, et al. (2011) Bioenergy. In: Edenhofer O, Pichs-Madruga R, Sokona Y, Seyboth K, Matschoss P et al., editors. IPCC Special Report on Renewable Energy Sources and Climate Change Mitigation. Cambridge, United Kingdom and New York, NY, USA: Cambridge University Press.
- 6. Lamers P, Junginger M, Hamelinck C, Faaij A (2012) Developments in international solid biofuel trade—An analysis of volumes, policies, and market factors. Renewable and Sustainable Energy Reviews 16: 3176–3199.
- 7. Goh CS, Junginger M, Cocchi M, Marchal D, Thrän D, et al. (2013) Wood pellet market and trade: a global perspective. Biofuels, Bioproducts and Biorefining 7: 24–42.
- 8. Diaz-Chavez R, Berndes G, Neary D, Elia Neto A, Fall M (2011) Water quality assessment of bioenergy production. Biofuels, Bioproducts and Biorefining 5: 445–463.
- 9. Meyfroidt P, Rudel TK, Lambin EF (2010) Forest transitions, trade, and the global displacement of land use. Proceedings of the National Academy of Sciences 107: 20917–20922. pmid:21078977
- 10. Brockerhoff EG, Jactel H, Parrotta JA, Ferraz SFB (2013) Role of eucalypt and other planted forests in biodiversity conservation and the provision of biodiversity-related ecosystem services. Forest Ecology and Management 301: 43–50.
- 11. Bringezu S, O’Brien M, Schütz H (2012) Beyond biofuels: Assessing global land use for domestic consumption of biomass: A conceptual and empirical contribution to sustainable management of global resources. Land Use Policy 29: 224–232.
- 12. Meyer MA, Priess JA (2014) Indicators of bioenergy-related certification schemes – An analysis of the quality and comprehensiveness for assessing local/regional environmental impacts. Biomass and Bioenergy 65: 151–169.
- 13. Lamers P, Thiffault E, Paré D, Junginger M (2013) Feedstock specific environmental risk levels related to biomass extraction for energy from boreal and temperate forests. Biomass and Bioenergy 55: 212–226.
- 14. Qiu J, Turner MG (2013) Spatial interactions among ecosystem services in an urbanizing agricultural watershed. Proceedings of the National Academy of Sciences 110: 12149–12154. pmid:23818612
- 15. Raudsepp-Hearne C, Peterson GD, Bennett EM (2010) Ecosystem service bundles for analyzing tradeoffs in diverse landscapes. Proceedings of the National Academy of Sciences 107: 5242–5247. pmid:20194739
- 16. Bennett EM, Balvanera P (2007) The future of production systems in a globalized world. Frontiers in Ecology and the Environment 5: 191–198.
- 17. Foley JA, DeFries R, Asner GP, Barford C, Bonan G, et al. (2005) Global Consequences of Land Use. Science 309: 570–574. pmid:16040698
- 18. Kremen C, Miles A (2012) Ecosystem Services in Biologically Diversified versus Conventional Farming Systems: Benefits, Externalities, and Trade-Offs. Ecology and Society 17.
- 19. Junginger M, van Dam J, Zarrilli S, Ali Mohamed F, Marchal D, et al. (2011) Opportunities and barriers for international bioenergy trade. Energy Policy 39: 2028–2042.
- 20. Muth DJ Jr, Bryden KM, Nelson RG (2013) Sustainable agricultural residue removal for bioenergy: A spatially comprehensive US national assessment. Applied Energy 102: 403–417. pmid:23237846
- 21. Tilman D, Socolow R, Foley JA, Hill J, Larson E, et al. (2009) Beneficial Biofuels—The Food, Energy, and Environment Trilemma. Science 325: 270–271. pmid:19608900
- 22. Fonseca MB, Burrell A, Gay H, Henseler M, Kavallari A, et al. (2010) Impacts of the EU biofuel target on agricultural markets and land use: a comparative modelling assessment. Luxembourg: JRC-Institute for Prospective Technological Studies.
- 23. Goldman RL, Thompson BH, Daily GC (2007) Institutional incentives for managing the landscape: Inducing cooperation for the production of ecosystem services. Ecological Economics 64: 333–343.
- 24. Zhang W, Ricketts TH, Kremen C, Carney K, Swinton SM (2007) Ecosystem services and dis-services to agriculture. Ecological Economics 64: 253–260.
- 25. Tscharntke T, Klein AM, Kruess A, Steffan-Dewenter I, Thies C (2005) Landscape perspectives on agricultural intensification and biodiversity – ecosystem service management. Ecology Letters 8: 857–874.
- 26. Lewandowski I, Faaij APC (2006) Steps towards the development of a certification system for sustainable bio-energy trade. Biomass and Bioenergy 30: 83–104.
- 27. van Dam J, Junginger M, Faaij APC (2010) From the global efforts on certification of bioenergy towards an integrated approach based on sustainable land use planning. Renewable and Sustainable Energy Reviews 14: 2445–2472.
- 28. Tscharntke T, Milder JC, Schroth G, Clough Y, DeClerck F, et al. (2014) Conserving biodiversity through certification of tropical agroforestry crops at local and landscape scales. Conservation Letters: n/a-n/a.
- 29. Ghazoul J, Garcia C, Kushalappa CG (2009) Landscape labelling: A concept for next-generation payment for ecosystem service schemes. Forest Ecology and Management 258: 1889–1895.
- 30. Mitchell ME, Bennett E, Gonzalez A (2013) Linking Landscape Connectivity and Ecosystem Service Provision: Current Knowledge and Research Gaps. Ecosystems 16: 894–908.
- 31. Manning P, Taylor G, E. Hanley M (2014) Bioenergy, Food Production and Biodiversity – An Unlikely Alliance? GCB Bioenergy: n/a-n/a.
- 32. Frank S, Fürst C, Witt A, Koschke L, Makeschin F (2014) Making use of the ecosystem services concept in regional planning—trade-offs from reducing water erosion. Landscape Ecology: 1–15.
- 33. Bourke D, Stanley D, O'Rourke E, Thompson R, Carnus T, et al. (2014) Response of farmland biodiversity to the introduction of bioenergy crops: effects of local factors and surrounding landscape context. GCB Bioenergy 6: 275–289.
- 34. Brockerhoff E, Jactel H, Parrotta J, Quine C, Sayer J (2008) Plantation forests and biodiversity: oxymoron or opportunity? Biodiversity and Conservation 17: 925–951.
- 35. USGS and USDOI (2010) Landfire 1.2.0—Environmental Site Potential layer. Available: http://landfire.cr.usgs.gov/viewer/. Accessed 15 January 2014.
- 36. Susaeta A, Lal P, Alavalapati J, Carter DR (2013) Modelling the impacts of bioenergy markets on the forest industry in the southern United States. International Journal of Sustainable Energy 32: 544–561.
- 37. Snipes CE, Nichols SP, Poston DH, Walker TW, Evans LP, et al. (2005) Current Agricultural practices of the Mississippi Delta. Prairie: Mississippi Agricultural and Forestry Experiment Station.
- 38. USDA NASS (2014) Corn and winter wheat production in bushels for Mississippi and the Upper Delta and the Lower Delta 2013. Available: http://quickstats.nass.usda.gov. Accessed 20 May 2014.
- 39. Perlack RD, Stokes B, Downing M, Eaton LM, Graham RL, et al. (2011) U.S. Billion-Ton Update: Biomass Supply for a Bioenergy and Bioproducts Industry. Oak Ridge: Oak Ridge National Laboratory.
- 40. Daly C, Halbleib M, Smith JI, Gibson WP, Doggett MK, et al. (2008) Physiographically sensitive mapping of climatological temperature and precipitation across the conterminous United States. International Journal of Climatology 28: 2031–2064.
- 41. CICES (2013) Common International Classification of Ecosystem Services. Available: http://cices.eu/. Accessed 15 January 2013.
- 42. Scarlat N, Dallemand J-F (2011) Recent developments of biofuels/bioenergy sustainability certification: A global overview. Energy Policy 39: 1630–1646.
- 43. McBride AC, Dale VH, Baskaran LM, Downing ME, Eaton LM, et al. (2011) Indicators to support environmental sustainability of bioenergy systems. Ecological Indicators 11: 1277–1289.
- 44. Efroymson R, Dale V, Kline K, McBride A, Bielicki J, et al. (2013) Environmental Indicators of Biofuel Sustainability: What About Context? Environmental Management 51: 291–306. pmid:22824960
- 45. Dale VH, Polasky S (2007) Measures of the effects of agricultural practices on ecosystem services. Ecological Economics 64: 286–296.
- 46. Alexander RB, Smith RA, Schwarz GE, Boyer EW, Nolan JV, et al. (2008) Differences in Phosphorus and Nitrogen Delivery to The Gulf of Mexico from the Mississippi River Basin. Environmental Science & Technology 42: 822–830.
- 47. Cardinale BJ, Duffy JE, Gonzalez A, Hooper DU, Perrings C, et al. (2012) Biodiversity loss and its impact on humanity. Nature 486: 59–67. pmid:22678280
- 48. Maes J, Paracchini ML, Zulian G, Dunbar MB, Alkemade R (2012) Synergies and trade-offs between ecosystem service supply, biodiversity, and habitat conservation status in Europe. Biological Conservation 155: 1–12.
- 49. Graham RL, Nelson R, Sheehan J, Perlack RD, Wright LL (2007) Current and Potential U.S. Corn Stover Supplies. Agron J 99: 1–11.
- 50. Kadam KL, McMillan JD (2003) Availability of corn stover as a sustainable feedstock for bioethanol production. Bioresource Technology 88: 17–25. pmid:12573559
- 51. McCarty JL (2011) Remote Sensing-Based Estimates of Annual and Seasonal Emissions from Crop Residue Burning in the Contiguous United States. Journal of the Air & Waste Management Association 61: 22–34.
- 52. Nelson E, Mendoza G, Regetz J, Polasky S, Tallis H, et al. (2009) Modeling multiple ecosystem services, biodiversity conservation, commodity production, and tradeoffs at landscape scales. Frontiers in Ecology and the Environment 7: 4–11.
- 53. Kareiva P, Tallis H, Ricketts TH, Daily GC, Polasky S (2011) Natural Capital: Theory and Practice of Mapping Ecosystem Services. Oxford: Oxford University Press.
- 54. Bridgham S, Megonigal JP, Keller J, Bliss N, Trettin C (2006) The carbon balance of North American wetlands. Wetlands 26: 889–916.
- 55. Ruesch A, Gibbs H (2008) New IPCC Tier-1 Global Biomass Carbon Map for the Year 2000. Available: http://cdiac.ornl.gov/epubs/ndp/global_carbon/carbon_documentation.html. Accessed 14 January 2014.
- 56. Sainju UM, Whitehead WF, Singh BP (2005) Carbon accumulation in cotton, sorghum, and underlying soil as influenced by tillage, cover crops, and nitrogen fertilization. Plant and Soil 273: 219–234.
- 57. Smith JE, Heath LS, Skog KE, Birdsey RA (2006) Methods for Calculating Forest Ecosystem and Harvested Carbon with Standard Estimates for Forest Types of the United States. Delaware: Northern Research Station. pmid:16705966
- 58. Eggleston HS, Buendia L, Miwa K, Ngara T, Tanabe K (2006) 2006 IPCC Guidelines for National Greenhouse Gas Inventories. Paris.
- 59. Franzluebbers AJ (2005) Soil organic carbon sequestration and agricultural greenhouse gas emissions in the southeastern USA. Soil and Tillage Research 83: 120–147.
- 60. Birdsey RA (1992) Carbon Storage and Accumulation in United States Forest Ecosystems. Radnor: Northeastern Forest Experiment Station.
- 61. USGS GAP (2011) National Land Cover, Version 2. Available: http://gapanalysis.usgs.gov/gaplandcover/data/. Accessed 25 November 2013.
- 62. USDA NASS (2010) Cropland Data Layer (CDL). Available: www.nass.usda.gov/research/Cropland/SARS1a.htm. Accessed 20 November 2013.
- 63. Lehner B, Verdin K, Jarvis A (2008) New Global Hydrography Derived From Spaceborne Elevation Data. Eos, Transactions American Geophysical Union 89: 93–94.
- 64. FAO Geonetwork (2004) Global map of monthly reference evapotranspiration—10 arc minutes (GeoLayer). Available: http://www.fao.org/geonetwork/srv/en/main.home. Accessed 20 January 2014.
- 65. USDA NRCS (2014) Web Soil Survey—Soil Survey Geographic (SSURGO) Database. Available: http://websoilsurvey.nrcs.usda.gov/. Accessed 20 January 2014.
- 66. Allen RG, Pereira LS, Raes D, Smith M (2001) Crop evapotranspiration—Guidelines for computing crop water requirements. Rome.
- 67. Scurlock JMO, Asner GP, Gower ST (2001) Worldwide Historical Estimates of Leaf Area Index, 1932–2000. Oak Ridge Oak Ridge National Laboratory.
- 68. Canadell J, Jackson RB, Ehleringer JB, Mooney HA, Sala OE, et al. (1996) Maximum rooting depth of vegetation types at the global scale. Oecologia 108: 583–595.
- 69. Schenk HJ, Jackson RB (2002) The Global Biogeography of Roots. Ecological Monographs 72: 311–328.
- 70. Mishra HS, Rathore TR, Pant RC (1997) Root growth, water potential, and yield of irrigated rice. Irrigation Science 17: 69–75.
- 71. Natural Resources Conservation Service (NRCS) (2012) Engineering Field Handbook. Washington, DC: U.S. Department of Agriculture,.
- 72. Burns LA, Allen BW, Barber MC, Bird SL, Cheplick JM, et al. (1992) Pesticide and Industrial Chemical Risk Analysis and Hazard Assessment, Version 3.0. Athens: Environmental Research Laboratory, Office of Research and Development.
- 73. Campbell Group (2013) Juvenile Pine Plantation Fertilization recommendations. [Unpublished work]
- 74. Harmel D, Potter S, Casebolt P, Reckhow K, Green C, et al. (2006) Compilaton of measured nutrient load data for agricultural land uses in the United States. JAWRA Journal of the American Water Resources Association 42: 1163–1178.
- 75. Reckhow KH, Beaulac M, Simpson J (1980) Modeling Phosphorous Loading and Lake Response under Uncertainty: A Manual and Compilation of Export Coefficients Washington, DC.
- 76. Tallis HT, Ricketts T, Guerry AD, Wood SA, Sharp R, et al. (2013) InVEST 2.5.6 User’s Guide. Stanford.
- 77. Wischmeier WH, Smith DD (1978) Predicting rainfall erosion losses: A guide to conservation planning. Washington, DC.
- 78. Roose E (1996) Land husbandry—Components and strategy. Rome.
- 79. Perica S, Martin D, Pavlovic S, Roy I, St. Laurent M, et al. (2013) Precipitation-Frequency Atlas of the United States. Silver Spring: National Weather Service.
- 80. USDA NRCS and ARS (2000) Revised Universal Soil Loss Equation (RUSLE) EPA Pesticide Project. National Resources Conservation Service and Agricultural Research Service
- 81. USDA NRCS (2002) C Factor used for erosion prediction in Michigan. Available: http://www.iwr.msu.edu/rusle/doc/cfactors.pdf. Accessed 20 January 2014.
- 82. Martin A, Gunter J, Regens J (2003) Estimating erosion in a riverine watershed bayou liberty-tchefuncta river in louisiana. Environmental Science and Pollution Research 10: 245–250. pmid:12943008
- 83. Morgan R (2005) Soil erosion and conservation. Oxford: Wiley-Blackwell.
- 84. Fernandez C, Wu JQ, McCool DK, Stöckle CO (2003) Estimating water erosion and sediment yield with GIS, RUSLE, and SEDD. Journal of Soil and Water Conservation 58: 128–136.
- 85. Dissmeyer GE, Foster GR (1984) A guide for predicting sheet and rill erosion on forest land. Forest Service, Southern Region.
- 86. Suárez LA (2005) PRZM-3, A Model for Predicting Pesticide and Nitrogen Fate in the Crop Root and Unsaturated Soil Zones: Users Manual for Release 3.12.2. Washington, DC: Ecosystems Research Division, National Exposure Research Laboratory.
- 87. Westenbroek SM, Kelson VA, Dripps WR, Hunt RJ, Bradbury KR (2010) SWB—A modified Thornthwaite-Mater Soil-Water-Balance code for estimating groundwater recharge. Reston.
- 88. Dripps WR, Bradbury KR (2007) A simple daily soil–water balance model for estimating the spatial and temporal distribution of groundwater recharge in temperate humid areas. Hydrogeology Journal 15: 433–444.
- 89. Menne MJ, Durre I, Vose RS, Gleason BE, Houston TG (2012) An Overview of the Global Historical Climatology Network-Daily Database. Journal of Atmospheric and Oceanic Technology 29: 897–910.
- 90. Wolock DM (2003) Estimated mean annual natural ground-water recharge in the conterminous United States. Available: http://water.usgs.gov/lookup/getspatial?rech48grd. Accessed 25 March 2014.
- 91. Priest S (2004) Evaluation of ground-water contribution to streamflow in coastal Georgia and adjacent parts of Florida and South Carolina. Reston.
- 92. Welch H, Green C, Coupe R (2011) The fate and transport of nitrate in shallow groundwater in northwestern Mississippi, USA. Hydrogeology Journal 19: 1239–1252.
- 93. Kramer E, Conroy MJ, Elliott MJ, Anderson EA, Bumback WR, et al. (2003) A GAP Analysis of Georgia. Athens: Institute of Ecology and Georgia Cooperative Fish & Wildlife Research Unit, University of Georgia.
- 94. Vilella FJ, Minnis RB, Elmore RD, Bowman JL, Evans DL, et al. (2003) A GAP Analysis of Mississippi. Starkville: Mississippi Cooperative Fish and Wildlife Research Unit, Mississippi State University.
- 95. Brandt P, Abson DJ, DellaSala DA, Feller R, von Wehrden H (2014) Multifunctionality and biodiversity: Ecosystem services in temperate rainforests of the Pacific Northwest, USA. Biological Conservation 169: 362–371. pmid:25064333
- 96. Jones KB, Neale A, Nash M, Van Remortel R, Wickham J, et al. (2001) Predicting nutrient and sediment loadings to streams from landscape metrics: A multiple watershed study from the United States Mid-Atlantic Region. Landscape Ecology 16: 301–312.
- 97. Dauber J, Hirsch M, Simmering D, Waldhardt R, Otte A, et al. (2003) Landscape structure as an indicator of biodiversity: matrix effects on species richness. Agriculture, Ecosystems & Environment 98: 321–329.
- 98. Mouchet MA, Lamarque P, Martín-López B, Crouzat E, Gos P, et al. (2014) An interdisciplinary methodological guide for quantifying associations between ecosystem services. Global Environmental Change 28: 298–308.
- 99. R Development Core Team (2009) R: A language and environment for statistical computing. Available: http://www.r-project.org/. Accessed 05 November 2013.
- 100. Yeh S, Berndes G, Mishra GS, Wani SP, Elia Neto A, et al. (2011) Evaluation of water use for bioenergy at different scales. Biofuels, Bioproducts and Biorefining 5: 361–374.
- 101. Immerzeel DJ, Verweij PA, van der Hilst F, Faaij APC (2014) Biodiversity impacts of bioenergy crop production: a state-of-the-art review. GCB Bioenergy 6: 183–209.
- 102. Syrbe R-U, Walz U (2012) Spatial indicators for the assessment of ecosystem services: Providing, benefiting and connecting areas and landscape metrics. Ecological Indicators 21: 80–88.
- 103. Wrbka T, Erb K-H, Schulz NB, Peterseil J, Hahn C, et al. (2004) Linking pattern and process in cultural landscapes. An empirical study based on spatially explicit indicators. Land Use Policy 21: 289–306.
- 104. McGarigal K, Cushman SA, Ene E (2012) FRAGSTATS v4: Spatial Pattern Analysis Program for Categorical and Continuous Maps. Available: http://www.umass.edu/landeco/research/fragstats/fragstats.html. Accessed 01 April 2014.
- 105. Heikkinen RK, Luoto M, Virkkala R, Rainio K (2004) Effects of habitat cover, landscape structure and spatial variables on the abundance of birds in an agricultural–forest mosaic. Journal of Applied Ecology 41: 824–835.
- 106. Borcard D, Gillet F, Legendre P (2011) Numerical ecology with R. New York Springer.
- 107. Blanchet FG, Legendre P, Borcard D (2008) Forward selection of explanatory variables. Ecology 89: 2623–2632. pmid:18831183
- 108. Villa F, Voigt B, Erickson JD (2014) New perspectives in ecosystem services science as instruments to understand environmental securities. Philosophical Transactions of the Royal Society B: Biological Sciences 369. pmid:24591707
- 109. West PC, Gibbs HK, Monfreda C, Wagner J, Barford CC, et al. (2010) Trading carbon for food: Global comparison of carbon stocks vs. crop yields on agricultural land. Proceedings of the National Academy of Sciences 107: 19645–19648. pmid:21041633
- 110. Clark BR, Hart RM, Gurdak JJ (2011) Groundwater availability of the Mississippi embayment. Reston: U.S. Geological Survey.
- 111. Payne DF, Abu R, Malek, Clarke JS (2005) Simulation of Ground-Water Flow in Coastal Georgia and Adjacent Parts of South Carolina and Florida -Predevelopment, 1980, and 2000. Reston.
- 112. Konikow LF (2013) Groundwater depletion in the United States (1900−2008). Reston.
- 113. Gos P, Lavorel S (2012) Stakeholders' expectations on ecosystem services affect the assessment of ecosystem services hotspots and their congruence with biodiversity. International Journal of Biodiversity Science, Ecosystem Services & Management 8: 93–106.
- 114. Martín-López B, Montes C, Benayas J (2007) The non-economic motives behind the willingness to pay for biodiversity conservation. Biological Conservation 139: 67–82.
- 115. Bennett EM, Peterson GD, Gordon LJ (2009) Understanding relationships among multiple ecosystem services. Ecology Letters 12: 1394–1404. pmid:19845725
- 116. Goldstein JH, Caldarone G, Duarte TK, Ennaanay D, Hannahs N, et al. (2012) Integrating ecosystem-service tradeoffs into land-use decisions. Proceedings of the National Academy of Sciences 109: 7565–7570. pmid:22529388
- 117. Bateman IJ, Harwood AR, Mace GM, Watson RT, Abson DJ, et al. (2013) Bringing Ecosystem Services into Economic Decision-Making: Land Use in the United Kingdom. Science 341: 45–50. pmid:23828934
- 118. Vigerstol KL, Aukema JE (2011) A comparison of tools for modeling freshwater ecosystem services. Journal of environmental management 92: 2403–2409. pmid:21763063
- 119. Terrado M, Acuña V, Ennaanay D, Tallis H, Sabater S (2014) Impact of climate extremes on hydrological ecosystem services in a heavily humanized Mediterranean basin. Ecological Indicators 37, Part A: 199–209.
- 120. Arnold JG, Fohrer N (2005) SWAT2000: current capabilities and research opportunities in applied watershed modelling. Hydrological Processes 19: 563–572.
- 121. Lautenbach S, Volk M, Strauch M, Whittaker G, Seppelt R (2013) Optimization-based trade-off analysis of biodiesel crop production for managing an agricultural catchment. Environmental Modelling & Software 48: 98–112.
- 122. Convertino M, Valverde LJ Jr (2013) Portfolio Decision Analysis Framework for Value-Focused Ecosystem Management. PLoS ONE 8: e65056. pmid:23823331
- 123. Johnson JF, Novak J, Varvel G, Stott D, Osborne S, et al. (2014) Crop Residue Mass Needed to Maintain Soil Organic Carbon Levels: Can It Be Determined? BioEnergy Research 7: 481–490.
- 124. McCarty JL, Justice CO, Korontzi S (2007) Agricultural burning in the Southeastern United States detected by MODIS. Remote Sensing of Environment 108: 151–162.
- 125. Frank S, Fürst C, Koschke L, Makeschin F (2012) A contribution towards a transfer of the ecosystem service concept to landscape planning using landscape metrics. Ecological Indicators 21: 30–38.
- 126. Peel MC, Finlayson BL, McMahon TA (2007) Updated world map of the Köppen-Geiger climate classification. Hydrol Earth Syst Sci 11: 1633–1644.
- 127. st General Assembly of the U.S. State of Georgia (2010) Georgia Mountain and River Corridor Protection Act. (O.C.G.A. 12-2-8).
- 128. Kim K-H, Pauleit S (2007) Landscape character, biodiversity and land use planning: The case of Kwangju City Region, South Korea. Land Use Policy 24: 264–274.
- 129. Baessler C, Klotz S (2006) Effects of changes in agricultural land-use on landscape structure and arable weed vegetation over the last 50 years. Agriculture, Ecosystems & Environment 115: 43–50.
- 130. USGS GAP (2011) Slope. Available: http://gapanalysis.usgs.gov/species/data/download/#avoidance. Accessed 25 November 2013.
- 131. USGS GAP (2011) Aspect. Available: http://gapanalysis.usgs.gov/species/data/download/#avoidance. Accessed 25 November 2013.
- 132. USGS GAP (2011) Human impact avoidance. Available: http://gapanalysis.usgs.gov/species/data/download/#avoidance. Accessed 25 November 2013.
- 133. EPD (2001) Satilla River Basin Dissolved Oxygen TMDLs. Atlanta: Georgia Department of Natural Resources.
- 134. MDEQ (2008) Total Maximum Daily Load—Total Nitrogen and Total Phosphorus For Selected Large Rivers in the Delta—Yazoo River Basin. Jackson.
- 135. MDEQ (2003) TMDL for Organic Enrichment, Nutrients and Sediment for the Big Sunflower River—Yazoo River Basin—Sunflower, Coahoma, Washington, Humphreys, and Sharkey Counties, Mississippi. Jackson: Mississippi State University.
- 136. Mullen CA, Boateng AA, Goldberg NM, Lima IM, Laird DA, et al. (2010) Bio-oil and bio-char production from corn cobs and stover by fast pyrolysis. Biomass and Bioenergy 34: 67–74.
- 137. Bridgeman TG, Jones JM, Shield I, Williams PT (2008) Torrefaction of reed canary grass, wheat straw and willow to enhance solid fuel qualities and combustion properties. Fuel 87: 844–856.