Anthropogenic global change alters the activity and functional composition of soil communities that are responsible for crucial ecosystem functions and services. Two of the most pervasive global change drivers are drought and nutrient enrichment. However, the responses of soil organisms to interacting global change drivers remain widely unknown. We tested the interactive effects of extreme drought and fertilization on soil biota ranging from microbes to invertebrates across seasons. We expected drought to reduce the activity of soil organisms and fertilization to induce positive bottom-up effects via increased plant productivity. Furthermore, we hypothesized fertilization to reinforce drought effects through enhanced plant growth, resulting in even drier soil conditions. Our results revealed that drought had detrimental effects on soil invertebrate feeding activity and simplified nematode community structure, whereas soil microbial activity and biomass were unaffected. Microbial biomass increased in response to fertilization, whereas invertebrate feeding activity substantially declined. Notably, these effects were consistent across seasons. The dissimilar responses suggest that soil biota differ vastly in their vulnerability to global change drivers. Thus, important ecosystem processes like decomposition and nutrient cycling, which are driven by the interdependent activity of soil microorganisms and invertebrates, may be disrupted under future conditions.
Anthropogenic global environmental change affects ecosystem properties worldwide and threatens important ecosystem functions1,2. Climate change is predicted to alter precipitation regimes towards more frequent and severe drought events in the future3. Simultaneously, human activities, such as fossil fuel combustion and fertilization, are causing an acceleration of the turnover rates of the nitrogen cycle and will double nitrogen deposition in the future4,5. The same is true for phosphorous inputs, which also increased at a global scale6. Thus, multiple global change drivers are occurring side by side, and their effects are not necessarily additive or antagonistic. Our knowledge on their interactive effects, however, is still highly limited7,8. This is particularly true for the responses of soil organisms, which mediate crucial ecosystem functions and services, such as nutrient cycling and decomposition9,10. Their significant role is not adequately reflected in the body of global change literature yet. Therefore, a more comprehensive understanding of above- and belowground dynamics is key to predict the responses of terrestrial ecosystems in a changing world7.
Many soil organisms are dependent on a water-saturated atmosphere or on water films on soil aggregates11,12,13,14. Altered precipitation patterns will result in drought periods, which are likely to have substantial effects on their abundances and community structure, thus affecting important soil organism-mediated ecosystem processes. Previous studies reported detrimental effects of drought on soil microbial respiration and biomass as well as a reduction of the diversity of microbial communities15. Furthermore, drought was shown to cause a decline in soil microarthropod abundances16. In contrast, drought seems to have only marginal effects on nematode community composition17. Yet, a reduction of soil moisture content can induce community shifts via lower trophic levels, often favouring fungal-feeding nematodes over bacteria-feeders, as fungi perform relatively better under dry conditions17,18.
Nutrient enrichment is another key factor that affects the soil community by altering the physical and chemical properties of the soil, e.g., by influencing pH, soil porosity, and organic fractions19,20,21. Nitrogen addition has been identified to decrease soil microbial respiration and biomass, often leading to shifts in the soil microbial community composition under the use of mineral fertilizer (NPK)22,23,24. On the other hand, fertilization treatments were shown to increase soil microbial catabolic and functional diversity25,26. Furthermore, nitrogen addition alters the nematode community structure towards bacterivores, thus promoting the bacterial-dominated decomposition pathway27, and was shown to simplify communities17. Similarly, nitrogen was reported to create unfavourable conditions for soil microarthropods, leading to declines in abundance as well as diversity28,29. At the same time, nitrogen enrichment is one of the major drivers determining aboveground primary production30. Nitrogen and phosphorous addition are known to increase total aboveground biomass and consequently the quantity and quality of plant litter input to the soil26,31. In addition, nitrogen also affects plant rhizodeposition by altering the amount and quality of substrates released from roots32,33. Both mechanisms can potentially enhance resource availability via bottom-up effects and can therefore increase soil microarthropod abundances34. Concurrently, the fertilization-induced increase in aboveground biomass may cause higher transpiration rates, which are likely to reinforce drought effects on soil organisms35.
To investigate the interactive effects of extreme drought events and fertilization (NPK), we established a field experiment at the UFZ Experimental Research Station (Bad Lauchstädt, Germany), which combines the treatments of two globally distributed networks – the Drought-Network and the Nutrient Network36. Here, we tested the responses of soil microorganisms, nematodes, and overall soil invertebrate activity to the interactive effects of extreme drought and fertilization (NPK) across all seasons. Based on prior research, we hypothesized that (1) drought will reduce the activity of soil organisms, whereas (2) fertilization will increase their activity, owing to enhanced plant litter input that subsequently increases resource availability for soil organisms. Furthermore, we predicted that (3) the interactive effects of drought and fertilization will result in detrimental conditions for soil organisms as the negative effects of drought were expected to be further enhanced by increased plant growth under fertilization, resulting in reduced soil water availability for soil organisms.
The study site is located at the Experimental Research Station of the Helmholtz Centre for Environmental Research (UFZ), which is situated in Bad Lauchstädt, Germany. The field site is located in the central German dry area with a mean annual precipitation of 487 mm and an average annual daily temperature of 8.9 °C (Meteorological data of Bad Lauchstädt, Helmholtz Centre for Environmental Research GmbH - UFZ, Department of Soil System Science, 1896–2017). The area represents an anthropogenic grassland, which is maintained by moderate mowing (twice a year since 2012). It is a successional plant community dominated by Vulpia myuros (L.) C. C. Gmel., Picris hieracioides (L.) and Taraxacum officinale (F. H. Wigg.) with Apera spica-venti (L.) P. Beauv. and Cirsium arvense (L.) Scop. being very common. The soil is classified as a haplic chernozem, developed upon carbonatic loess substrates, distinguished by a composition of 70% silt and 20% clay37. Within the upper 30 cm, the soil contains 0.18% total nitrogen, 1 g kg−1 total phosphorus, and 20 g kg−1 total potassium. For more details see Altermann et al.37.
Weather conditions within the two-year sampling period of this study were in line with the long-term average (2005–2015) despite some exceptions (Meteorological data of Bad Lauchstädt, Helmholtz Centre for Environmental Research GmbH - UFZ, Department of Soil System Science): precipitation patterns deviated from the long-term average in 2016 with a dry May (21.2 mm compared to an average of 62.3 mm) and a wet June (80.2 mm compared to an average of 41.2). September tended to be drier than usual in both years (19.5 mm in 2016 and 22.1 mm in 2017 compared to an average of 51.8 mm).
Experimental design and treatments
The experimental site was established in March 2015. The experimental design consists of five blocks with five plots each. The plots have a size of 2 × 2 m and are arranged at a distance of 3 m from each other (Fig. S1). The experiment includes two treatments with two levels each (first applied in March 2016): drought (control/drought) and fertilization (no NPK/NPK addition), as well as their interaction (drought × fertilization). Notably, this experiment crosses treatments of two globally distributed experimental networks: the full NPK fertilization treatment of the Nutrient Network36 and the drought treatment of the Drought-Network (http://www.drought-net.colostate.edu/)38,39,40.
In order to simulate drought, a rainfall manipulation system was established39 using corrugated acrylic strips. The roofs have a size of 3 × 3 m and reduce precipitation by 55% throughout the year, simulating a severe long-term reduction in precipitation. Roofs were built with a slope of 20° to ensure water runoff and account for the expected snow load in the region. Exclusion of potential artefacts was realized by equal roof constructions using inverted acrylic strips intended to let rainfall pass41 (Fig. S2). To control for possible infrastructure effects of the roof constructions itself, a fifth plot was added to each block without any roof construction (ambient plots), thus receiving ambient precipitation (not crossed with the fertilization treatment and thus only used to assess if the roof construction itself affected soil water content, see Fig. S1). To validate the drought treatment, soil water content was quantified on all plots in every sampling campaign. All three precipitation levels differed significantly in their soil water content (Tukey’s HSD test, p < 0.05): as intended, the lowest soil water content was found for the drought treatment (−19.4% compared to the ambient plots). Also the infrastructure control plots (with concave roof constructions) differed significantly from the ambient plots (without roof construction), indicating that there were effects of the roof construction itself (−13.4%). Furthermore, soil water content varied significantly between seasons (Table S1; Fig. S3).
The fertilization treatment was realized by annual addition of a mixture of separate fertilizers for nitrogen (N), phosphorus (P) and potassium (K) (i.e. NPK fertilization; applied at 10 g m−2 y−1 by elemental mass for each of the three main fertilizer elements) before each growing season. Following the protocol of the Nutrient Network36, we used coated urea (CO(NH2)2) as nitrogen fertilizer (Multicote, Haifa – Pioneering the Future Haifa, Matam-Haifa, Israel), P2O5 as phosphorus fertilizer (Triple Super Phosphate, Delitzscher Landhandels- und Dienste GmbH, Delitzsch, Germany), and K2SO4 as potassium fertilizer (KaliSOP gran. max. 1.0% Cl, K + S KALI GmbH, Kassel, Germany). In addition, the micronutrient mix “Micromax Premium” (Everris, Geldermalsen, The Netherlands) was applied in the first treatment year36. Specifically, we applied 25 g m−² Multicote, 50.9 g m−² Triple Super Phosphate, and 22.3 g m−² KaliSOP per year, and 100 g m−² Micromax Premium in the first year.
The first soil sampling took place in March 2016. Sampling campaigns were repeated every three months to cover every season (spring, summer, fall, winter) from March 2016 to December 2017 (i.e., eight samplings across two years). Samples were taken on all plots with roof construction (drought and control) with a steel core sampler (1 cm in diameter; 15 cm deep). Seven subsamples per plot were homogenized, sieved at 2 mm, and stored at 4 °C. Soil samples were used to determine soil water content and microbial respiration. In addition, nematodes were extracted from the soil samples in spring and summer of 2017, and pH was measured for all four seasons in 2017.
The Bait Lamina Test
Feeding activity of soil invertebrates was surveyed using the bait lamina test (Terra Protecta GmbH, Berlin, Germany), which presents a commonly used rapid ecosystem function assessment method42. The test uses rigid PVC sticks (1 mm × 6 mm × 120 mm) with 16 holes of 1.5 mm diameter in 5 mm distance. Original sticks were filled with a bait substrate consisting of 70% cellulose powder, 27% wheat bran, and 3% activated carbon, which was prepared according to the recommendations of Terra Protecta. The bait substrate is primarily consumed by mites, collembolans, nematodes, enchytraeids, millipedes, and earthworms, whereas microbial activity plays a minor role in bait loss43,44,45,46. The bait strips were inserted vertically into the soil with the topmost hole just below the ground surface. To avoid damaging the strips, a steel knife was used to prepare the ground prior to insertion. Five strips were used per plot to account for spatial heterogeneity47. For each sampling campaign, the bait lamina strips were removed from the soil after three weeks of exposure and evaluated directly in the field. Bait consumption was recorded for each of the 16 holes per strip as empty (1), partly empty (0.5), or filled (0). Thus, soil invertebrate feeding activity per bait strip could range from 0 to 16 (maximum feeding activity). Mean bait consumption per plot (averaged among the five strips) was calculated prior to statistical analyses.
Microbial biomass and activity
An O2-microcompensation system was used to measure the respiratory response of soil microorganisms in two separated steps using approximately 6.5 g of fresh soil48. First, basal respiration was determined as a measure of soil microbial activity (µl O2 h−1 g−1 soil dry weight) without the addition of any substrate. Second, the maximal respiratory response to a single addition of glucose (4 mg g−1 dry weight soil, solved in 1.5 ml distilled water) allowed us to determine soil microbial biomass (μg Cmic g−1 soil dry weight)49. For an overview of the experimental setup see Fig. S4.
Nematode extraction was conducted with a modified Baermann method50. Approximately 25 g of soil per plot were transferred to plastic vessels with a milk filter and a fine gauze (200 µm) at the bottom and placed in water-filled funnels. More water was added to saturate the soil samples and to ensure a connected water column throughout the sample and the funnel. Hence, nematodes migrated from the soil through the milk filter and the gauze into the water column and gravitationally-settled at the bottom of a closed tube connected to the funnel. After 72 h at 20 °C, the nematodes were transferred to a 4% formaldehyde solution. Nematodes were counted at 100x magnification using a Leica DMI 4000B light microscope. Identification was conducted at 400x magnification. For identification, sediment material from the bottom of each sample vial was extracted with a 2 ml plastic pipette and examined in temporary mounted microscope slides. At least 100 well-preserved specimens (if available in the sample) were randomly selected and identified to genus (adults and most of the juveniles) or family level (juveniles), following Bongers (1988)51. Nematode taxa were then arranged into trophic groups (bacteria-, fungal- and plant-feeders, omnivores and predators)52,53. Due to low densities, omnivorous and predatory nematodes were grouped into a combined feeding type for most analyses, which was based on the fact that both groups often share similar traits, like being carnivores (i.e. representing higher trophic levels) and being persisters rather than colonizers on the c-p scale (see explanation below), thus responding similarly to environmental disturbances54. Nematodes were ordered according to the colonization-persistence gradient (c-p values)55,56, which classifies nematode taxa based on their life history strategy (i.e. r or K strategists). Cp-1 taxa are distinguished by their short generation cycles and high fecundity. They mainly feed on bacteria. Cp-2 taxa have longer generation times, lower fecundity and consist of bacterivores and fungivores57. Both are categorized as r-strategists. Cp-3 to cp-5 are classified as K-strategist nematodes with longer generation times, higher trophic feeding levels and increasing sensitivity against disturbances57. The c-p-values can be used to calculate the Maturity Index (MI) as weighted means of nematode families assigned to c-p-values. It is used to describe soil health and as an indicator of overall food web complexity55,56.
with v(i) being the c-p-value of a taxon i and f(i) being the frequency of that taxon in a sample.
Furthermore, nematode taxa were assigned to functional guilds according to Ferris et al.57, which then served as a basis to calculate additional indices. Functional guilds refer to the following trophic groups: bacterial feeders (BaX), fungal feeders (FuX), omnivores (OmX), and carnivores (CaX). Associated numbers (i.e., the x of the respective trophic group) are again referring to the c-p values described above. The Enrichment Index (EI) indicates the responsiveness of the opportunistic bacterial (Ba1 and Ba2) and fungal feeders (Fu2) to food web enrichment57 and is calculated as follows:
with e as weighted frequencies of Ba1 and Fu2 and b as weighted frequencies of Ba2 and Fu2 nematodes57. The Channel Index (CI) reflects the nature of decomposition channels through the soil food web. High values indicate a predominant decomposition pathway of organic matter dominated by fungal-feeding nematodes, whereas low values refer to bacterial-dominated decomposition pathways57.
with 0.8 and 3.2 representing enrichment weightings for Fu2 and Ba1 nematodes57. The Structure Index (SI) provides information about the complexity of the soil food web. A highly structured food web with a high SI suggests ecosystem stability, while low values imply environmental disturbance57.
with s calculated as the weighted frequencies of Ba3-Ba4, Fu3-Fu4, Ca3-Ca5 and Om3-Om5 nematodes, and b representing the weighted frequencies of Ba2 and Fu2 nematodes57.
Soil microorganisms and invertebrates
Linear mixed-effects models (LMM) were used to analyse the effects of drought, NPK fertilization, season, and their interactions on invertebrate feeding activity, microbial activity, and microbial biomass using the R-package “nlme”58. The random intercept of the model was structured with plots nested within blocks, nested within year (year as a categorical factor). To account for repeated measurements within plots, we compared first-order autoregressive and compound symmetry covariance structures based on the Akaike information criterion (AIC). As differences between AIC values were lower than 2, the simplest covariance structure (i.e. compound symmetry) was used. Based on the importance of soil water content for microbial activity and biomass59, soil water content was added as an additional explanatory variable to the LMMs (Tables S3 and S4, Figs S5 and S6). As we were expecting a strong relation between aboveground plant biomass and microbial biomass60, additional LMMs were used to test the influence of plant biomass on microbial biomass (Table S5, Fig. S7). To evaluate model variation explained by fixed and random effects, marginal and conditional R2 were calculated using the “MuMIn” package61; marginal R2 represents model variation explained by fixed effects in the final model and conditional R2 represents model variation explained by both random and fixed effects.
Nematode community indices
LMMs were also used to assess the effects of drought, NPK fertilization, season (spring and summer 2017), and their interactions on nematode indices, i.e. Enrichment Index, Structure Index, Channel Index, and Maturity Index. A random intercept with plots nested within block was included in the models. We accounted for repeated measurements within plots by using a compound symmetry covariance structure, which fitted the data better than a first-order autoregressive covariance structure based on the AIC. To evaluate model variation explained by fixed and random effects, marginal and conditional R2 were calculated using the “MuMIn” package61.
We also used LMMs to assess the effects of drought, NPK fertilization, and their interaction on soil pH for all seasons in 2017. Additionally, we tested the influence of soil pH on invertebrate feeding activity. A random intercept with blocks nested within season was included in the models. We accounted for repeated measurements within plots by using a compound symmetry covariance structure, which fitted the data better than a first-order autoregressive covariance structure based on the AIC. To evaluate model variation explained by fixed and random effects, marginal and conditional R2 were calculated using the “MuMIn” package61.
Nematode density, richness, and trophic groups
Generalized mixed-effects models (GLMM) were used to assess the effects of drought, NPK fertilization, season (spring and summer 2017), and their interactions on nematode richness, total density (i.e. total number of individuals in the nematodes community) and the abundance of each trophic group (i.e. percentage of individuals in each trophic group). Nematode richness and total density of nematodes were modelled with Poisson distribution (link = “log”), while the trophic groups were modelled with Binomial distribution (link = “logit”). The random intercept of the model was structured with plots nested within blocks. To account for over-dispersion, an observation-level random effect was used in the model with omnivorous and predatory nematodes as a response variable.
Nematode functional guilds and cp groups
GLMMs were also used to assess the effects of drought, NPK fertilization, and their interactions on nematode functional guilds and cp-groups (Table S6) using Binomial distribution (link = “logit”). The random intercept of the model was structured with plots nested within blocks, nested within sampling (sampling as a categorical factor). GLMMs were performed using the “lme4” package62.
Model assumptions of the LMMs and the GLMMs were checked by visually inspecting residual plots for homogeneity and quantile-quantile plots for normality (i.e. no correlation between the residuals and the fitted parameters of the model). To meet the assumptions of the model, invertebrate feeding activity and microbial activity were log-transformed (log(x + 1)). Figures are based on mixed-effects model fits extracted using the package “ggeffects”63. All statistical analyses were conducted using R version 3.4.264.
Soil microbial responses
Soil microbial activity ranged from 0.7 to 5.1 µl O2 h−1 g−1 dry weight soil with an average of 1.7 µl O2 h−1 per g dry weight soil across all measurements. We could not detect a significant effect of the drought or the fertilization treatment on soil microbial activity (Fig. 1a). However, microbial respiration was significantly affected by season, with lowest activity in summer and highest activity in winter (Table 1; Fig. 1b). In addition, we found a positive relation between microbial activity and soil water content (F1, 111 = 170.83, p < 0.001; Table S3) that was independent of the drought and fertilization treatment (Fig. S5).
Soil microbial biomass ranged from 168.0 to 979.8 µg Cmic g−1 dry weight soil with an average of 530.6 µg Cmic g−1 dry weight soil across all measurements. Overall, soil microbial biomass increased significantly with NPK fertilization (Fig. 1c). Microbial biomass was also significantly affected by season with lowest biomass in summer and highest biomass in fall (Fig. 1d, Table 1). Furthermore, fertilization and soil water content interactively affected microbial biomass (F1, 111 = 10.60, p = 0.002; Table S4); while microbial biomass increased with higher soil water content under ambient conditions, it slightly decreased with higher soil water content on plots with NPK fertilization (Fig. S6). In addition, soil microbial biomass increased significantly with aboveground plant biomass (F1, 59 = 8.81, p = 0.004; Table S5; Fig. S7).
Neither total nematode density nor richness were significantly affected by any of the experimental treatments (Fig. 2a,b; Table 2); we could only detect significant differences between spring and summer (Fig. S7a,b). Among the nematode trophic groups, only bacteria-feeders were significantly increased by the fertilization treatment (Fig. 2c), which was mainly due to a significant increase of the r-strategic Ba1-nematodes (χ2 = 4.57, p = 0.032; Fig. S8a). In addition, bacteria-feeders were highly abundant in summer (Fig. S9c). Plant-feeders were affected by the interactive effects of fertilization and season: while fertilization favoured plant-feeding nematodes in spring, it had a negative effect in summer (Figs 2d and S9d). The combined group of omnivorous and predatory nematodes marginally significantly decreased under drought and NPK fertilization (Fig. 2e), with a stronger negative effect of fertilization in spring (Fig. S9e). Fungal-feeders were not significantly affected by any of the treatments (Fig. 2f). A closer look at changes in the nematode community composition revealed that cp2 plant-feeding nematodes increased with drought (χ2 = 6.65, p = 0.0099; Fig. S10c; Table S6), whereas nematodes with higher c-p values, in detail Fu3-nematodes (χ2 = 4.97, p = 0.026; Fig. S10e), Om4-nematodes (marginally; χ2 = 3.80, p = 0.051; Fig. S10g), cp3 (marginally; χ2 = 2.74, p = 0.098; Fig. S10d), and cp4-nematodes (χ2 = 7.83, p = 0.0051; Fig. S10f) decreased significantly in response to fertilization.
While the increase in the Enrichment Index was marginally significant under drought conditions (Table 3; Fig. 3a), drought led to a marginally significant decrease of the Structure Index and the Maturity Index (Fig. 3b,c). Fertilization increased the importance of the bacterial decomposition channel as indicated by a marginally significant decrease of the Channel Index (Fig. 3d). In addition, fertilization decreased nematode complexity as indicated by a significant decrease of the Structure Index and Maturity Index. (Fig. 3b,c).
Soil invertebrate feeding responses
Mean soil invertebrate feeding activity per plot ranged from 0 to 60% of consumed bait substrate with an average of 11% bait consumption. Feeding activity was significantly affected by an interactive effect of drought x fertilization; overall, fertilization decreased invertebrate feeding activity at ambient precipitation, but had no significant effect under drought conditions (Fig. 4a). These treatment effects were consistent across seasons (no treatment x season interaction), however, the level of soil invertebrate feeding activity varied strongly between seasons and tended to be highest in summer and strongly decreased in winter (Table 1; Fig. 4b).
Soil pH was significantly reduced by NPK fertilization across all seasons in 2017 (F1,56 = 14.11; p < 0.001; Table S7; Fig. S11a). In addition, we could show that an decrease in soil pH led to a marginally significant decrease in invertebrate feeding activity across all seasons in 2017 (F1,58 = ; p = 0.07; Table S8; Fig. S11b).
We studied the impacts of two major global change drivers, namely drought and fertilization, and their interactive effects on soil communities and functions. By investigating the responses of a wide range of soil organisms across all seasons within a two-year timeframe, we gained a comprehensive picture of how soil ecosystem functions may be altered in a changing world. Intriguingly, we saw vastly different responses among trophic levels that were constant across seasons.
Our first hypothesis, predicting detrimental effects of drought on soil organisms, was confirmed to some extent: drought reduced soil invertebrate feeding activity and led to a more disturbed soil nematode community structure, whereas soil microbial activity and biomass were not significantly affected. The dependency of soil invertebrates on soil moisture content is well documented65 as is the fact that soil microfauna is more prone to water stress than bacteria and fungi66. The detrimental drought effects on faunal activity are thus in line with previous studies, which claim that abiotic conditions shape the performance of the soil faunal community67. Microarthropods (mites and collembolans), enchytraeids, and earthworms are some of the most relevant groups found in the upper soil layer in temperate regions43 and are likely to account for most of the feeding activity leading to bait perforation68,69. Extreme drought not only forces them to migrate to deeper soil layers, but also interferes with their reproduction and development success, which is possibly the reason why they are highly susceptible to drought70,71,72,73. Furthermore, drought conditions entail drier food sources for detritivores, which are more difficult to digest47.
In line with our expectations, drought was also responsible for (moderate) shifts in nematode indices. The environmental conditions were changed towards an enriched, more disturbed, less structured system, with a higher proportion of opportunistic nematodes. Already at ambient precipitation levels, the guilds of the opportunistic Fu2- and Ba2-nematodes accounted for the highest shares at our experimental site, indicating a basal food web that is capable to cover a wide ecological amplitude and is already adapted to some environmental stress57. The positive response of the Enrichment Index to drought suggests mortality at higher trophic levels, which subsequently promoted nutrient enrichment and gave further rise to opportunistic nematodes57. Thus, overall, drought led to simplified trophic structures of the nematode community.
In contrast to our initial hypothesis, soil microbial activity and biomass were not affected by the drought treatment. This was unexpected given the intensity of the drought treatment applied in the experiment (precipitation was reduced by 55% during the entire study period) and the fact that most soil microbes are strongly dependent on soil moisture59,74. However, this finding is in line with Pailler et al.75, who also found little soil microbial functional responses to drought. In addition, we observed distinct variation of microbial activity and biomass across seasons and could reveal that soil water content explained a significant proportion of the variability in microbial activity, yet irrespective of the treatments. Notably, soil water content itself was strongly varying among seasons (more than in response to the drought treatment; Tables S9 and S10). This suggests that microorganisms residing in the top soil are in general highly dependent on soil moisture levels, which are fluctuating across the year. Therefore, they must be able to sustain drought periods, for instance, through physiological modifications. Such adaptations may comprise an adjustment of internal water potential, sporulation, or production of exopolysaccharides that provide protection against exsiccation76,77. This provides evidence that temporal environmental variability is a strong predictor of species activity and emphasizes the dependency of soil organisms on seasonal patterns78,79,80. We therefore infer that seasonal fluctuations in natural precipitation at our site (Table S9) may have led to acclimatization of the microbial communities to natural drought periods as they are part of their climatic history81,82. We speculate that this may explain the negligible responses to the experimentally induced drought, which may still be within the adaptive range of the community (Table S10).
The responses of soil biota were again ambiguous with regard to our second hypothesis, in which we expected fertilization to promote the activity of soil biota. Consistent with our hypothesis, soil microbial biomass increased under fertilization. Soil invertebrate feeding activity, however, substantially declined under elevated nutrient supply, questioning the universal validity of our initial hypothesis. Notably, in a recent meta-analysis, Yian et al.83 reported negative effects of nitrogen fertilization on soil microbial biomass, which may be attributable to changes in the community composition, but this requires further investigation, because microbe-mediated activity markers were, on the other hand, increased. The pronounced responsiveness of soil microbial biomass to NPK fertilization that we found in our study is in line with similar studies reporting positive effects of nitrogen fertilization on microbial biomass and changes in microbial community structure and function84,85. Fertilization certainly enhanced nutrient availability, resulting in higher yields of aboveground plant biomass (Berger et al., in prep.), which is often accompanied by an expanded root system30. Subsequently, this increases the release of organic compounds into the soil86, providing substrates that support the growth of microbial communities towards higher population densities60.
Also nematode indices were highly responsive to NPK fertilization, resulting in a less structured and more disturbed system with an enhanced bacteria-driven decomposition pathway. The latter was additionally supported by a strong increase in bacteria-feeding nematodes (especially Ba1) and an equally strong decrease in fungal-feeding nematodes (Fu3) under fertilization, indicating that fertilization had detrimental effects on soil fungi. This is in line with the general notion that fertilization favours bacteria-dominated decomposition18,27,57,87. The simplification of the nutrient-enriched soil food web is also reflected by declines of the omnivorous nematodes (Om4) and the cp3 and cp4 nematodes, which consist of long-living, pollutant sensitive, rather immobile organisms that are prone to environmental stress56. When linking these changes reported for the nematode indices to the responses of the microbial community, our results suggest that fertilization promoted the growth of bacteria, which then accounted for a strong increase in microbial biomass. As a result, this restructuring of the microbial community may thus have provided the basis for the observed increase in bacteria-feeding nematodes and some of the shifts in nematode indices.
Current evidence for soil invertebrate responses to fertilization is equivocal. Several studies reported an enhancing effect of fertilization on soil invertebrate activity and diversity88,89, whereas others revealed no such effects16,90, or recorded declines in soil fauna abundances and diversity after fertilizer application43. Most likely, the diminished feeding activity of soil invertebrates can be explained by alterations of soil physicochemical properties. In our study, we found that fertilization decreased soil pH, which can serve as one potential explanation of the reported decline of invertebrate feeding activity. This is in line with previous studies showing that reduced soil pH as a result of mineral fertilization was negatively correlated with the abundance of most soil invertebrates91,92. Especially earthworms, which represent a significant part of soil invertebrate biomass93, are known to decline noticeably in numbers under reduced soil pH94. Overall, environmental constraints, such as altered energy channels, simplified food web structures, and reduced soil pH outweighed potential positive bottom-up effects through enhanced plant growth, which we expected to find.
Prior studies emphasized the importance of interactive effects of global change drivers as they will profoundly alter ecosystem functions and services7,95. Accordingly, our third hypothesis predicted fertilization to reinforce drought effects, resulting in reduced soil water content and thus aggravated living conditions for soil organisms. Indeed, drought and fertilization interacted significantly in restraining soil invertebrate feeding activity, partially supporting our hypothesis. However, as discussed above, fertilization obviously created an unfavourable environment for most soil invertebrates at our site. Although both global change drivers individually decreased soil invertebrate feeding activity, the interaction, however, did not result in further declines. We therefore conclude that the combined effects may have led to a distinct restructuring of the soil faunal community by promoting species better adapted to adverse conditions, and thus revealing no measurable change in net effects. Since the combined global change drivers are likely to modify aboveground plant communities96,97,98, alterations in the quality of aboveground litter inputs can be expected. Leaf litter quality, in turn, affects soil fauna and might therefore be responsible for reshaping the faunal community99,100. With the methods applied in our study, however, we can only speculate about potential changes in the soil faunal community composition. This highlights the need for future research to detect which specific groups are responsible for bait perforation. This could be done, for instance, by exposing bait lamina strips with a labelled substrate under controlled laboratory conditions101,102. Building on that, the abundances of the most important groups of soil organisms could be monitored in the field, while being exposed to different global change drivers.
In contrast to the invertebrate feeding activity, microbial activity was not significantly affected by the interaction of the two global change drivers. Moreover, we could not detect any interactive effects on nematode indices or nematode groups. This illustrates the robustness of a large portion of the soil community to interactive global change effects, which might therefore be able to buffer prospective global change effects to a certain extent.
In conclusion, the main groups of soil organisms investigated in the present study responded differently to the individual and interacting effects of global change drivers. Soil invertebrate activity was strongly impaired by both global change drivers and their interaction, while microbial biomass benefited from enhanced nutrient availability, and microbial activity was surprisingly unaffected by all treatments. Despite the strong seasonal dynamics of temperate regions, these treatment effects remained constant across all seasons within two years. Notably, nematode indices pointed to changes in the state of the ecosystem, shifting towards simplified and more disturbed systems under drought and especially under fertilization that mostly facilitated opportunistic species. We could show that soil biota differ considerably in their sensitivity to global change drivers and in their seasonal dynamics – also highlighting the importance of integrating seasonal effects into experimental frameworks. This may lead to far-reaching alterations of crucial ecosystem processes, since decomposition and nutrient cycling are driven by the interdependent concurrence of soil microbial and faunal activities46. By covering a range of different taxonomic and trophic levels of soil organisms, we could therefore show that single as well interacting global change drivers induce complex changes in soil food webs and functions.
The datasets analysed during the current study are available from the corresponding author on reasonable request.
Vitousek, P. M. Beyond global warming: ecology and global change. Ecology 75, 1861–1876 (1994).
Steffen, W. et al. Global change and the earth system: a planet under pressure. (Springer Science & Business Media, 2006).
IPCC, T. P. S. B. 2007. Climate Change 2007. The Physical Science Basis. Contribution of Working Group I to the Fourth Assessment Report of the Intergovernmental Panel on Climate Change [Solomon, S., D. Qin, M.o Manning, Z. Chen, M. Marquis, K.B. Averyt, M. Tignor and H.L. Miller (eds)]. Vol. 4 (Cambridge University Press, Cambridge, United Kingdom and New York, NY, USA., 2007).
Galloway, J. N. et al. Transformation of the nitrogen cycle: recent trends, questions, and potential solutions. Science 320, 889–892 (2008).
Lamarque, J. F. et al. Assessing future nitrogen deposition and carbon cycle feedback using a multimodel approach: Analysis of nitrogen deposition. Journal of Geophysical Research: Atmospheres 110 (2005).
Wang, R. et al. Significant contribution of combustion-related emissions to the atmospheric phosphorus budget. Nature Geoscience 8, 48 (2015).
Eisenhauer, N., Cesarz, S., Koller, R., Worm, K. & Reich, P. B. Global change belowground: impacts of elevated CO2, nitrogen, and summer drought on soil food webs and biodiversity. Global Change Biology 18, 435–447 (2012).
De Vries, F. T. et al. Land use alters the resistance and resilience of soil food webs to drought. Nature Climate Change 2, 276–280 (2012).
Bardgett, R. D. & van der Putten, W. H. Belowground biodiversity and ecosystem functioning. Nature 515, 505–511 (2014).
Verhoef, H. & Brussaard, L. Decomposition and nitrogen mineralization in natural and agroecosystems: the contribution of soil animals. Biogeochemistry 11, 175–211 (1990).
Orchard, V. A. & Cook, F. Relationship between soil respiration and soil moisture. Soil Biology and Biochemistry 15, 447–453 (1983).
Baldrian, P., Merhautová, V., Petránková, M., Cajthaml, T. & Šnajdr, J. Distribution of microbial biomass and activity of extracellular enzymes in a hardwood forest soil reflect soil moisture content. Applied Soil Ecology 46, 177–182 (2010).
Riutta, T., Clack, H., Crockatt, M. & Slade, E. M. Landscape-scale implications of the edge effect on soil fauna activity in a temperate forest. Ecosystems 19, 534–544 (2016).
Blankinship, J. C., Niklaus, P. A. & Hungate, B. A. A meta-analysis of responses of soil biota to global change. Oecologia 165, 553–565 (2011).
Hueso, S., García, C. & Hernández, T. Severe drought conditions modify the microbial community structure, size and activity in amended and unamended soils. Soil Biology and Biochemistry 50, 167–173 (2012).
Lindberg, N., Engtsson, J. B. & Persson, T. Effects of experimental irrigation and drought on the composition and diversity of soil fauna in a coniferous stand. Journal of Applied Ecology 39, 924–936 (2002).
Cesarz, S. et al. Nematode functional guilds, not trophic groups, reflect shifts in soil food webs and processes in response to interacting global change factors. Pedobiologia 58, 23–32 (2015).
Kardol, P., Cregger, M. A., Campany, C. E. & Classen, A. T. Soil ecosystem functioning under climate change: plant species and community effects. Ecology 91, 767–781 (2010).
Galantini, J. & Rosell, R. Long-term fertilization effects on soil organic matter quality and dynamics under different production systems in semiarid Pampean soils. Soil and Tillage Research 87, 72–79 (2006).
Liu, E. et al. Long-term effect of chemical fertilizer, straw, and manure on soil chemical and biological properties in northwest China. Geoderma 158, 173–180 (2010).
Marinari, S., Masciandaro, G., Ceccanti, B. & Grego, S. Influence of organic and mineral fertilisers on soil biological and physical properties. Bioresource Technology 72, 9–17 (2000).
Pan, Y. et al. Impact of long-term N, P, K, and NPK fertilization on the composition and potential functions of the bacterial community in grassland soil. FEMS Microbiology Ecology 90, 195–205 (2014).
Treseder, K. K. Nitrogen additions and microbial biomass: A meta‐analysis of ecosystem studies. Ecology Letters 11, 1111–1120 (2008).
Ramirez, K. S., Craine, J. M. & Fierer, N. Nitrogen fertilization inhibits soil microbial respiration regardless of the form of nitrogen applied. Soil Biology and Biochemistry 42, 2336–2338 (2010).
Dan, W. et al. Bacterial community structure and diversity in a black soil as affected by long-term fertilization. Pedosphere 18, 582–592 (2008).
Li, J. H. et al. Effects of nitrogen and phosphorus fertilization on soil carbon fractions in alpine meadows on the Qinghai-Tibetan Plateau. PLOS One 9, e103266 (2014).
Song, M. et al. Responses of soil nematodes to water and nitrogen additions in an old-field grassland. Applied Soil Ecology 102, 53–60 (2016).
Gardi, C., Menta, C., Montanarella, L. & Cenci, R. Main threats on soil biodiversity: The case of agricultural activities impacts on soil microarthropods. Threats to Soil Quality in Europe, 101–112 (2008).
Wang, S., Chen, H. Y., Tan, Y., Fan, H. & Ruan, H. Fertilizer regime impacts on abundance and diversity of soil fauna across a poplar plantation chronosequence in coastal Eastern China. Scientific Reports 6, 20816 (2016).
Stevens, C. J. et al. Anthropogenic nitrogen deposition predicts local grassland primary production worldwide. Ecology 96, 1459–1465 (2015).
Liu, L. & Greaver, T. L. A global perspective on belowground carbon dynamics under nitrogen enrichment. Ecology Letters 13, 819–828 (2010).
Ge, T. et al. Rice rhizodeposition and its utilization by microbial groups depends on N fertilization. Biology and Fertility of Soils 53, 37–48 (2017).
Wichern, F., Eberhardt, E., Mayer, J., Joergensen, R. G. & Müller, T. Nitrogen rhizodeposition in agricultural crops: methods, estimates and future prospects. Soil Biology and Biochemistry 40, 30–48 (2008).
Sjursen, H., Michelsen, A. & Jonasson, S. Effects of long-term soil warming and fertilisation on microarthropod abundances in three sub-arctic ecosystems. Applied Soil Ecology 30, 148–161 (2005).
Craven, D. et al. Plant diversity effects on grassland productivity are robust to both nutrient enrichment and drought. Phil. Trans. R. Soc. B 371, 20150277 (2016).
Borer, E. T. et al. Finding generality in ecology: a model for globally distributed experiments. Methods in Ecology and Evolution 5, 65–73 (2014).
Altermann, M. et al. Chernozem—Soil of the Year 2005. Journal of Plant Nutrition and Soil Science 168, 725–740 (2005).
Lemoine, N. P., Sheffield, J., Dukes, J. S., Knapp, A. K. & Smith, M. D. Terrestrial Precipitation Analysis (TPA): A resource for characterizing long‐term precipitation regimes and extremes. Methods in Ecology and Evolution 7, 1396–1401 (2016).
Yahdjian, L. & Sala, O. E. A rainout shelter design for intercepting different amounts of rainfall. Oecologia 133, 95–101 (2002).
Gherardi, L. A. & Sala, O. E. Automated rainfall manipulation system: a reliable and inexpensive tool for ecologists. Ecosphere 4, 1–10 (2013).
Vogel, A. et al. Separating drought effects from roof artifacts on ecosystem processes in a grassland drought experiment. PLOS One 8, e70997 (2013).
Kratz, W. The bait-lamina test. Environmental Science and Pollution Research 5, 94–96 (1998).
Gardi, C. et al. Soil biodiversity monitoring in Europe: ongoing activities and challenges. European Journal of Soil Science 60, 807–819 (2009).
Hamel, C., Schellenberg, M. P., Hanson, K. & Wang, H. Evaluation of the “bait-lamina test” to assess soil microfauna feeding activity in mixed grassland. Applied Soil Ecology 36, 199–204 (2007).
Rożen, A., Sobczyk, Ł., Liszka, K. & Weiner, J. Soil faunal activity as measured by the bait-lamina test in monocultures of 14 tree species in the Siemianice common-garden experiment, Poland. Applied Soil Ecology 45, 160–167 (2010).
Simpson, J. E., Slade, E., Riutta, T. & Taylor, M. E. Factors affecting soil fauna feeding activity in a fragmented lowland temperate deciduous woodland. PLOS One 7, e29616 (2012).
Thakur, M. P. et al. Reduced feeding activity of soil detritivores under warmer and drier conditions. Nature Climate Change 8, 75–78 (2018).
Scheu, S. Automated measurement of the respiratory response of soil microcompartments: active microbial biomass in earthworm faeces. Soil Biology and Biochemistry 24, 1113–1118 (1992).
Anderson, J. & Domsch, K. A physiological method for the quantitative measurement of microbial biomass in soils. Soil Biology and Biochemistry 10, 215–221 (1978).
Ruess, L. Studies on the nematode fauna of an acid forest soil: spatial distribution and extraction. Nematologica 1, 229–239 (1995).
Bongers, T. The Nematodes of the Netherlands. The Nematodes of the Netherlands. (1988).
Yeates, G., Bongers, T., De Goede, R., Freckman, D. & Georgieva, S. Feeding habits in soil nematode families and genera—an outline for soil ecologists. Journal of Nematology 25, 315 (1993).
Okada, H., Harada, H. & Kadota, I. Fungal-feeding habits of six nematode isolates in the genus Filenchus. Soil Biology and Biochemistry 37, 1113–1120 (2005).
Bongers, T. & Ferris, H. Nematode community structure as a bioindicator in environmental monitoring. Trends in Ecology & Evolution 14, 224–228 (1999).
Bongers, T. The maturity index: an ecological measure of environmental disturbance based on nematode species composition. Oecologia 83, 14–19 (1990).
Bongers, T. & Bongers, M. Functional diversity of nematodes. Applied Soil Ecology 10, 239–251 (1998).
Ferris, H., Bongers, T. & De Goede, R. A framework for soil food web diagnostics: extension of the nematode faunal analysis concept. Applied Soil Ecology 18, 13–29 (2001).
Pinheiro, J., Bates, D., DebRoy, S., Sarkar, D. & Team, R. C. Nlme: Linear and nonlinear mixed effects models (R package version 3.1–128, 2016). R Software (2017).
Wan, S., Norby, R. J., Ledford, J. & Weltzin, J. F. Responses of soil respiration to elevated CO2, air warming, and changing soil water availability in a model old‐field grassland. Global Change Biology 13, 2411–2424 (2007).
Kent, A. D. & Triplett, E. W. Microbial communities and their interactions in soil and rhizosphere ecosystems. Annual Reviews in Microbiology 56, 211–236 (2002).
Barton, K. Package ‘MuMIn’. R package version 1.40. 4. (2018).
Bates, D., Mächler, M., Bolker, B. & Walker, S. Fitting linear mixed-effects models usinglme4. ArXiv preprint arXiv:1406.5823 (2014).
Lüdecke, D. Ggeffects: Create Tidy Data Frames of Marginal Effects for ggplot (Version 0.3.4). R Software (2018).
R Core Team, R. C. T. R: A language and environment for statistical computing. Vienna, Austria; 2014 (2017).
Coleman, D. C., Crossley, D. A. Jr. & Hendrix, P. F. Fundamentals of Soil Ecology. (Academic press, 2004).
Manzoni, S., Schimel, J. P. & Porporato, A. Responses of soil microbial communities to water stress: results from a meta‐analysis. Ecology 93, 930–938 (2012).
Briones, M. J. I., Ineson, P. & Piearce, T. G. Effects of climate change on soil fauna; responses of enchytraeids, Diptera larvae and tardigrades in a transplant experiment. Applied Soil Ecology 6, 117–134 (1997).
Gongalsky, K. B., Persson, T. & Pokarzhevskii, A. D. Effects of soil temperature and moisture on the feeding activity of soil animals as determined by the bait-lamina test. Applied Soil Ecology 39, 84–90 (2008).
Helling, B., Pfeiff, G. & Larink, O. A comparison of feeding activity of collembolan and enchytraeid in laboratory studies using the bait-lamina test. Applied Soil Ecology 7, 207–212 (1998).
Frampton, G. K., Van Den Brink, P. J. & Gould, P. J. Effects of spring drought and irrigation on farmland arthropods in southern Britain. Journal of Applied Ecology 37, 865–883 (2000).
Maraldo, K. & Holmstrup, M. Enchytraeids in a changing climate: a mini-review. Pedobiologia 53, 161–167 (2010).
Siepel, H. Biodiversity of soil microarthropods: the filtering of species. Biodiversity & Conservation 5, 251–260 (1996).
Wever, L. A., Lysyk, T. J. & Clapperton, M. J. The influence of soil moisture and temperature on the survival, aestivation, growth and development of juvenile Aporrectodea tuberculata (Eisen)(Lumbricidae). Pedobiologia 45, 121–133 (2001).
Griffiths, R. I., Whiteley, A. S., O’Donnell, A. G. & Bailey, M. J. Physiological and community responses of established grassland bacterial populations to water stress. Applied and Environmental Microbiology 69, 6961–6968 (2003).
Pailler, A., Vennetier, M., Torre, F., Ripert, C. & Guiral, D. Forest soil microbial functional patterns and response to a drought and warming event: Key role of climate–plant–soil interactions at a regional scale. Soil Biology and Biochemistry 70, 1–4 (2014).
Harris, R. Effect of water potential on microbial growth and activity. Water Potential Relations in Soil Microbiology, 23–95 (1981).
Roberson, E. B. & Firestone, M. K. Relationship between desiccation and exopolysaccharide production in a soil Pseudomonas sp. Applied and Environmental Microbiology 58, 1284–1291 (1992).
Deng, Q. et al. Responses of soil respiration to elevated carbon dioxide and nitrogen addition in young subtropical forest ecosystems in China. Biogeosciences 7, 315–328 (2010).
Sorensen, P. O., Germino, M. J. & Feris, K. P. Microbial community responses to 17 years of altered precipitation are seasonally dependent and coupled to co-varying effects of water content on vegetation and soil C. Soil Biology and Biochemistry 64, 155–163 (2013).
Tonkin, J. D., Bogan, M. T., Bonada, N., Rios‐Touma, B. & Lytle, D. A. Seasonality and predictability shape temporal species diversity. Ecology 98, 1201–1216 (2017).
Cruz-Martínez, K. et al. Despite strong seasonal responses, soil microbial consortia are more resilient to long-term changes in rainfall than overlying grassland. The ISME Journal 3, 738 (2009).
Waldrop, M. & Firestone, M. Seasonal dynamics of microbial community composition and function in oak canopy and open grassland soils. Microbial Ecology 52, 470–479 (2006).
Jian, S. et al. Soil extracellular enzyme activities, soil carbon and nitrogen storage under nitrogen fertilization: A meta-analysis. Soil Biology and Biochemistry 101, 32–43 (2016).
Campbell, B. J., Polson, S. W., Hanson, T. E., Mack, M. C. & Schuur, E. A. The effect of nutrient deposition on bacterial communities in Arctic tundra soil. Environmental Microbiology 12, 1842–1854 (2010).
Cusack, D. F., Silver, W. L., Torn, M. S., Burton, S. D. & Firestone, M. K. Changes in microbial community characteristics and soil organic matter with nitrogen additions in two tropical forests. Ecology 92, 621–632 (2011).
Bais, H. P., Weir, T. L., Perry, L. G., Gilroy, S. & Vivanco, J. M. The role of root exudates in rhizosphere interactions with plants and other organisms. Annu. Rev. Plant Biol. 57, 233–266 (2006).
Wardle, D. & Yeates, G. The dual importance of competition and predation as regulatory forces in terrestrial ecosystems: evidence from decomposer food-webs. Oecologia 93, 303–306 (1993).
Graenitz, J. & Bauer, R. The effect of fertilization and crop rotation on biological activity in a 90 year long-term experiment. Bodenkultur-wien and munchen- 51, 99–106 (2000).
Van der Wal, A. et al. Dissimilar response of plant and soil biota communities to long-term nutrient addition in grasslands. Biology and Fertility of Soils 45, 663–667 (2009).
Maraun, M. et al. Indirect effects of carbon and nutrient amendments on the soil meso-and microfauna of a beechwood. Biology and Fertility of Soils 34, 222–229 (2001).
Kaneko, N. & Kofuji, R.-I. Effects of soil pH gradient caused by stemflow acidification on soil microarthropod community structure in a Japanese red cedar plantation: an evaluation of ecological risk on decomposition. Journal of Forest Research 5, 157–162 (2000).
Wang, S., Tan, Y., Fan, H., Ruan, H. & Zheng, A. Responses of soil microarthropods to inorganic and organic fertilizers in a poplar plantation in a coastal area of eastern China. Applied Soil Ecology 89, 69–75 (2015).
Fierer, N., Strickland, M. S., Liptzin, D., Bradford, M. A. & Cleveland, C. C. Global patterns in belowground communities. Ecology Letters 12, 1238–1249 (2009).
Gudleifsson, B. Impact of long term use of fertilizer on surface invertebrates in experimental plots in a permanent hayfield in Northern-Iceland. Agric. Soc. Iceland 15, 37–49 (2002).
Zhou, L. et al. Interactive effects of global change factors on soil respiration and its components: a meta‐analysis. Global Change Biology 22, 3157–3169 (2016).
Gough, L., Osenberg, C. W., Gross, K. L. & Collins, S. L. Fertilization effects on species density and primary productivity in herbaceous plant communities. Oikos 89, 428–439 (2000).
Bobbink, R. et al. Global assessment of nitrogen deposition effects on terrestrial plant diversity: a synthesis. Ecological Applications 20, 30–59 (2010).
Thuiller, W., Lavorel, S., Araújo, M. B., Sykes, M. T. & Prentice, I. C. Climate change threats to plant diversity in Europe. Proceedings of the National Academy of Sciences of the United States of America 102, 8245–8250 (2005).
Carrillo, Y., Ball, B. A., Strickland, M. S. & Bradford, M. A. Legacies of plant litter on carbon and nitrogen dynamics and the role of the soil community. Pedobiologia 55, 185–192 (2012).
Cornwell, W. K. et al. Plant species traits are the predominant control on litter decomposition rates within biomes worldwide. Ecology Letters 11, 1065–1071 (2008).
Briones, M., Bol, R., Sleep, D., Allen, D. & Sampedro, L. Spatio-temporal variation of stable isotope ratios in earthworms under grassland and maize cropping systems. Soil Biology and Biochemistry 33, 1673–1682 (2001).
Dyckmans, J., Scrimgeour, C. M. & Schmidt, O. A simple and rapid method for labelling earthworms with 15N and 13C. Soil Biology and Biochemistry 37, 989–993 (2005).
We thank the staff of the Bad Lauchstädt Experimental Research Station for their help in maintaining the experimental site, and Alla Kavtea, Tom Künne, and Ulrich Pruschitzki for their support with lab and field work. Furthermore, we thank the coordination of the International Drought-Net Experiment for providing protocols and support. Financial support came from the German Centre for Integrative Biodiversity Research Halle–Jena–Leipzig, funded by the German Research Foundation (FZT 118).
The authors declare no competing interests.
Publisher’s note: Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.
Electronic supplementary material
About this article
Cite this article
Siebert, J., Sünnemann, M., Auge, H. et al. The effects of drought and nutrient addition on soil organisms vary across taxonomic groups, but are constant across seasons. Sci Rep 9, 639 (2019). https://doi.org/10.1038/s41598-018-36777-3
Assessing the habitat suitability of paddy fields for avian indicators based on hydropedological parameters of the wet agricultural soil along the Cauvery delta basin, India
Paddy and Water Environment (2021)