Variation in Community-Level Trophic Niches of Soil Microarthropods With Conversion of Tropical Rainforest Into Plantation Systems as Indicated by Stable Isotopes (15N, 13C)

Introduction

The niche concept forms the basis of concepts explaining the coexistence of species (Hutchinson, 1959; Chase and Leibold, 2003). There are two different niche-related processes, i.e., environmental filtering, assuming that the assemblage of communities is based on the similarity of niches of the species coexisting locally, and niche differentiation resulting from competition among species (MacArthur and Levins, 1967; Vellend, 2010; Violle et al., 2011; Kraft et al., 2015). At stable environmental conditions long-term coexistence of species results in distinct niches of the coexisting species and in predictable community composition with pronounced niche differentiation among coexisting species (Giller, 1996). By contrast, in fragmented habitats or in systems with fluctuating environmental conditions, communities are likely to be assembled at least in part at random, and therefore niches of species may overlap (Giller, 1996; Chesson, 2000; Caruso et al., 2012). Trophic niches define the impact of one species on other species and ecosystem processes and therefore are closely related to the role of species in ecosystems (Korotkevich et al., 2018). The complement of trophic niches of coexisting species defines the community-level trophic niche, which is likely to differ between ecosystems due to species turnover and changes in trophic niches of individual species (Tilman, 2004; Salles et al., 2009). Species with broader trophic niches likely are able to better cope with disturbances, such as changes in land use or invading species, compared to species with narrower niches (Bommarco et al., 2010; Dammhahn et al., 2017). By contrast, species with narrower niches are more likely to go locally extinct if environmental conditions and the availability of food resources change (Gan et al., 2014). These changes in community-level trophic niches are likely to be associated with changes in the functionality of communities.

Mechanisms responsible for diversity—ecosystem functioning relationships are based on the niches of species and their functional space (Tilman, 2001; Adler and Bradford, 2002). In this approach, the community-level trophic niche can be described by using diversity indices. In particular, functional diversity, including functional richness, functional evenness and functional divergence, have been shown to be closely linked to ecosystem functioning (Hulot et al., 2000; Pearson, 2001; Bremner et al., 2003) and these indices can be applied to describe trophic niches (Cucherousset and Villéger, 2015). For example, if functional richness of trophic niches is low, part of the available resources remain unused by the local community, resulting in low productivity (Petchey, 2003). By contrast, increased ecosystem functioning is based on high functional richness, coupled with niche differentiation leading to efficient use of resources (Mason et al., 2005). This also applies to multitrophic communities, i.e., trophic complementarity across trophic levels in food webs is positively related to ecosystem functioning (Poisot et al., 2013). Along with other functional indices, trophic complexity of communities is expected to decline in disturbed ecosystems, as was shown for springtails in the temperate zone (Korotkevich et al., 2018). However, this pattern has not been tested in other soil taxa and other regions.

The global demand for food, fuel and fiber is associated with the transformation and degradation of ecosystems, and this is increasing rapidly (Sodhi et al., 2010; Wilcove et al., 2013; Meijide et al., 2018). Especially tropical regions are suffering from transformation and degradation (Sodhi et al., 2010; Wilcove et al., 2013; Meijide et al., 2018). Tropical forest ecosystems, characterized by the highest biodiversity and highest level of endemism worldwide, are shrinking and are transformed into intensively managed monoculture plantations at increasing rates (Myers et al., 2000; Sodhi et al., 2010; Drescher et al., 2016). Biodiversity in plantations typically is strongly reduced compared to rainforests due to reduced diversity of trees as well as more pronounced fluctuating environmental conditions (Wilcove and Koh, 2010). Reduced diversity in plantations may impair the functioning of these systems and this at least in part is likely to be due to changes in trophic interactions and community-level trophic niches (Potapov et al., 2019a).

Only little is known on the effect of land-use change in tropical regions on soil organisms responsible for major ecosystem functions such as decomposition processes and nutrient cycling, and this applies in particular to soil mesofauna such as oribatid mites (Maraun and Scheu, 2000; Bardgett, 2005). Oribatid mites span over about four trophic levels and include trophic guilds of lichen feeders, fungal feeders, primary and secondary decomposers as well as predators/scavengers (Schneider et al., 2004; Illig et al., 2005; Maraun et al., 2011). Due to their high diversity and wide range of trophic niches oribatid mites are an ideal model taxon for studying effects of land-use change on community functioning.

Natural variations in ¹⁵N/¹⁴N and ¹³C/¹²C ratios are increasingly used for characterizing trophic niches of soil animals and provide insight into trophic levels, basal resources as well as the trophic structure of entire communities (Tiunov, 2007; Potapov et al., 2019b). Animal tissue is enriched by about 3.4‰ per trophic level in ¹⁵N, allowing to study changes in the trophic position of species with environmental changes (DeNiro and Epstein, 1978; Post, 2002; Pollierer et al., 2009; Potapov et al., 2019b). In contrast to ¹⁵N, ¹³C is little enriched in consumers compared to their diet, allowing to trace basal food resources in food webs (DeNiro and Epstein, 1978; Spence and Rosenheim, 2005; Pollierer et al., 2009; Potapov et al., 2019b). Stable isotopes have been used to analyze trophic niches of a wide range of soil invertebrates (Scheu and Falca, 2000; Halaj et al., 2005; Maraun et al., 2007, 2011; Tiunov, 2007). However, they rarely have been used to investigate how changes in trophic niches of soil organisms are affected by changes in land use (but see Lagerlöf et al., 2017; Minor et al., 2017; Korotkevich et al., 2018). Additionally, previous studies based on stable isotopes did not account for abundance and/or biomass of the studied species, i.e., all species were assumed to have the same importance or impact (Layman et al., 2007; Jackson et al., 2011). Novel techniques allow accounting for these deficiencies but have not been applied to soil communities (Cucherousset and Villéger, 2015).

The current study formed part of the interdisciplinary project “Ecological and socioeconomic functions of tropical lowland rainforest transformation systems” (EFForTS), established in Jambi Province, southwest Sumatra, Indonesia (Drescher et al., 2016). In the framework of this project, it has been shown that plants as well as invertebrates above and below the ground strongly decline with the conversion of rainforest into rubber and oil palm plantations (Grass et al., 2020). In particular, the density of oribatid mites declined by ca. 20% and species richness by ca. 60% (D. Sandmann, unpubl. data). Here we focused on changes in the trophic structure of oribatid mite communities with conversion of rainforest into plantation systems by measuring natural variations in ¹⁵N/¹⁴N and ¹³C/¹²C ratios. Four land-use systems, widespread across Southeast Asia were investigated, i.e., rainforest, rubber agroforest (“jungle rubber”), rubber and oil palm monoculture plantations. We focused on the niche structure and overall niche position at the level of communities rather than on the changes in trophic niches of individual species, which were addressed in an earlier study (Krause et al., 2019). We hypothesized (1) that the community-level trophic niche of oribatid mites is larger in more natural ecosystems, such as rainforest and jungle rubber, than in intensively managed agricultural systems, such as rubber and oil palm plantations. Further, we hypothesized (2) that the community-level trophic niche of oribatid mites is shifted in intensively managed agricultural systems toward living plant-based resources due to lower availability of litter resources and more open canopy allowing more pronounced growth of understory plants and algae. In addition, we hypothesized (3) that functional redundancy in rainforest is higher compared to plantation systems due to more species rich oribatid mite communities.

Materials and Methods

Sampling Sites

Samples were taken in two landscapes of Jambi Province, Bukit Duabelas (2° 0′ 57″ S, 120° 45′ 12″ E) and Harapan (1° 55′ 40″ S, 103° 15′ 33″ E), located about 40 km from each other. In each landscape, four different land-use systems were investigated: rainforest, jungle rubber, rubber and oil palm plantations (Drescher et al., 2016). Rainforest sites were “primary degraded forests” (as classified by Margono et al., 2014) and had been selectively logged at least once. Jungle rubber sites were established by planting rubber trees (Hevea brasiliensis) into rainforest and contain rainforest tree species. Jungle rubber sites represent low intensive land-use systems, lacking fertilizer input as well as herbicide application. By contrast, rubber and oil palm (Elaeis guineensis) monocultures represent high land-use intensity plantation systems managed by the addition of fertilizers as well as herbicides. Oil palm plantations differ from those of rubber, among others, in that fronds of oil palms are cut regularly for fruit harvesting and piled up in rows, whereas in rubber leaves are shed annually at the end of the dry season and form a litter layer which is virtually lacking in oil palm plantations. More details on the study site are given in Drescher et al. (2016). For each of the four land-use systems four replicates were established in each of the two landscapes, resulting in a total of 32 plots. The two landscapes were spaced by ca. 80 km and the replicate plots per land-use system within landscapes by 2–40 km. Each plot was positioned within a larger plantation or forest patch, spanned 50 × 50 m and included three randomly placed subplots of 5 × 5 m. Subplots were spaced by a minimum of 5 m from the plot edges to avoid edge effects. More details on the location of the study sites and their characteristics are given in Drescher et al. (2016).

Sampling, Extraction, and Species Determination

In October 2013, randomly placed samples (16 × 16 cm; including the litter layer and 0–5 cm of the mineral soil) were taken from each of the subplots, i.e., a total of 96 samples. The samples were transported to the laboratory and extracted in a heat gradient (Kempson et al., 1963). Determination of oribatid mites was done to species/morphospecies level using Balogh and Balogh (2012). Species and morphospecies were documented by pictures, linked with morphological traits and species identification numbers (species ID), and included into the Ecotaxonomy database¹. Until further analysis, species were stored in 70% ethanol. For calibration of animal stable isotope values mixed litter samples were taken from each subplot (Klarner et al., 2017).

Stable Isotope Analysis

For each land-use system in the two landscapes (Bukit Duabelas and Harapan) species for stable isotope analysis were selected based on their relative abundance; for each land-use system species representing 80% of total oribatid mite individuals were analyzed (Supplementary Table 1). These species were assumed to represent the functional “core” of the community of oribatid mites of the respective land-use system. Three individuals (if available) were pooled for one sample (sample weight 0.02–0.19 mg). In total, 367 samples of 117 species contributing to 80% of the individuals were analyzed (out of the total of 220 species occurring at the study sites; D. Sandmann, unpubl. data).

Prior to stable isotope analysis samples were dried at 60°C for 24 h. Litter samples were ground in a ball mill (Retsch Mixer Mill MM200, Haan, Germany). Samples were analyzed using a coupled system of an elemental analyzer (NA 1500, Carlo Erba, Milan, Italy) and a mass spectrometer (MAT 251, Finnigan, Bremen, Germany) adapted for the analysis of small sample sizes (Langel and Dyckmans, 2014). Stable isotope abundance (δX) was expressed using the δ notation with δX (‰) = (R_sample–R_standard)/R_standard × 1000, with X representing the target isotope (¹⁵N or ¹³C) and R_sample and R_standard the respective target isotope ratio (¹⁵N/¹⁴N or ¹³C/¹²C). As standard for ¹³C Vienna PD Belemnite and for ¹⁵N atmospheric nitrogen were used. Acetanilid was used for internal calibration.

Means of δ¹³C and δ¹⁵N values of litter samples from all subplots were used for calibration of stable isotope values of oribatid mites of the respective plot following Klarner et al. (2014). Calibrated δ¹³C and δ¹⁵N values were calculated as difference between the plot-specific litter δ¹³C and δ¹⁵N values, and the δ¹³C and δ¹⁵N values of oribatid mite species, and given as Δ¹³C and Δ¹⁵N values, respectively. Calibrated values were used to ascribe oribatid mites to trophic levels including primary decomposers, secondary decomposers/fungal feeders and predators/scavengers based on Maraun et al. (2011) assuming an enrichment of ¹⁵N by 3.4‰ per trophic level except for primary decomposers, which were assumed to be only enriched in ¹⁵N by a maximum of 1.7‰ compared to litter (Vanderklift and Ponsard, 2003; Potapov et al., 2019b). Calibrated Δ¹³C and Δ¹⁵N values were used for statistical analyses. All data manipulations were done in R v 3.5.2 (R Core Team, 2018) with R studio interface (RStudio, Inc.).

Statistical Analysis

For characterizing the trophic structure of communities we calculated “isotopic metrics” (Layman et al., 2007; Cucherousset and Villéger, 2015). These metrics describe the position of species of a studied community within two-dimensional space, represented by δ¹⁵N and δ¹³C values. Cucherousset and Villéger (2015) further developed metrics based on the ones from Layman et al. (2007), by merging them with the functional diversity metrics suggested by Villéger et al. (2008) and Laliberté and Legendre (2010).

We used the R script provided by Cucherousset and Villéger (2015) to scale two stable isotope axes and calculate isotopic metrics for each community (Figure 1). Δ¹³C and Δ¹⁵N values were scaled between 0 and 1 based on maximum and minimum across communities to ensure equal contribution of two isotopes in the multidimensional metrics calculation (Cucherousset and Villéger, 2015). Before calculating community mean values and multidimensional metrics, species were weighted according to their contribution to the total community biomass per plot and therefore, those metrics were adjusted according to the functional relevance of the species (Cucherousset and Villéger, 2015). To calculate biomasses of species, individual body masses of all mite species were calculated from individual measurements of body length and width (D. Sandmann, unpubl. data) using the allometric regression log P = 1.53 × log L + 1.53 × log l− 6.67, with P body mass, L body length and l body width (Lebrun, 1971). Overall, thirteen isotopic metrics were calculated for each of 32 communities (i.e., sampling plots). First, we calculated single-dimensional metrics separately for Δ¹³C and Δ¹⁵N values—minimum, maximum, range and biomass-weighted mean. Maximum and minimum Δ¹³C and Δ¹⁵N values were represented by the species with the most extreme values within the community. The range represented the difference between minimum and maximum Δ¹³C and Δ¹⁵N values. Second, we calculated five multidimensional metrics including isotopic divergence, isotopic dispersion, isotopic evenness, isotopic uniqueness and isotopic richness, all weighted by biomass of species (Cucherousset and Villéger, 2015). Isotopic divergence represents the distance between all species and the center of the convex hull area. Isotopic divergence values close to 0 indicate that species with the most extreme stable isotope values, e.g., lichen-feeders and predators, are rare, whereas isotopic divergence values close to 1 indicate that species with the most extreme stable isotope values dominate. Isotopic dispersion combines the convex hull area with isotopic divergence values and can be interpreted as scaled multidimensional variance. Isotopic dispersion approaches 1 when species with contrasting stable isotope values have similar abundance (for instance, primary and high-level consumers are similarly abundant), whereas it approaches 0 when most biomass is positioned near the “center of gravity” of the community. Isotopic evenness, in contrast to the first two metrics, which do not consider the distance between species, quantifies the distribution of species in stable isotope space. Isotopic evenness values close to 1 indicate that the isotope values of the species of the studied community are evenly distributed. By contrast, isotopic evenness values close to 0 indicate that most stable isotope values of the studied species cluster together (for instance, all species are herbivores or predators, but no decomposers present). Isotopic uniqueness is defined as the inverse of the average isotopic redundancy, which reflects the closeness of stable isotope values of the studied species within the community. Isotopic uniqueness approaches 0 if stable isotope values of species within the community are similar indicating that most of the species have another isotopically similar species within this community. By contrast, isotopic uniqueness is close to 1 if stable isotope values of species differ within communities indicating that many species have no other isotopically similar species within this community. Finally, isotopic richness represents the isotopic space (convex hull area) filled by the community, i.e., the functional richness. Functional richness is scaled between 0 and 1 using the volume occupied by all studied species across sites as the maximum (Mason et al., 2005; Villéger et al., 2008).

FIGURE 1

Figure 1. Calculated isotopic metrics. For the analysis, Δ¹³C and Δ¹⁵N values of species in each community were scaled between 0 and 1 and their distribution in isotopic space was analyzed with biomass-weighted isotopic metrics (see text for details). An example of metrics for one community (HR4) is given; eight such communities were analyzed for each of the four land-use systems.

Data were analyzed using the aov (analysis of variance) function with landscape and land-use system as factors followed by post hoc comparison of means using the HSD.test function to inspect differences between land-use systems. Results were displayed using the ggplot2 package (Wickham, 2016). The baseline was set to zero. Points on all figures in the main text represent communities, and not species or individuals.

Results

One-Dimensional Metrics

The weighted means of Δ¹³C and Δ¹⁵N values (isotope positions) across oribatid mite communities separated the two more natural land-use systems (rainforest and jungle rubber) from the two monoculture plantations (Figure 2). Communities of rainforest and jungle rubber overlapped widely in their isotopic positions; the same was true for oil palm and rubber plantations. The average community positions of both Δ¹³C and Δ¹⁵N values varied significantly between the land-use systems [F₍₃,₂₇₎ = 7.09, p < 0.001 for Δ¹³C and F₍₃,₂₇₎ = 7.93, p = < 0.001 for Δ¹⁵N; Figures 3A–E]. Average community positions of Δ¹³C were similar in rainforest and jungle rubber, but significantly lower in rubber and oil palm plantations, on average by 1.58‰ (Figure 3A and Supplementary Table 2). By contrast, average community positions of Δ¹⁵N in rubber and oil palm plantations in trend were higher than in jungle rubber, on average by 1.79‰, and significantly higher than in rainforest, on average by 3.03‰ (Figure 3E and Supplementary Table 2).

FIGURE 2

Figure 2. Weighted means of Δ¹³C and Δ¹⁵N values of oribatid mite communities in rainforest (green), jungle rubber (blue), rubber (red) and oil palm plantations (yellow) (eight replicates each). Each point represents a weighted mean (isotopic position) for one community, error bars represent standard errors; 32 communities were analyzed.

FIGURE 3

Figure 3. One-dimensional metrics for Δ¹³C (upper panel) and Δ¹⁵N values (lower panel) of oribatid mite communities in rainforest (F, green), jungle rubber (J, blue), rubber (R, red) and oil palm plantations (O, yellow). Average position (A,E), maximum (B,F), minimum (C,G), and range between minimum and maximum (D,H); means (circles) and confidence intervals. Each point represents one community. For the calculation of the metrics see section “Materials and Methods” and Supplementary Table 2. For the calculation of the average positions, species were weighted according to their contribution to the total community biomass per plot. Means, sharing the same letter are not significantly different (Tukey’s HSD test, P < 0.05).

Maximum Δ¹³C values, but not maximum Δ¹⁵N values, varied significantly with land-use system [F₍₃,₂₇₎ = 7.22, p = 0.001 for Δ¹³C and F₍₃,₂₇₎ = 0.41, p = 0.74 for Δ¹⁵N] (Figures 3B,F). Maximum Δ¹³C values were similar in rainforest, jungle rubber and rubber plantations, but significantly lower in oil palm plantations, on average by 2‰ (Figure 3B, Supplementary Table 2, and, Supplementary Figure 1D). Further, minimum Δ¹³C and Δ¹⁵N values varied significantly with land-use system [F₍₃,₂₇₎ = 19.51, p < 0.001 for Δ¹³C and F₍₃,₂₇₎ = 10.56, p ≤ 0.001 for Δ¹⁵N]. Minimum Δ¹³C were similar in rainforest, jungle rubber and oil palm plantations, but significantly lower in rubber plantations, on average by 4.46‰. Some oribatid mite species in rubber plantations were depleted in ¹³C relative to the litter up to 6‰ (Supplementary Figure 1C). By contrast, minimum Δ¹⁵N values were similar in rainforest, jungle rubber and rubber plantations, being significantly higher in oil palm plantations, on average by 4.15‰ (Figure 3G and Supplementary Table 2). Rainforest and rubber plantations harbored species with ¹⁵N values lower than those of litter (Supplementary Figures 1A,C).

Similar to the previous metrics, the range between maximum and minimum Δ¹³C and Δ¹⁵N values varied significantly between land-use systems [F₍₃,₂₇₎ = 16.31 p = 0.005 for Δ¹³C and F₍₃,₂₇₎ = 5.18 p = 0.006 for Δ¹⁵N]. The range in Δ¹³C values was similar in rainforest, jungle rubber and oil palm plantations, but significantly higher in rubber plantations, on average by 4.87‰ (Figure 3D and Supplementary Table 2). The range in Δ¹⁵N values was similar in rainforest, jungle rubber and rubber plantations, but was significantly lower in oil palm plantations, on average by 4.94‰ (Figure 3H and Supplementary Table 2). As indicated by ¹⁵N values, rainforest, jungle rubber and rubber plantations harbored species spanning over three trophic levels including primary and secondary decomposers as well as predators (Supplementary Figures 1A–C). By contrast, oil palm plantations lacked primary decomposers and only comprised secondary decomposers and predators (Supplementary Figure 1D).

Multidimensional Metrics

Isotopic dispersion, isotopic divergence and isotopic evenness did not differ significantly between the four land-use systems (Figures 4A–C) [F₍₃,₂₇₎ = 1.65, p = 0.201, F₍₃,₂₇₎ = 0.46, p = 0.714, and F₍₃,₂₇₎ = 1.53, p = 0.228, respectively]. By contrast, isotopic richness varied significantly between the land-use systems [F₍₃,₂₇₎ = 8.1, p < 0.001]; it was similar in rainforest and jungle rubber, in trend lower in oil palm plantations and highest in rubber plantations, on average by 0.11 (scaled value; Figure 4D and Supplementary Table 3). Further, isotopic uniqueness increased slightly from rainforest to jungle rubber and rubber plantations, and was significantly higher in oil palm plantations than in rainforest, on average by 0.3 [F₍₃,₂₇₎ = 5.33, p = 0.005; Figure 4E and Supplementary Table 3]. For detailed information on plot level metrics values see Supplementary Figures 2A–D.

FIGURE 4

Figure 4. Multidimensional isotopic metrics of oribatid mite communities of four land-use systems, rainforest (F, green), jungle rubber (J, blue), rubber (R, red) and oil palm plantations (O, yellow)—(A) isotopic dispersion, (B) isotopic divergence, (C) isotopic evenness, (D) isotopic richness and (E) isotopic uniqueness; means (circles) and confidence intervals. Each point represents one community. For calculations see section “Materials and Methods” and Supplementary Table 3. For the calculation of the metrics, species were weighted according to their contribution to the total community biomass per plot. Means sharing the same letter are not significantly different (Tukey’s HSD test, P < 0.05).

Discussion

We investigated effects of land-use change on the trophic organization of oribatid mite communities as model taxon of soil invertebrates in the decomposer food web. The study adds to the few existing studies investigating variations in community trophic niches and energy fluxes in soil (Korotkevich et al., 2018; Kühn et al., 2018; Susanti et al., 2019). Our study represented species accounting for 80% of total oribatid mite individuals on each site and thus are likely to represent key functional changes of the entire community. The results are generally supporting our hypotheses and indicate that (i) the community niche of oribatid mites differs most between more natural systems (rainforest and jungle rubber) and monoculture plantation systems (rubber and oil palm plantations), and that communities in oil palm plantations have shorter trophic chains and lower trophic redundancy than in other systems. In addition, we found that in rubber monoculture plantations oribatid mites use basal resources not existing in any of the other studied land-use systems.

One-Dimensional Metrics

Generally, both Δ¹³C and Δ¹⁵N values were similar in rainforest and jungle rubber and distant from those in oil palm and rubber plantations, indicating that the trophic structure of soil food webs changes strongly with land-use change from natural systems or extensive agricultural systems to intensively managed agricultural systems. This supports findings of Krause et al. (2019) who analyzed six individual oribatid mite species and showed that trophic niches shifted most from rainforest to monoculture plantation systems, reflecting that oribatid mites are able to respond in a plastic way to changes in resource supply at the species level. Here, we showed changes in both the use of basal resources as well as trophic positions of the entire oribatid mite communities. Using fatty acids as trophic markers Susanti et al. (2019) found changes in the flux of energy through soil food webs with the conversion of rainforest into rubber and oil palm plantations. Changes in energy channels with land-use intensity suggest that soil fauna communities in general are able to respond in a flexible way to changes in the availability of resources and environmental conditions. In rainforest, energy in soil food webs is channeled mainly to higher trophic levels via the bacterial energy channel, whereas in oil palm plantations the plant-based channel is more important (Susanti et al., 2019). Furthermore, generalist predators such as centipedes (Chilopoda) have been shown to switch from decomposer prey to other prey, predominantly herbivore species, in monoculture plantations, presumably due to reduced or lacking litter layer in the latter two systems (Klarner et al., 2017). The amount of leaf litter in the litter layer in natural ecosystems typically is higher than in plantation systems (Hyodo et al., 2015), and this also applies to the ecosystems investigated in the present study (Krashevska et al., 2017). In our study the litter layer in oil palm plantations was lacking or poorly developed, but a dense herb layer of mostly introduced weeds was present (Drescher et al., 2016). Similar to the results of Klarner et al. (2017) and Susanti et al. (2019) the shift toward lower Δ¹³C values in oribatid mite communities in our study indicates that conversion of rainforest into plantation systems is associated with the strengthening of the plant-based energy channel in plantation systems (lower “detrital shift”; Pollierer et al., 2009; Potapov et al., 2019b). By contrast, high Δ¹³C values in rainforest and jungle rubber indicate that soil food webs in the more natural systems are predominantly based on microbial energy channels (Potapov et al., 2013, 2019b). Oribatid mite communities in oil palm plantations lack species with high Δ¹³C and low Δ¹⁵N values, reflecting that the primary decomposers among microarthropods are absent or strongly reduced. Earlier studies from Ecuadorian montane forests also showed that in some tropical ecosystems primary decomposers may be scarce or lacking (Illig et al., 2005). In these ecosystems, the trophic niche of oribatid mites likely shifted from feeding on detritus to scavenging or predation, e.g., by feeding on nematodes (Heidemann et al., 2011, 2014).

Minimum Δ¹³C values of oribatid mite communities were significantly lower (reflecting one species with the most extreme values from the community) in rubber plantations (up to 6‰) than in the other three land-use systems. In fact, four species in rubber plantations, i.e., cf. Trachyoribates cf. florens, cf. Rostrocetes cf. shibai, Cyrthermannia tuberculata and Eremulus densus, had δ¹³C values <−32‰, indicating that oribatid mites in rubber plantations use some basal resources with exceptionally low δ¹³C values not available in the other land-use systems. Such low δ¹³C values are unique and have never been observed before in soil invertebrates (Potapov et al., 2019b). The pattern in part might be explained by the use of carbon from understory plants and algae, which assimilated ¹³C-depleted CO₂ originating from decomposing organic matter (canopy effect; Van der Merwe and Medina, 1991). However, this is unlikely to explain the extreme difference in minimum Δ¹³C values of oribatid mite communities between rubber plantations and the other land-use systems studied as neither the abundance of algae nor of understory plants is higher in rubber monoculture plantations than in the other land-use systems studied (Rembold et al., 2017; Schulz et al., 2019; Susanti et al., 2019). Another possibility might be that low Δ¹³C values of oribatid mite communities reflect the use of plant compounds depleted in ¹³C such as lignin (Bowling et al., 2008; Pollierer et al., 2009). However, the use of lignin as carbon source is also unlikely since—with very few exceptions—animals are unable to digest lignin (Berg and Ryszard, 2005). Future studies are needed to clarify the low Δ¹³C values of oribatid mites in rubber plantations. Due to the very low minimum Δ¹³C values in oribatid mites of rubber plantations the range of Δ¹³C values and isotopic richness were significantly higher compared to the other three land-use systems. Very high ¹³C values in jungle rubber and rubber such as in Plonaphacarus kugohi presumably were due to the incorporation of calcium carbonate in their exoskeleton (Norton and Behan-Pelletier, 1991; Maraun et al., 2011; Pachl et al., 2012).

Multidimensional Metrics

Isotopic dispersion, isotopic divergence and isotopic evenness did not differ significantly between the four land-use systems indicating that the oribatid mite communities in the studied land-use systems are rather balanced and the niche differentiation, on average, differed little. Presumably, at least in part this reflects the ability of oribatid mite species to adapt to local resources (Krause et al., 2019). In contrast to the three metrics above, isotopic richness was significantly higher in rubber plantations than in the three other land-use systems studied, confirming the results of isotopic ranges due to the use of resources depleted in ¹³C (see above).

Isotopic uniqueness in oil palm plantations exceeded that in the other three land-use systems, with jungle rubber and rubber plantations being intermediate between oil palm plantations and rainforest. High isotopic uniqueness indicates that all abundant species in the community have very different stable isotope values, e.g., species are “unique” in their trophic niche (Cucherousset and Villéger, 2015). High values in oil palm plantations and low values in rainforest therefore suggest low functional redundancy in the former and high functional redundancy in the latter. This indicates that further loss of species is more likely to be associated with a loss of functions in oil palm plantations than in rainforest.

Conclusion

Our results document that oribatid mites in tropical ecosystems occupy a wide range of trophic niches allowing insight into changes in the structure and functioning of decomposer systems with changes in land use. Changes in community-level trophic niches with conversion of rainforest into plantation systems were due to both changes in trophic position (Δ¹⁵N values) as well as changes in the use of basal resources (Δ¹³C values). Notably, changes in the use of basal resources were more prominent and consistent than those in trophic positions, indicating that land use mainly affects the use of basal resources of soil microarthropods. Oribatid mite communities in both rubber and oil palm monocultures rely more heavily on plant-based resources and lack primary decomposers, whereas communities in rainforest and jungle rubber are based predominantly on microorganisms and litter-based resources. Oribatid mite communities in rubber plantations are using carbon resources not existing in the other land-use systems studied, but the identity of these resources remains unknown. High isotopic uniqueness in oil palm plantations suggests that in particular these plantations are susceptible to losses of function with the loss of species. Overall, the results document that conversion of rainforest into plantation systems is associated with pronounced shifts in community-level trophic niches of soil microarthropods, which are likely associated with changes in the functioning of the decomposer system and the channeling of energy through the decomposer food web.

Data Availability Statement

The datasets presented in this study can be found in Supplementary Material. Morphospecies descriptions are available from ecotaxonomy.org.

Author Contributions

AK and SS led the manuscript writing. AP, RW, NH, DS, and MM contributed to the manuscript writing. AP designed the data analysis. AK and AP analyzed the data. DS determined the oribatid mite species. SE validated the species determination. SS and MM designed the experiment and were the scientific supervisors of the experiment. All authors contributed to the article and approved the submitted version.

Funding

This study was funded by the Deutsche Forschungsgemeinschaft (DFG, German Research Foundation)—project no. 192626868—SFB 990 in the framework of the collaborative German—Indonesian research project CRC990. Work of AP was supported by the Russian Science Foundation (project 19-74-00154). The study was conducted based on the research permits no. 332/SIP/FRP/SM/IX/2012, 389/SIP/FRP/SM/X/2013 and 145/SIP/FRP/SM/V/2013 issued by the State Ministry of Research and Technology of the Republic of Indonesia (RISTEK), and the collection permit no. S.07/KKH-2/2013 issued by the Ministry of Forestry of the Republic of Indonesia. Sample export for analysis in Germany was based on permit no. 125/KKH-5/TRP/2014 issued by the Ministry of Forestry of the Republic of Indonesia.

Conflict of Interest

The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.

Acknowledgments

We thank Bernhard Klarner for collecting the samples as well as Svenja Meyer, Kristina Richter, Anneliese Beckendorff, and Melissa Jüds for help in determining oribatid mites. Furthermore, we thank the staff of the Kompetenzzentrum Stabile Isotope Göttingen (KOSI) for measurement of stable isotopes.

Supplementary Material

The Supplementary Material for this article can be found online at: https://www.frontiersin.org/articles/10.3389/fevo.2021.592149/full#supplementary-material

Footnotes

1. ^ http://ecotaxonomy.org/

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