Invasion of non-native species is among the top threats for the biodiversity and functioning of native and agricultural ecosystems worldwide. We investigated whether the herbivory of the slug Arion vulgaris (formerly Arion lusitanicus; Gastropoda), that is listed among the 100 worst alien species in Europe, is affected by soil organisms commonly present in terrestrial ecosystems (i.e. earthworms—Annelida: Lumbricidae and arbuscular mycorrhizal fungi—AMF, Glomerales). We hypothesized that slug herbivory would be affected by soil organisms via altered plant nutrient availability and plant quality. In a greenhouse experiment, we created a simple plant community consisting of a grass, a forb, and a legume species and inoculated these systems with either two earthworm species and/or four AMF taxa. Slugs were introduced after plants were established. Earthworms significantly reduced total slug herbivory in AMF-inoculated plant communities (P = 0.013). Across plant species, earthworms increased leaf total N and secondary metabolites, AMF decreased leaf thickness. Mycorrhizae induced a shift in slug feeding preference from non-legumes to legumes; the grass was generally avoided by slugs. AMF effects on legume herbivory can partly be explained by the AMF-induced increase in total N and decrease in C/N ratio; earthworm effects are less clear as no worm-induced alterations of legume plant chemistry were observed. The presence of earthworms increased average AMF colonization of plant roots by 140 % (P < 0.001). Total shoot mass was significantly increased by AMF (P < 0.001). These data suggest that the feeding behavior of this invasive slug is altered by a belowground control of plant chemical quality and community structure.
In many terrestrial ecosystems, both arbuscular mycorrhizal fungi (AMF; Glomerales) and earthworms (Oligochaeta: Clitellata) are considered as ecosystem engineers because of their eminent impact on ecosystem structure and functioning (Jones et al. 1997; Cameron 2010). Another factor of increasing importance that affects ecosystem biodiversity, sustainability, and overall functioning is the invasion of non-native species (United Nations Environment Programme 2006). Nevertheless, to the best of our knowledge, the combined impacts of these ubiquitous soil organisms on the activity of invasive herbivores have never been investigated explicitly.
In temperate grasslands in Europe, earthworms represent the dominant fraction of soil animal biomass (Lee 1985; Curry 1994). These earthworm communities commonly consist of only a few species (Edwards and Bohlen 1996) comprising three functional groups: vertically burrowing anecics, horizontally burrowing endogeics, and surface-dwelling epigeics (Bouché 1977). By their activity, earthworms turn over several tons of soil per hectare a year (Zaller and Arnone 1997) and speed up the decomposition and mineralization of organic matter in soils (James 1991; Chevallier et al. 2006) with consequences on the growth, nutrient uptake, and quality of plants (Bradford et al. 2002; Scheu 2003; Eisenhauer et al. 2009). These earthworm-induced changes in plant performance have been shown to affect aboveground sap-sucking herbivores (Wurst and Jones 2003; Wurst et al. 2003, 2004a). Earthworms can also be important invasive species with severe consequences on native ecosystems (Bohlen et al. 2004; Migge-Kleian et al. 2006; Sanchez-de Leon and Johnson-Maynard 2009). However, to the best of our knowledge, so far only one study investigated their role in affecting herbivory of invasive slug species (Zaller et al. 2013a).
Arbuscular mycorrhizal fungi form symbiotic associations with about 80 % of the herbaceous plants in grassland ecosystems (Wang and Qiu 2006). The hyphal network of the symbiont serves as extension of the plant root systems, improving plant water and nutrient supply and plant growth (Smith and Read 2008). Numerous studies have shown that presence and species composition of AMF affects plant growth and foliar chemistry with consequences on aboveground herbivores (reviewed in Koricheva et al. 2009). Again, nothing is known on whether AMF affects herbivory of invasive slug species.
The up to 15-cm-long slug species, Arion vulgaris Moquin-Tandon (Mollusca, Arionidae; formerly widely known as Arion lusitanicus Mabille) expanded all over Europe during the last five decades (South 1992) and is now listed among the 100 worst alien species in Europe due to its devastating effects on natural and agricultural ecosystems (www.europe-aliens.org). Since 1998, this species has also been observed in the USA and given a top national quarantine significance (Cowie et al. 2009) and is suggested to further expand with climate change (Knop and Reusser 2012). Gastropods exhibit diets of wide diversity, but nevertheless reflect distinct food plant preferences (Dirzo 1980; Frank and Friedli 1999; Zaller et al. 2003). Food selection by slugs is broadly defined by two factors: the presence of inhibiting substances (avoidance hypothesis) and the presence of feeding stimulants (preference hypothesis; South 1992). By selectively grazing certain plant species, molluscs alter the species composition and relative abundances within plant communities (Thompson et al. 1993; Hanley et al. 1995a, 1995b; Buschmann et al. 2005).
The aim of this study was to investigate whether the feeding behavior of this invasive generalist slug species is affected by such important soil organisms as earthworms or AMF. Central questions were: (1) Do the consequences of the activity of soil organisms cascade via plants to herbivores? (2) Is slug herbivory more affected by AM fungi than by earthworms? (3) What sort of interactions, if any, occur between these major soil organismic groups? We hypothesized that both soil organisms will influence plant growth and palatability and thereby influence herbivore feeding habits either by altering their consumption rates or changing feeding preferences (Crawley 1983). It has been documented that earthworms and AMF interact directly as earthworms were shown to selectively feed on fungal mycelia (Bonkowski et al. 2000), disperse AMF spores (Reddell and Spain 1991; Gange 1993; Lee et al. 1996), increase AMF biomass in the soil (Gormsen et al. 2004), and either increase (Ortiz-Ceballos et al. 2007) or do not affect root AMF colonization (Wurst et al. 2004b). By enhancing nutrient availability in soil, earthworms might also decrease the mycorrhizal dependency of plants. So far, interrelationships between AMF and earthworms have only been investigated on aboveground sap-sucking insect herbivores (Wurst et al. 2004b). But to the best of our knowledge, potential effects on a mollusc generalist herbivore have never been addressed, despite their documented importance in shaping plant communities (Peters et al. 2006). Assuming that slugs, like insect herbivores are generally limited more by N than P (Mattson 1980), we hypothesized to see stronger effects by earthworms than by AMF provided that the mechanism of interaction between soil organisms and the herbivore is a nutritional one. These hypotheses were explored in a full-factorial greenhouse experiment where one slug species could freely choose its food within a simple plant community (one grass, one non-leguminous, one leguminous forb species) that was inoculated with a mix of earthworms (one anecic, one endogeic species) and/or four AMF taxa.
Materials and methods
We conducted a full-factorial pot experiment in a greenhouse of the University of Natural Resources and Life Sciences Vienna (BOKU), Austria, manipulating the factors earthworms and AMF (each of these factors comprising two levels, see details below). Each treatment combination was replicated six times (pot size 14 × 14 cm wide, 30 cm high; volume 3 l). The growth substrate consisted of arable field soil (Haplic Chernozem, silty loam) from the BOKU Experimental Farm mixed with quartz sand (particle size 1.4–2.2 mm) in a 40:60 v/v ratio (pH-H2O = 7.4, Corg = 24.2 g kg−1, Ntot = 0.89 g kg−1, P in Ca lactate–acetate (CAL) = 61.1 mg kg−1, K-CAL = 107.6 mg kg−1). This mixture was steam-sterilized for 16 h at 110 °C in order to kill active AMF propagules living therein. Quartz sand was added in order to facilitate harvesting of roots from this rather loamy field soil. This type of substrate was successfully used in other experiments comprising the same plant, earthworm and AMF taxa (Heiner et al. 2011; Putz et al. 2011; Zaller et al. 2011a). To prevent earthworms and slugs from escaping, the inside bottoms of the pots were lined with two layers of fleece material and the upper rims of the pots extended by 30-cm-high transparent plastic barriers smeared with soft soap.
Pots were first filled with 2 l of the steam-sterilized substrate mixture and then with 1-l steam-sterilized substrate amended with 80 g inoculum containing equal proportions of four different AMF taxa [“+M” treatment; Glomus claroideum N.C. Schenck & G.S. Smith BEG 96, Glomus geosporum (Nicol. & Gerd.) C. Walker (La Banque Européenne des Glomales e BEG 199), Glomus intraradices N.C. Schenck & G.S. Smith BEG 163, Glomus mosseae (T.H. Nicolson & Gerdemann) Gerdemann & Trappe BEG 198] obtained from a commercial supplier (Symbiom, Lanskroun, Czech Republic; www.symbiom.cz). The AMF control (“-M” treatment) was prepared with the same amount of steam-sterilized AMF inoculum.
In April 2010, the grass Arrhenaterum elatius L. J. Presl & C. Presl, the non-leguminous forb Plantago lanceolata L. and the leguminous forb Trifolium pratense L. were sown directly in the pots using a regular grid of three individuals per species (distance between plants 4 cm); plant species always had the same neighboring species. Initially, we sowed two seeds per position and later removed emerging surpassing smaller seedlings. Seed material was obtained from a commercial supplier (Rieger-Hofmann, Blaufelden, Germany). Pots were irrigated daily with a constant volume of tap water. Mesocosms were subjected to natural light cycle; average air temperature during the course of the experiment was 25.2 ± 1.2 °C at 35.4 ± 3.4 % relative humidity. The pots were watered daily with a constant amount of tap water for all treatments.
Earthworms were introduced to the respective pots 28 days after plant seeding; by then all plant species were established. The earthworm treatment (“+E”) consisted of one individual of the anecic Lumbricus terrestris L. (fresh mass: 3.87 ± 0.20 g pot−1, mean ± SE) and two individuals of the endogeic Aporrectodea caliginosa Savigny complex (total fresh mass: 1.66 ± 0.06 g pot−1). L. terrestris were purchased from a fishing shop in Vienna, A. caliginosa was collected in the botanical garden of BOKU (Christian and Zicsi 1999). In order to avoid that earthworms act as vectors for mycorrhiza into the treatment pots, they were thoroughly washed and placed in a box containing sterilized soil for 2 days. This procedure was repeated once more; afterwards, earthworms were carefully washed free of attached soil, weighed and introduced into the respective treatment pots.
On day 65 after seeding, two juvenile specimens of the slug A. vulgaris (average length, 4 cm; fresh mass, 2.93 ± 0.12 g pot−1) were randomly placed on the soil surface of the respective pots. Slugs were collected in a garden near the city of Wiener Neustadt, Austria. Prior to their introduction into the pots they were kept in plastic boxes in a climate chamber (15 °C) and fed with fresh lettuce ad libitum for 5 days; feeding stopped 24 h prior to introduction to the pots. Slugs were left in the treatment pots for 5 days where they could freely choose their food plants; thereby, we wanted to avoid that a plant individual was completely removed by slugs and would hence affect the feeding on other plant species. Mesocosms were weekly randomized on the glasshouse bench to avoid a potential bias of microclimatic conditions.
Plant germination and growth was monitored on average every 3 days until day 39 after seeding. A plant was considered as germinated when its cotyledons were visible.
Destructive harvest of the pots took place between day 69 and 71 after seeding by first removing all slugs from the pots and counting and weighing them. Afterwards, each plant was cut at the soil surface. Maximum leaf length was measured for each of the three species, total number of leaves was counted for P. lanceolata and T. pratense, total number of stems was counted for A. elatius. Afterwards, one individual per plant species and pot was weighed and immediately frozen at −20 °C before analyzing the secondary metabolites therein (see below). Another individual per species was used to determine specific leaf area and leaf thickness (see below). The remaining plant material was oven dried at 50 °C for 48 h and weighed.
Pots were then flipped over, the soil carefully inspected for earthworms and roots therein sorted out for 7 min per pot. Roots were carefully washed free of soil over a 1-mm sieve under a jet of tap water. About half of the roots were stored in 50 % ethanol before analyzing AMF colonization, the other portion was dried at 55 °C for 48 h to determine dry mass. The percentage of root length colonized by AMF was assessed after ink-staining (Vierheilig et al. 1998) using the grid-line intersect method considering at least 100 intersections per sample under the microscope (Giovanetti and Mosse 1980).
Measuring plant quality and slug damage
Secondary metabolites were assessed on frozen samples after grinding the plant material in liquid nitrogen using pestle and mortar. One hundred milligrams of ground plant material was extracted with 2 ml of a solvent (methanol/acetic acid, 99:1, v/v) over night. Afterwards, the solute was evaporated with a Savant speed vac. Dry samples were re-dissolved with 75 μl of methanol and analyzed by high-performance liquid chromatography (HPLC). The system was a Dionex Summit equipped with a photodiode array detector and a Famos autosampler. The column was a Phenomenex Synergi Max C12, 150 × 2 mm, 5-μm particle size. The column oven was adjusted to 40 °C, and the flow rate was 0.2 ml min−1. Solvent A was water/methanol/o-phosphoricacid (9:1:0.5, v/v/v), solvent B was pure methanol. The gradient started with 100 % of A for 2 min and then linearly changed to 100 % of B within 98 min. The final concentration was held further for 10 min. Five microliters of sample solution were injected. UV spectra were recorded from 590 to 220 nm. The identification of iridoids and flavonoids was based on comparisons of UV spectra, retention times, and elution sequences with an in-house spectrum library that contained reference spectra of isolated and structure elucidated as well as commercially obtained secondary metabolites. As each species showed a specific composition of secondary metabolites, we included different secondary metabolites for each species in the evaluation: for A. elatius we considered flavonoids (apigenin derivates), ferulic acid and a group of unknown phenols; for T. pratense daidzein, glycitein, and genistein as well as five unidentified isoflavones; for P. lanceolata the iridoid glucosides catalpol and aucubin. These groups of secondary metabolites were consistently detected in the samples; other metabolites with only occasional appearances were not considered in the statistical analyses. The area of each peak was integrated to facilitate a comparison of secondary metabolite production within an investigated factor but not between plant species.
Oven-dried shoot samples were ground using a ball mill (Mixer Mill MM 200, Retsch, Haan, Germany) and analyzed for total carbon (Ctot) and nitrogen (Ntot) concentration using an elementary analyzer (LECO-CN2000, LECO Corp., Saint Joseph, MI, USA).
Specific leaf area (SLA, square centimeter per gram) was calculated after scanning the biggest leaf of each plant species per pot using a flatbed scanner (300 DPI) and measuring the leaf area with an image analysis software (Scion Image, www.scioncorp.com) and dividing this area by the respective dry mass after drying at 55 °C for 24 h.
Slug herbivory was assessed during the harvest by carefully inspecting all leaves for damage and estimating the leaf area eaten by slugs using millimeter paper. By using the specific SLA ratio per leaf, we were able to convert the eaten area into consumed biomass.
Homogeneity of variances was tested using the Levene’s test; normality of residuals was checked using qq-plots. Data were log transformed when they were not fulfilling the assumptions of analysis of variance (ANOVA). Three-way ANCOVAs with AMF, earthworms and plant species as factors were used to compare individual variables among treatments. Tukey’s HSD tests were used for pairwise multiple comparisons between treatments. We used the individual age of a plant (i.e., number of days past germination or emergence), initial slug mass pot−1 and initial earthworm mass pot−1 as covariables in the analyses. Root mass did not meet ANOVA assumptions even after transformation and was therefore analyzed using the non-parametric Kruskal–Wallis test. All statistical analyses were performed using the software package R.2.10.1 (R Development Core Team 2008, www.Rproject.org). Values given in the text are arithmetic means ± 1 standard error. Effects 0.05 > P < 0.10 were considered as marginally significant.
Mycorrhization of plant roots was significantly higher when earthworms were present (14.3 ± 2.7 vs. 34.5 ± 2.9 % for –E vs. +E treatments, respectively; F = 25.672, P < 0.001; generally, no mycorrhization was detected in –M pots). At harvest of the pots we found 0.86 ± 0.18 g pot−1earthworms in –M and 0.83 ± 0.10 g pot−1 earthworm fresh mass in + M pots; AMF had no impact on earthworm fresh mass recovery (t test: P = 0.880). At harvest, we found all slug individuals introduced; slug fresh mass at the end of the experiment was 2.64 ± 0.19 g pot−1, which is 93 % of the initial fresh mass (t test: P = 0.634). Neither earthworms nor AMF affected slug fresh mass. Seed germination differed between species: 50 % seed germination was reached for T. pratense after 7 days, for A. elatius after 9 days, and for P. lanceolata after 11 days. Twenty-five days after seeding, the maximum germination was reached for all species: 100 % for T. pratense, 98 % for P. lanceolata, and 85 % for A. elatius. The presence of AMF had no impact on the time of germination or on the number of germinating seeds (data not shown).
Of the individual plant species, shoot mass of T. pratense was significantly higher (P < 0.001) and P. lanceolata marginally significantly higher (P = 0.051) in +M pots than −M pots (Fig. 1a, Table 1). Earthworms had no effect on shoot mass of individual plant species; however, there was a significant interaction between AMF and earthworms on T. pratense shoot mass (P = 0.011) with similar shoot mass at +M but a decrease in shoot mass at −M (Fig. 1a, Table 1). Total shoot mass was significantly affected by both earthworm and AMF (Fig. 1b, Table 1). Root dry mass per pot was 1.358 ± 0.150 g and unaffected by AMF or earthworms (Table 1). All T. pratense roots showed root nodules; however, these were not quantified.
Plant species differed significantly in their leaf Ctot, Ntot, C/N ratio, total secondary metabolites, and specific leaf area (Table 2 , Table 3); across plant species earthworms significantly affected Ntot and total secondary metabolites and marginally significantly C/N ratios, AMF only tended to affect specific leaf area (Table 2 , Table 3). Regarding leaf quality variables, several significant interactions between earthworms and AMF were detected (Table 3). Earthworms significantly affected Ctot and specific leaf area of A. elatius and total secondary metabolites of P. lanceolata but did not affect leaf quality of T. pratense (Table 3). AMF significantly affected total secondary metabolites of P. lanceolata (P < 0.001) and Ntot (P < 0.001) C/N ratio (P < 0.001) and specific leaf area (P = 0.045) of T. pratense (Table 3).
Slugs were observed climbing on all three plant species. Of individual plant species only herbivory on T. pratense was significantly affected by AMF (P < 0.001) or earthworms (P = 0.001; Fig. 2a, Table 4 ). Total plant mass consumed by slugs was significantly affected by AMF (P = 0.007) and earthworms (P = 0.013; Fig. 2b, Table 4 ). Leaf consumption by slugs differed significantly between plant species (P < 0.001); this was influenced by AMF or earthworms (significant interaction terms; Table 4 ).
In the slug’s diet, relative consumption of P. lanceolata was 42 % reduced by AMF and remained unaffected by earthworms; relative consumption of T. pratense was 342 % increased by AMF (P < 0.001) and significantly reduced by earthworms (P < 0.001; Fig. 3 ; Table 4 ).
This study demonstrates that the feeding behavior of an aggressive slug in many agroecosystems can be affected by interactions between earthworms and AMF. The documented influence of earthworms and/or AMF on the food selection of these generalist slugs suggests potential far-reaching consequences on the structure, plant diversity and functioning of grassland communities (South 1992; Frank 2003; Peters et al. 2006), which definitely merit further attention.
From previous studies on effects of earthworms or AMF in isolation, we already know that plant growth, plant development, and insect herbivores can be affected by either AMF or earthworms (Scheu 2003; Smith and Read 2008). Total root biomass was surprisingly unaffected by the activity of both soil organisms suggesting a rather slow response of roots to these soil organisms, and that root biomass (e.g., as opposed to root length) represents a too insensitive trait to differentiate between these two soil organisms.
Previous studies investigating combined effects of earthworms and AMF provide some hints of potential underlying mechanisms (Tuffen et al. 2002; Wurst et al. 2004b; Eisenhauer et al. 2009; Milleret et al. 2009; Zarea et al. 2009; Wurst and Forstreuter 2010; Zaller et al. 2011c). However, the lack of a general pattern point to context-specific interactions where different species of earthworms, AMF and plants and different experimental settings yield different results.
Overall, slugs preferred the legume and the forb over the grass although leaf quality variables did not clearly indicate less palatability of the latter. The tendency of molluscs to avoid grasses has been noted previously (Dirzo 1980) and may in the long term contribute to an increased abundance of grasses in such model systems. We expected to see either preference for plants with high nutrient contents and avoidance of less palatable plants or compensatory feeding with more damage on plants with thinner leaves (higher SLA values) because we assumed that slugs need to consume more leaf material to achieve a given nutrient value or avoid inhibiting substances (South 1992; Zaller et al. 2003). However, it seems that all assessed leaf quality variables interact in complex ways especially in a situation where herbivores could freely choose their food sources. The shift in the functional group preference from P. lanceolata in –M treatments to T. pratense in +M treatments is likely due to an increased foliar N content of the latter species with mycorrhiza. Of the three species, T. pratense had the highest Ntot and lowest C/N ratio across treatments, however was only preferred in +M treatments. The lack of a relationship between plant quality and slug herbivory has been found previously suggesting that other factors than plant quality are more important (Peters et al. 2000; Zaller et al. 2003; Zaller et al. 2013a). The possibility exists that the greater overall abundance of food may have influenced consumption in this experiment (Arnone et al. 1995), for instance that slugs preferred the least abundant plant species. However, in our experiment slug consumption was not influenced by the quantity of available food (Figs. 2 and 3 ) which agrees with Cook et al. (1996). Other explanations could be that slugs just sample the available foods, even those which are less palatable, or, that slugs require a varied food intake so that uncommon and often unpalatable foods may be eaten (South 1992). Fenner et al. (1999) tested the palatability of 29 plant species for the slug Deroceras reticulatum using food-choice experiments and it was found that P. lanceolata is about three times more palatable than T. pratense; a pattern that was observed in the current experiment only in treatments without AMF. Assuming that the results from this food-choice experiment with a different slug species can be transferred to our experimental scenario this suggests that AMF may reduce the palatability of P. lanceolata as compared to T. pratense. The finding that AMF made the legume T. pratense more palatable indicates that AMF improved the nutrient availability, agreeing with numerous studies showing that plant nutritive value was higher in the presence of mycorrhiza (Bennett et al. 2006; Zaller et al. 2011a). Slugs consumed three times more biomass of the legume in presence of AMF; however, this effect was alleviated by the presence of earthworms. Earthworms have recently been found to alleviate insect herbivore damage (Wurst 2010) and quantitatively reduce secondary metabolites of P. lanceolata (Wurst et al. 2004b)—the current study confirms this also for slugs. Although slugs fed well on plant material, their fresh mass was slightly lower at the end of the experiment referring to some stress during the course of the experiment.
In our experiment, we saw several interactions between AMF and earthworms suggesting that different effects are induced at different levels. We found significant effects of earthworms and AMF on secondary metabolites of P. lanceolata, which is in accordance with previous reports (Wurst et al. 2004a). The former study also found AMF induced reduction in Ntot and earthworm-induced reductions in catalpol concentrations which was not confirmed by our results (data not shown). Our study suggest that the effects of earthworms and AMF go beyond a simple amelioration of the plants’ nutritional status involving other interactions that might influence plant community structure (Hempel et al. 2009; Zaller et al. 2011b).
We observed a decline of earthworm biomass over the course of the experiment irrespective of AMF treatment. Some decline in earthworm biomass is frequently observed in earthworm laboratory studies, especially when experiments lasted several months (e.g., Wurst et al. 2004b; Zaller et al. 2013b). In the current study, we observed regular earthworm activity by surface castings until the end of the experiment; however, we did not quantify this activity and did not count the number of earthworms present at harvest. Therefore, we cannot show whether the biomass loss derives from escaping earthworms or mortality during the course of the experiment. The decline in earthworms could also be due to low bacteria or fungi biomass in soil due to sterilization (Bonkowski et al. 2000) or due to the use of rather small (more sensitive) individuals of A. caliginosa. Hence, some of the reported earthworm effects could also result from nutrient input caused by decomposing worm tissue rather than from actual earthworm activity. In previous experiments with the same substrate type and earthworm species, we documented earthworm activity throughout several months (Zaller et al. 2013b) with earthworm recovering rates of up to 93 % (Zaller et al. 2011c).
Taken collectively, our results show that the feeding habits of slugs in this simple plant community can be affected by both earthworms and AMF. In a previous experiment, we showed that slug herbivory is also affected by the diversity of plant communities with 40 % lower herbivory in communities containing 12 plant species as compared to those containing only three plant species (Zaller et al. 2013a). Effects of earthworms on slug herbivory were greater in low diverse than in high diverse communities (Zaller et al. 2013a).
Whether effects of earthworms and AMF, however, will also be similar under field conditions remains to be investigated. To what extent differential herbivory by an invasive slug species between invasive and native plant species changes species composition of ecosystems has not been studied yet. In any case, these sizeable effects of both earthworms and AMF on these invasive slugs adds further evidence for belowground control of plant community structure via modifying aboveground herbivore behavior. Moreover, these results provide impetus for more attention directed towards belowground–aboveground interactions in order to gain a better insight into processes structuring the diversity and functioning of grassland communities.
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We are grateful to Susanne Sochurek for providing the slugs and to Norbert Schuller and Lina Weissengruber for their help in the laboratory and during the harvest. This work was supported by the Austrian Science Fund (FWF project no. P20171-B16).
Raphaël Trouvé and Johann G. Zaller contributed equally to this work.
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Trouvé, R., Drapela, T., Frank, T. et al. Herbivory of an invasive slug in a model grassland community can be affected by earthworms and mycorrhizal fungi. Biol Fertil Soils 50, 13–23 (2014). https://doi.org/10.1007/s00374-013-0827-1
- Aboveground–belowground interactions
- Invasive species
- Plant–soil interactions
- Soil ecology
- Symbiotic fungi