Invasive Drosophila suzukii outnumbers native controphics and causes substantial damage to fruits of forest plants

Impacts of biological invasions are diverse and can have far-reaching consequences for ecosystems. The spotted wing drosophila, Drosophila suzukii , is a major invasive pest of fruits, which negatively affects fruit and wine production. However, little is known about the ecological impact of this fly species on more natural ecosystems it has invaded, such as forests. In this study, we investigated the use of potential host plants by D. suzukii at 64 sites in different forest communities in Switzerland from mid-June to mid-October 2020. We examined more than 12,000 fruits for egg deposits of D. suzukii to assess its direct impact on the plants. We recorded symptoms of fruit decay after egg deposition to determine if D. suzukii attacks trigger fruit decay. In addition, we monitored the drosophilid fauna with cup traps baited with apple cider vinegar, as we expected that D. suzukii would outnumber and potentially outcompete native controphics, especially other drosophilids. Egg deposits of D. suzukii were found on the fruits of 31 of the 39 potential host plant species studied, with 18 species showing an attack rate > 50%. Overall, fruits of Cotoneaster divaricatus (96%), that its presence might have far-reaching ecosystem-level consequences. The rapid decay of fruits attacked by D. suzukii leads to a loss of resources and may disrupt seed-dispersal mutualisms through the reduced consumption of fruits by dispersers such as birds. We 19a and 26f/g for our study, as they include a comparable range of fruiting plants. In addition, we investigated forest edges, as they serve as important habitat for a large range of fruiting plants. We examined the three forest communities at four sites ≥ 1 km apart, from 400 to 1165 m a.s.l. At each site, we selected four 25 m × 25 m plots of the particular forest community from the available grid cells (also 25 m × 25 m) in a stratified random design, using a vegetation mapping GIS in the canton of Zurich (Kanton Zürich 2020) and vegetation maps in the canton of Zug. We applied the following criteria in selecting plots: (1) distance between plots ≥ 150 m, (2) distance to the forest edge ≥ 150 m (due to the shape of the area, only a distance of ≥ 70 m was possible at the site “Zollischlag”). We measured the distances between sites, between plots and to the edge of the forest using the mapping platform of the Swiss Confederation (www. map.geo.admin.ch) and subsequently checked them in the field. We reviewed the forest community classification in the field based on indicator plant species. We defined the centre of the plots as the tree nearest to the actual centre point of the 25 m × 25 m area. We moved a selected plot to the adjacent grid cell if the area was temporarily unstocked (n=2), was covered with logging residues (n=1), or had no characteristics of the respective forest communities (n=3). We investigated forest edges at four sites with four plots each in the canton of Zug. We selected two sites at low elevations (400–600 m a.s.l.)


Introduction
Biotic exchange and subsequent invasions by non-native species in natural and humanmodified ecosystems are among the greatest threats to biodiversity worldwide (Wilcove et al. 1998;Pyšek et al. 2020). They can have far-reaching consequences for ecosystems (Vilà et al. 2010), including their functioning (Mack et al. 2000;Ehrenfeld 2010), and for human well-being (Shackleton et al. 2019), and they can cause extraordinary economic costs (Pimentel et al. 2005;Diagne et al. 2021). The perception and recognition of impacts of biological invasions, as well as how they are measured, are diverse and depend on the variables and scales considered (Jeschke et al. 2014). While assessments of economic impacts are measured in terms of economic costs, ecological impacts are evaluated as measurable changes to the properties of an ecosystem by a non-native species. However, the ecological impact of an invader is not easy to define or quantify, due to the context dependency of impacts, the variation in the per capita effect within and across species, and the complex interactions between invaders and their biotic and abiotic environments (Pyšek and Richardson 2010;Ricciardi et al. 2013).
Invasive non-native species may affect native species on the level of individuals (e.g. fecundity, mortality), populations (e.g. abundance, genetic diversity), communities (e.g. species richness and composition, trophic structure) and ecosystems (e.g. nutrient cycling, physical habitat, overall structure and function) (Parker et al. 1999). The impact of a non-native species on native populations and communities varies greatly in temporal (Strayer et al. 2006) and spatial (Mollot et al. 2017) terms and depends critically on the abundance and trophic position of the invasive species (Bradley et al. 2019). This explains why the extent of ecological impact varies greatly between invaders (Kumschick et al. 2015;Lapin et al. 2021).
Insects make up a large proportion of introduced species (DAISIE 2009; Seebens et al. 2017). They are usually introduced accidentally, rarely reach large populations, and/ or are often not noticed. However, a small minority become highly abundant and ecologically significant (Liebhold and Tobin 2008). Impacts of non-native insects on native species and ecosystems have many potential mechanisms, but only a very small proportion of non-native insects have been studied regarding their ecological impacts (Kenis et al. 2009). While direct impacts through mechanisms such as predation or competition are more obvious, indirect impacts, such as apparent and exploitative competition or alteration of interactions between native species, often remain unexplored (Traveset and Richardson 2006;White et al. 2006). For example, a meta-analysis of the effects of the invasions of the Argentine ant (Linepithema humile) showed that areas with L. humile from the dispersal of such microbes, as they obtain signals from their metabolic products for finding sugar resources (Madden et al. 2018).
Drosophila suzukii exploits resources that usually consist of small separate units and are patchy and ephemeral, i.e. they support only one generation. The temporal and spatial constraints of these unpredictable resources may favour generalists (Jaenike 1990). Niche breadth usually correlates positively with geographical range size (Slatyer et al. 2013), but does not necessarily explain invasion success (Carscadden et al. 2020). Following this general rule, the temporal and spatial niche breadth of the invasive D. suzukii have been shown to be relatively large compared with other Drosophila species in Japan (Yamamoto 1984). Besides using fruits as its preferred substrate for oviposition, it has also been found to develop on fungi (Kimura 1976) and can even complete development on chicken manure (Stockton et al. 2019). Within its invasive range, D. suzukii can use the fleshy fruits of many crops and wild plants (e.g. Poyet et al. 2015;Arnó et al. 2016;Kenis et al. 2016). In the year 2020, 198 plant species representing 40 families were already confirmed as host plants (Little et al. 2020), so the fly can be considered extremely polyphagous (sensu Normark and Johnson 2011).
Polyphagous herbivores (or generalists) are more impacted by plant toxicity than specialists (Ali and Agrawal 2012), as specialisation in phytophagous insects is thought to assist in the evolution of adaptations to overcome plant defences (Ehrlich and Raven 1964). However, D. suzukii hardly needs to specialise to overcome plant defences. On the one hand, because fleshy fruits are generally intended to be eaten by vertebrates (Lei et al. 2021), the pulp of such ripe fruits is rather easily digested (Cipollini 2000). On the other hand, the association with microbes may help with detoxification and digestion (Douglas 2009(Douglas , 2015. Fruits share particular volatiles across plant species (Prasanna et al. 2007). As a resource specialist utilising particular plant structures, i.e. fruits, with predictable odour cues, it may not be crucial for D. suzukii to specialise on particular plant species in order to increase host location, because olfactory responses to substrate-relevant volatiles of a resource instead of a plant species enables coping with a much narrower range of odours (e.g. Becher et al. 2012;Cunningham and Zalucki 2014;Cunningham et al. 2016).
Drosophila suzukii's attacks on the fruits of agricultural crops cause considerable economic damage to fruit growers through yield losses and the need to take measures to prevent attacks and minimise damage (Bolda et al. 2010;Knapp et al. 2020). Research on D. suzukii as a fruit crop pest is therefore ongoing and diverse. In recent studies, the occurrence of D. suzukii outside agricultural crops has been investigated to assess pest pressure from adjacent habitats. Woodlands have been shown to be suitable refugia and overwintering habitats (Briem et al. 2016;Pelton et al. 2016;Thistlewood et al. 2018;Wallingford et al. 2018) and can provide a large reservoir of hosts that produce fruits, ensuring continuity of resource availability over time (Poyet et al. 2015;Arnó et al. 2016;Elsensohn and Loeb 2018;Thistlewood et al. 2019). Therefore, large numbers of D. suzukii can be expected in forests, as has also been shown in trapping case studies (e.g. Briem et al. 2018;Haro-Barchin et al. 2018;Santoiemma et al. 2018), and population densities are likely to be more constant and higher than in semi-open habitats such as agricultural landscapes. So far, almost no research has been conducted to address the ecological impact of this fly on the ecosystems it has invaded. Roche et al. (2021) highlighted how D. suzukii may produce ecological changes to eastern forests in the USA. Invasion by D. suzukii may have consequences for food resources and, consequently, on species with which they compete for fruits. Competitive interactions, i.e. competition for shared resources or interference between species, generally increase with increasing phylogenetic relatedness (Li et al. 2015) and functional similarity (Dick et al. 2017) between the invader and the native species. Accordingly, D. suzukii could affect native drosophilids due to two main mechanisms. First, D. suzukii can use a wide range of substrates for oviposition, which gives it a competitive advantage over native drosophilids (Karageorgi et al. 2017;Silva-Soares et al. 2017). Unlike other drosophilids that use damaged and overripe fruits, D. suzukii has an enlarged, serrated ovipositor which makes it possible for females to pierce the skin of fruits (Atallah et al. 2014). It thus can use undamaged fruit, i.e. it can occupy fruits earlier than other drosophilids. Second, according to the enemy release hypothesis, a lower parasitisation rate leads to a larger population size (Keane 2002;Shea 2002), and parasitisation is an important cause of mortality for drosophilid larvae (Janssen et al. 1988;Fleury et al. 2009).
In this study, we assessed the use of potential host plants in forests by examining egg depositions of D. suzukii, reflecting its direct effect on the plants. Since there is a diverse abundance and varying availability of host plants within a plant community, which affects the choice of host plants for D. suzukii, we selected different forest communities and forest edges as study sites. We addressed the following questions: (1) Are there differences in the potential host plants of D. suzukii growing in different forest communities? (2) To what extent are the potential host plants attacked by D. suzukii, and what are the factors influencing the attack rates?
Due to the large numbers of D. suzukii trapped in previous studies, we expected that this species would outnumber and potentially outcompete native controphics, especially drosophilids. To test this hypothesis, we trapped drosophilids during the study period and addressed the following questions: (3) What proportion of drosophilid individuals are D. suzukii? (4) Does the proportion of D. suzukii differ among forest communities? (5) Does the abundance of D. suzukii affect the abundance of other drosophilids?

Study area
We conducted our study in the adjacent cantons of Zug (47.092440-47.218600°N, 8.407940-8.680231°E; elevation 400-1200 m a.s.l.) and Zurich (47.163290-47.365790°N, 8.424865-8.687711°E;440-1165 m a.s.l.) in Switzerland from June to November in 2020 (Fig. 1). In both regions, the annual average temperature ranges between 4-6 °C at higher elevation sites to 10-12 °C at lower elevation sites and the annual precipitation ranges between 1100-1300 mm and 1700-2000 mm at sites in the canton Zug and 900-1100 mm and 1100-1300 mm at sites in the canton Zurich (climate norm values 1991-2020; Federal Office of Meteorology and Climatology MeteoSwiss; extracted from https://map.geo.admin.ch/). We selected the forest communities 7a (GALIO ODORATI-FAGETUM TYPICUM), 19a (ABIETI-FAGETUM LUZULETOSUM) and 26f/g (ACERI-FRAXINETUM MERCURIALIDETOSUM) (see Ellenberg and Klötzli 1972) for our study, as they include a comparable range of fruiting plants. In addition, we investigated forest edges, as they serve as important habitat for a large range of fruiting plants. We examined the three forest communities at four sites ≥ 1 km apart, from 400 to 1165 m a.s.l. At each site, we selected four 25 m × 25 m plots of the particular forest community from the available grid cells (also 25 m × 25 m) in a stratified random design, using a vegetation mapping GIS in the canton of Zurich (Kanton Zürich 2020) and vegetation maps in the canton of Zug. We applied the following criteria in selecting plots: (1) distance between plots ≥ 150 m, (2) distance to the forest edge ≥ 150 m (due to the shape of the area, only a distance of ≥ 70 m was possible at the site "Zollischlag"). We measured the distances between sites, between plots and to the edge of the forest using the mapping platform of the Swiss Confederation (www. map.geo.admin.ch) and subsequently checked them in the field. We reviewed the forest community classification in the field based on indicator plant species. We defined the centre of the plots as the tree nearest to the actual centre point of the 25 m × 25 m area. We moved a selected plot to the adjacent grid cell if the area was temporarily unstocked (n=2), was covered with logging residues (n=1), or had no characteristics of the respective forest communities (n=3). We investigated forest edges at four sites with four plots each in the canton of Zug. We selected two sites at low elevations (400-600 m a.s.l.) and two at high elevations (800-1000 m a.s.l.). We defined these plots as areas of 12.5 m × 50 m along the forest edge (instead of 25 m × 25 m). Where possible, the forest edges were orientated in different cardinal directions. Forest edge sites were ≥ 1 km apart and plots were separated by ≥ 250 m. All sites were located in managed forests.

Field surveys of potential host plants
We considered any fleshy-fruited species, characterised by a high fruit water content, a potential host plant. We used the term "fruit" for all fruit types (i.e. berries, drupes, aggregate drupelets, aggregate nutlets and pomes), independent of the tissue of origin of the pulp. We also examined the aril of European yew (Taxus baccata) for egg deposition and included it under the term "fruit" below.
We mapped all potential reproducing host plant species in each plot (25 m × 25 m or 12.5 m × 50 m = 625 m 2 ) and noted its occurrence. We used an estimated dominance value to determine the area (m 2 ) covered by a plant species, and used this value and the recorded height to calculate the plant species' volume. For each potential host plant at each field survey per plot, we estimated the seasonal phenology and the number of ripe fruits present, assigning maturation stage between 0 and 2, corresponding to the majority of plant individuals: 0 = no ripe fruits, 0.25-0.75 = before main fruit maturity (some ripe fruits), 1.0-1.25 mainly ripe fruits, 1.5-1.75 = after main fruit maturity (more overripe, fermented fruits than ripe fruits), 2 = no more fruits. Since fruit ripening is usually associated with a change in colour, we used colour change as an indicator of the maturity of the examined fruits. In some species, such as European fly honeysuckle (Lonicera xylosteum), rowan (Sorbus aucuparia) or alder buckthorn (Frangula alnus), changes in fruit flesh firmness during ripening were not advanced at the time of colour change. We judged these fruits to be ripe when they also softened. After maturity, fruits enter senescence (the period during which chemical synthesis pathways give way to degradation processes). As an indicator of the "overripe" stage, we used loss of moisture, which becomes visible as a loss of turgor. At the end of the field survey, we calculated the maturity period with the unit of half a month and estimated the amount of fruit, both per potential host plant species per plot. The exact method used for these estimates depended on the species and was based on counts (e.g. all observed fruits, fruits per square metre, fruits per individual plant, or infructescence). We then extrapolated counts to the plot level. The number of fruits was likely underestimated by this approach and was thus a rather conservative estimate. Fruits that were removed, destroyed or lost due to drought stress near the end of the ripening process were not subtracted from the estimated numbers (see Suppl. material 1: Table S1 for month of fruit maturity, number of fruits, and occurrence (volume) of potential host plant species of Drosophila suzukii in the study plots).
Near the plots and in the same forest communities, we additionally examined native potential host plants that occurred in less than three plots (Lonicera alpigena, Taxus baccata, Prunus spinosa, Crataegus laevigata, Lonicera periclymenum, Viburnum lantana). We conducted this additional investigation to estimate the average attack rate of plants with infrequent occurrence on the plots, but we excluded these fruits from the statistical analyses.
European brambles (Rubus L. subg. Rubus) are taxonomically divided into three sections: Rubus, Corylifolii and Caesii (with one species, Rubus caesius). The most abundant species in our plots were R. hirtus agg. (sect. Rubus), occurring in the plots of forest community 19a, and R. villarsianus (sect. Corylifolii), occurring in the plots of forest communities 7a and 26f/g. Especially at the forest edges, but also in the forest communities 26f/g and 7a, more than one species of the sections Rubus and/or Corylifolii occurred in the plots. We did not identify the described and named species of the sections Rubus and Corylifolii in the plots and therefore used the term Rubus fruticosus corylifolius aggr. as the taxonomic unit.

Investigation of fruit attacks by Drosophila suzukii
We examined ripe fruits at an accessible height (up to 2 m) for egg deposition using a hand lens (10× magnification). If we observed at least one D. suzukii egg on the fruit, we considered the fruit "attacked", regardless of the number of egg deposits or larvae (for literature on the number of eggs per host plant, see e.g. Lee et al. 2015;Poyet et al. 2015;Olazcuaga et al. 2019; for development potential in different hosts see e.g. Arnó et al. 2016;Kenis et al. 2016;Tonina et al. 2016). We examined at least 10 fruits per population or individual of a potential host plant per plot, and we removed the examined fruits from the plants. If multiple individuals of a plant species occurred in the plot, we examined several individuals. In the case of large populations of brambles (R. fruticosus corylifolius agg.) or bilberry (Vaccinium myrtillus), i.e. covering > 25% of the plot area, we randomly selected 5 areas of 1 m 2 for investigating egg deposition. Egg deposition by D. suzukii is detectable for only a limited time, due to decay of the fruit substance, rotting, development of the larvae, feeding by other animals, or secondary infections such as grey mould. No larvae in a damaged fruit does not allow inference of non-infestation. Further, damaged fruits may in turn be used as egg-laying substrate by other drosophilids. Therefore, we used only ripe, undamaged fruits to study egg deposition on potential host plants.
We investigated the fruits of European holly (Ilex aquifolium) for egg deposition after the field surveys because they had not yet reached fruit maturity during the study period. To check the oviposition activity of D. suzukii, we simultaneously examined fruits of the European dwarf elder (Sambucus ebulus) and brambles (Rubus fruticosus corylifolius aggr.) occurring near the European hollies under investigation. We did not examine European mistletoe (Viscum album) and common ivy (Hedera helix), which were also present in the plots, for D. suzukii attacks, as their fruit ripening period fell well outside our study period. The ripe fruits of the wild strawberry (Fragaria vesca) often showed numerous feeding marks and damage, such that egg deposition by D. suzukii could rarely be detected. We therefore decided not to investigate attacks further and excluded wild strawberry from the analyses. We could confirm its use as a host, however, as adults hatched from collected fruits and we found numerous drosophilid larvae in otherwise intact fruits.

Fruit and decay traits
We compiled fruit traits of the investigated plant species from Herrera (1987), Snow and Snow (1988), Eriksson and Ehrlen (1991), and Stiebel (2003) and from databases (eFloras 2021, TRY 2021). When the records of fruit traits were comparable or convertible, we included the data from several literature references and used the average value. We included the fruit traits: type, colour, diameter (mm), mass (g), water content of the pulp (%), sugar content of the pulp (glucose and fructose, % of dry mass), lipid content of the pulp (% of dry mass), protein content of the pulp (% of dry mass), pH, persistence of individual fruits (days) and "attacked by non-dispersal frugivores" (%). In addition, we used the amount of ripe fruit and the maturation start and duration, based on our field assessments (see section "Field surveys of potential host plants"), as fruit traits in the analyses.
Fruit decay is a complex natural phenomenon that is co-determined by numerous conditions. It occurs as a result of physical and chemical damage, enzymatic digestion, and especially microbial activity. The fruit skin, which serves as an external barrier, is damaged by the egg deposition of D. suzukii. We documented the fruit response to egg deposition, i.e. decay, to determine if attacks trigger fruit decay. We recorded the following symptoms of fruit decay: oviposition scar, denting, oozing of pulp, reduction of fruit substance/loss of shape, and colour change. We categorised the symptoms as mild (1), moderate (2) or severe (3).

Adult trapping
At each site of the forest communities (including forest edges), we installed two baited (80-100 ml) transparent plastic cup traps covered by a red lid with 3 mm diameter entry holes (Profatec AG, Malans, Switzerland) to trap Drosophilidae including D. suzukii. As an attractant, we used a mixture of apple cider vinegar and water (3:1; apple cider vinegar IP-Suisse, Denner AG, 8045 Zurich, Switzerland; acetic acid 50 g/l) with 1-2 drops of liquid soap (Oecoplan Abwaschmittel, Coop, 4002 Basel, Switzerland) per 5 dl. We positioned the traps at a height of 1.2-1.5 m on branches of plants that do not bear fleshy fruits, mostly beech (Fagus sylvatica), at a distance of 150-200 m from the field survey plots. We installed the traps from 22/06/2020 to 07/07/2020, during the first session of the egg deposition assessment. At the forest edges, we placed the traps approx. 3 m inside the forest (from the shrub belt). We kept the traps in the same positions throughout the experiment and visited them on the same dates as the egg deposition assessments. Therefore, each sampling period of adult drosophilids also lasted 20 days.
During each sampling session, we removed the contents of the traps and preserved them in ethanol, and we renewed the bait. We sorted the trap content into different taxa, which we identified to different taxonomic levels. We identified the non-native D. suzukii and other drosophilids to the species level using the identification key of Bächli et al. (2004). "Domestic species", in particular Drosophila simulans and Drosophila immigrans, and other non-native species (e.g. Drosophila curvispina and Chymomyza amoena) were occasionally trapped. Other non-native drosophilid species accounted for < 1% of all trapped individuals. Therefore, we used the term "native drosophilids" for all drosophilids other than D. suzukii. We identified other Diptera to the family level following Oosterbroek (2006). See Suppl. material 2: Table S2 for a list of the trap catches. Since trap captures of a single trap during our study period should not be considered as replicates, especially because of varying phenology in different species (e.g. Bahder et al. 2016), we used the totals of trap captures per trap for the analysis.

Statistical analyses
We carried out all statistical analyses using R version 4.0.2 (R Core Team 2020). We tested all models for multicollinearity using the 'check_collinearity' function of the performance package (Lüdecke et al. 2021). We performed a test for dispersion, zero inflation and residual diagnostics with the DHARMa package (Hartig 2022).

Differences in fruiting plant communities
To test whether the composition of the plant communities differed between the forest communities with respect to the plants with fruits relevant for D. suzukii, we conducted non-metric multidimensional scaling (NMDS) based on a Bray-Curtis distance matrix (function 'metaMDS', package vegan; Oksanen et al. 2020). We defined the abundance of plant species as the estimated number of fruits per study plot and season, square-root transformed. We used the 'adonis' function in vegan (permutational multivariate analysis of variance, PERMANOVA) to test for statistical differences between the forest communities.

Attack rate and probability of fruits of different plant species
We applied a binomial generalised mixed effects model (package glmmTMB; (Brooks et al. 2017)) to test for differences in fruit attacks between forest communities (including forest edges) and plant species. The ratio of attacked to unattacked fruits per study plot and time of recording (cbind(N attacked, N not attacked)) was the response variable, whereas the forest community, the plant species, the elevation (m a.s.l.), the number of ripe fruits, the fruit maturity status, and the canton were the predictor variables. We included study plot as a random term to account for the nested study design. We used an additional observation-level random factor due to dispersion issues. We simplified our model stepwise by excluding the factor with the highest p-value and comparing the two models with the anova function based on a CHI 2 -test. If the more complex model did not differ significantly in model performance from the simpler model, we used the latter. This procedure resulted in the exclusion of canton and elevation (height_NN) from the final model.
We calculated the attack probabilities (LS-means ± SE) of the different plant species in the forest communities and plotted them using the emmeans package (Lenth 2022) based on the final model.

The role of fruit traits in fruit attack and decay
We explored whether fruit traits could explain observed differences in attack rates. We first used NMDS to illustrate the fruit trait space of the 39 studied plant species. See the section "fruit traits" for a list of the fruit traits considered. We treated each plant species in each forest community separately to relate it to attack rate and phenology, which both differed between forest communities for a given plant species. We used the Gower dissimilarity coefficient (Gower 1971) with Podani's (Podani 1999) extension for ordinal variables to create a distance matrix from our fruit trait data ('gowdis' function in the FD package (Laliberté and Legendre 2010;Laliberté et al. 2014).
We performed NMDS (with two axes) on the Gower distance matrix using the 'metaMDS' function in the vegan package (Oksanen et al. 2020). For illustration, we plotted attack rates of the fruits with different circle sizes and the phenology (month of maturation start) in different colours. We plotted traits post-hoc using the 'envfit' function in vegan, with 1000 permutations.
We used a binomial generalised mixed effects model (package glmmTMB; (Brooks et al. 2017) to test whether fruit attacks were related to fruit traits. The ratio of attacked to unattacked fruits per study plot and time of recording (cbind(N attacked, N not attacked)) was the response variable, whereas fruit availability (amount of fruit per plot), start of ripe fruit availability and duration of ripe fruit availability (both 0.5 month resolution), fruit colour, fruit diameter, sugar content of the pulp, and pulp pH were the predictor variables. We excluded fruit type and mass as well as water content of the pulp because of multicollinearity issues, and lipid and protein content of the pulp, as well as persistence and "attacked by non-dispersal frugivores", because they had too many missing values. We defined study plot and plant species as random terms to respect the nested study design and the repeated measures on plant species. We used an additional observation-level random factor due to dispersion issues. We standardised all quantitative variables to zero mean and unit variance using the 'decostand' function in the vegan package (Oksanen et al. 2020) to allow comparisons of effect sizes.
We used a general linear model ('glm') with a Poisson distribution to test whether fruit traits determined the decay status of the fruits after the attack by D. suzukii. We used the sum of decay traits (see section "fruit and decay traits") as the response variable and fruit traits (fruit diameter, pulp pH, pulp water, sugar, lipid and protein content) as predictors. We excluded fruit type and mass because of multicollinearity issues. We standardised all quantitative variables to zero mean and unit variance using the 'decostand' function in the vegan package (Oksanen et al. 2020) to allow comparisons of effect sizes.

Effects of D. suzukii on native Drosophilidae
To test for the effects of forest community and canton on the abundance of D. suzukii adults captured in traps, we used a binomial generalised mixed effects model (package glmmTMB; (Brooks et al. 2017) with the ratio of D. suzukii and native Drosophilidae (cbind(N D. suzukii, N native Drosophilidae)) as response variable and study plot as random term. We calculated the predicted proportions of D. suzukii (LS-means ± 95% CI) of the Drosophilidae species caught in the traps in the forest communities and plotted them using the emmeans package (Lenth 2022) based on the above model. To predict the abundance of native Drosophilidae as a function of the abundance of D. suzukii, we used a generalised mixed effects model with a Poisson distribution (package glmmTMB; Brooks et al. 2017) and defined forest community and canton as additional fixed effect and study plot as random term. We then plotted the predicted effect of N D. suzukii on N native Drosophilidae using the effects package (Fox and Weisberg 2018).
For all GLMs and GLMMS, we performed a type II Wald chi-square test using the R package car (Fox and Weisberg 2019). For most analyses we plotted the standardised estimates (effect sizes) using the 'plot_model' function in the sjPlot package (Lüdecke et al. 2021).

Attacks on potential host plants
The composition of the potential host plants of D. suzukii differed among forest communities (PERMANOVA, F=5.432, R 2 =0.22, P=0.001). The effect of forest community in structuring the plant communities is illustrated by the clustering of the forest communities in the ordination plot, except for the plant community of the study site of a former alluvial forest (site 26_1), which was more similar to forest community 7a than to 26f/g (Fig. 2). The greatest differences in the potential host plant composition were evident between forest communities 19a and 26f/g (pairwise adonis, R 2 =0.21, P=0.001). Forest community 26f/g and the forest edge community were most similar (R 2 =0.07, P=0.08).
At the study sites of forest community 19a, 7 potential host plant species with an estimated 34,000 fruits were recorded. At the study sites of the forest community 26f/g, there were 30 potential host plant species and an estimated 60,200 fruits; in forest community 7a there were 21 potential host plant species and 140,500 fruits, and at the forest edge study sites 32 potential host plant species and 161,000 fruits were observed (Suppl. material 1: Table S1).
Of the 39 potential host plants investigated, attacks were observed on 31 species. Overall, fruits of Cotoneaster divaricatus (96%), Atropa bella-donna (91%), Rubus fruticosus corylifolius aggr. (91%), Frangula alnus (85%) and Sambucus nigra (83%) were attacked particularly frequently (Suppl. material 1: Fig. S1, proportions of fruits attacked by Drosophila suzukii per plant species, separated by forest community). Based on the standardised assessments within the plots, the attack rates differed significantly between plant species and forest communities (Table 1), with forest edges exhibiting particularly high rates, followed by 7a. Lonicera alpigena, Taxus baccata and Atropa bella-donna had the highest probability of being attacked (Fig. 3). Larger numbers of ripe fruits and fruits in a later maturation stage corresponded to higher attack rates (Table 1). Canton and elevation did not have a significant effect on the attack rate and were dropped during model simplification.
The fruit trait space covered by the studied fruits was quite large (Fig. 4, left). The ordination plot illustrates that the attack rate differed greatly among plant species and was determined by the maturation start. Later maturation and longer availability of ripe fruits had a positive effect on attack rate (Table 2, Fig. 4 right). In addition, fruit    Table 1) probability estimates are shown (LS-means ± SE, back-transformed from the logit scale to the original probability scale). Only fruits observed within the plots were considered. N refers to the number of observations. For average attack rates per species, including fruits outside the plots, see Suppl. material 1: Fig. S1.  colour affected attack rate, with orange fruits having a lower attack rate than black fruits, and blue and red ones tending to be attacked less than black fruits. In addition, larger fruits and fruits with a higher pulp pH had higher attack rates. Of the studied fruit traits, only pulp sugar content affected fruit decay status after an attack by D. suzukii, with a higher sugar content leading to more severe symptoms of decay (Table 3, Fig. 5).  Table S2). The species composition of drosophilids in the different forest communities differed, e.g. D. alpina was only found in forest community 19a and species of the genus Amiota were mainly caught in forest community 26f/g. However, the drosophilid assemblages were dominated by D. suzukii, independent of forest community (Fig. 6). We trapped 21,758 (84%) D. suzukii and 4,117 (16%) native drosophilids in the forest community 19a, 17,031 (81%) and 4,054 (19%) in 26f/g, 15,708 (86%) and 2,528 (14%) in 7a, and 26,871 (91%) and 2,530 (9%) at the forest edge. The ratio of D. suzukii to native drosophilids did not differ significantly between forest communities (Wald Chi-squared test, Chi 2 =3.053, DF=1, P=0.384) and cantons (Chi 2 =0.036, DF=1, P=0.849). The proportion of D. suzukii predicted by the models (purple symbols) was between 0.81 and 0.95 (Fig. 6). The abundance of D. suzukii significantly affected the abundance of native drosophilids captured in the traps (Wald Chi-squared Test, Chi 2 =74.072, DF=1, P<0.001). The higher the abundance of D. suzukii, the smaller the abundance of native drosophilids predicted (Fig. 7). The forest community (Chi 2 =2.445, DF=3, P=0.485) and the canton (Chi 2 =0.192, DF=1, P=0.661) did not affect the abundance of native drosophilids.

Discussion
Drosophila suzukii, an invasive parasite of forest fruits, attacked 31 species from 15 different plant families (79% of all potential host plants investigated) in the forests of cantons Zug and Zurich. This not only confirms the broad host plant spectrum described in previous studies, but points towards a broad host use for reproduction. A broad host plant spectrum was to be expected, as D. suzukii is specialised on fruits and not on plant species per se. Furthermore, D. suzukii has been shown to have high plasticity in its host choice (Kienzle et al. 2020;Little et al. 2020). Our results suggest that a large number of fruiting plant species in forests are affected by D. suzukii, with likely far-reaching consequences for ecosystem processes (e.g. plant recruitment, resource availability for frugivores) and services (e.g. berry picking).

What influences attacks on the forest plants studied?
The observed broad host plant spectrum raises the question of what limits the host spectrum. Species of Rosa or Sorbus, which bear rather hard fruits, were hardly infested. We assume that the pulp and skin firmness act as a barrier to egg deposition, as insects have a limited ability to penetrate the skin of the fruit and to lay an egg in hard fruit flesh. It has been reported that the probability of oviposition increases as the force required to penetrate fruit skin decreases (Burrack et al. 2013;Lee et al. 2016). Further, within grape cultivars and single berries, berry skin resistance was found to explain the oviposition preferences of D. suzukii (Entling et al. 2019;Tonina et al. 2020). The fact that Ilex aquifolium was not infested was probably because its maturity coincides with the reproductive diapause of the fly . We found that the red or blue, soft-skinned fruits of Polygonatum (Asparagaceae) were hardly used as a host, although this genus is widespread in the fly's area of origin (eFloras 2021). Drosophila suzukii may not detect all of the numerous potential host plants because its ability to process multiple sensory inputs is limited (Bernays 2001). Polyphagous herbivores have been shown to be attentive to the volatiles that are shared across host species (Silva and Clarke 2020). As the Asparagaceae are relatively distantly related to other host plants, the fruits and their microbial association with Asparagaceae species might not share certain volatiles with other host plants, making them undetectable to the fly.
The fruits of our 39 potential forest host plants differed in several characteristics that affect host location and oviposition site selection (Markow 2019), reflected by differences in observed attack rates in our study. Within the host plant range of D. suzukii, preferences (disproportionate use of potential host plants, i.e. egg deposits) have also been shown for crops in agricultural systems (Lee et al. 2011;Burrack et al. 2013;Olazcuaga et al. 2019) and for wild and ornamental non-crop hosts (Poyet et al. 2015) when fruits were exposed to flies in laboratory assays. These preferences may be due to numerous characteristics of the fruit, such as colour, diameter, shape, volatile compound content, firmness, skin texture, or chemical composition, such as sugar content. In the field, several plant characteristics and the diverse abundance and fluctuating availability of host plants, as well as other biotic and abiotic factors of the host site, may also affect the choice of hosts, which makes comparisons of our findings with laboratory assays difficult.
Our non-metric multidimensional scaling (NMDS) indicated high variability in fruit traits and phenology in relation to attack rate. The attack rate varied among fruit colours, with black fruits being most frequently attacked. Drosophila suzukii has previously been shown to use colour as visual cue, but that colour contrast rather than colour appearance may be of greater importance (Little et al. 2019). While visual cues are of some importance, especially in behaviours such as courtship , the olfactory and gustatory systems of Drosophila are crucial for host localisation and selection (Anholt 2020). We therefore expect that other factors correlated with colour might be decisive. For example, the fruit type "pome" or "hips", which usually has high pulp firmness, mostly had a low attack rate and was often orange or red in colour. Larger fruit size also had a positive effect on attack rate. This could be because a larger surface area, especially with aggregated fruits such as brambles, makes it is easier for D. suzukii to find a preferred substrate, e.g. one without damage (mechanical or due to infection) or in an earlier maturation state. We also found that the attack rate increased with higher pulp pH (from pH 2.89 to 6.48). During host location and oviposition site selection, the fly can hardly detect a pH value, and thus this effect might be indirect. Microbes can act as the interface between insect herbivores and their hosts (Janson et al. 2008;Hansen and Moran 2014;Ljunggren et al. 2019). Drosophila suzukii, like other Drosophila, is strongly attracted to volatiles produced by microorganisms in particular yeasts associated with fruits (Wright 2015;Hamby and Becher 2016;Bueno et al. 2020). It has also been shown that yeast volatiles, not fruit volatiles, mediate attraction and oviposition in D. melanogaster (Becher et al. 2012). In general, within the range of the fruit pulp pH, yeast and bacteria thrive better at higher pH values (Barth et al. 2009;Howell 2016). Fruits with a higher pH may host more microbes and could therefore be more attractive and easier to locate. In addition, moulds (filamentous fungi), an important competitor of Drosophila larvae (Wertheim et al. 2002;Trienens et al. 2010), generally exhibit better growth in a lower pH environment (Zhao et al. 2020). This could have led to a lower attractiveness for D. suzukii in our study, as decreased egg deposition in response to grey mould (Botrytis cinerea) was observed in a recent study (Chakraborty et al. 2022).
Host preferences are considered evidence of specialisation (Loxdale and Harvey 2016). In this case, however, we would expect phylogenetic relatedness in the preferred hosts, which we did not find, as the plant species with the highest observed attack rate belong to very distinct plant clades. Since the larvae feed in particular on microbes, host preferences, unlike those of folivorous insects, are determined more by the quality of the substrate in promoting the yeasts and bacteria associated with D. suzukii than by the phylogeny of the host plants. Our results suggest that D. suzukii responds to common cues from multiple host species, as well as specific cues from individual host species, as has been shown for other polyphagous herbivores (Silva and Clarke 2020). Other polyphagous herbivores also exhibit preference hierarchies for their hosts (e.g. Clarke et al. 2011;Wang et al. 2017), which may change through learning (West and Paul Cunningham 2002). Preferences should evolve toward maximising offspring fitness (Jaenike 1978), although preferences do not always correlate positively with offspring performance (e.g. Valladares and Lawton 1991;Clark et al. 2011), because other ecological, behavioural and physiological factors additionally influence host choice and host use (Jaenike 1990). While D. suzukii deposited its eggs on fruits from 16 different plant families in our study, we do not expect its offspring to perform equally well across the host spectrum, because preferences of insects with a broader host plant spectrum are less strongly associated with better offspring performance than insects specialised on plants within a certain family (Gripenberg et al. 2010). However, invasions are biologically unusual situations, and D. suzukii cannot be expected to show strong adaptive patterns of host use yet, as it was only recently introduced. Thus, some differences in larval performance might be expected and have also been shown between many non-crop hosts of D. suzukii (e.g. Poyet et al. 2015;Kenis et al. 2016;Olazcuaga et al. 2019).
Plant communities differ floristically and phytophysiognomically (Braun-Blanquet 1932) because species traits and an interacting milieu affect performance across environmental gradients such as temperature, moisture and soil chemistry (Mcgill et al. 2006). Therefore, the abundance and availability of host plants among forest communities must also differ. In our NMDS of available fruits of potential host plants in the plots, the forest communities were clustered. This finding and our model results indicated that the availability of different plant species determines the use of the host plants, as the forest community affected the attack rate. In addition to the diversity of host plants in an area, other associational effects, such as the density and frequency of neighbouring host plants, can influence the likelihood of a particular plant being used as a host, as can the density of the particular host plant (Underwood et al. 2014). As stated by the resource concentration hypothesis (Root 1973), a high density of host plants may increase the likelihood that the fly will find the fruits and remain on the host plant. This was supported by our results, as the number of ripe fruits present in our plots strongly affected the attack rate. Furthermore, since optimal oviposition behaviour depends not only on the suitability of the substrate, but also on the probability of finding a more suitable host in the time available (Jaenike 1978), adherence to a particular host plant species might be advantageous. A large amount of fruits may be more obvious to D. suzukii and thus increase the attack rate. A strong preference for more apparent resources in complex environments has also been shown for D. melanogaster (Verschut et al. 2016).
Our results further show that a longer fruit duration of fruits present increased the attack rate. Plants with more fruits, and especially plants such as brambles that produce ripe fruits over a long period, ensure continuous availability of resources without the need to search for new hosts, thus promoting the presence of overlapping generations of D. suzukii on the same host, further increasing attack rate. In Switzerland, between four and eight generations of D. suzukii per year are expected (Wiman et al. 2014). In addition, prior experience with olfactory and visual cues can enhance host location (Silva and Clarke 2020). Furthermore, a later ripening date was related to a higher attack rate, which may occur when the peak of abundance of D. suzukii and the period of fruit maturity coincide. The predominant maturity status of the plants in the plots also affected the attack rate. The more advanced the maturity, the greater the attack rate of the ripe fruits investigated. An advanced maturity status attracts more flies (Keesey et al. 2015), but also indicates overlapping generations on the same plant.

Adult trapping revealed Drosophila suzukii as a dominant species
The high fruit attack rate observed in our study was also reflected in a high abundance and dominance of D. suzukii in trap catches, independent of forest community and elevation. This indicates the broad environmental tolerance of the fly. However, frequent occurrence in mountainous regions does not necessarily mean that D. suzukii inhabits these regions year-round, as studies from Japan and the Italian Alps suggest that the fly exhibits extensive movements between low and high elevations (Mitsui et al. 2010;Tait et al. 2018) and is capable of travelling distances of up to 9 km ). However, it can be assumed that the fly can survive the winter at these sites, as D. suzukii is firmly established on the island of Hokkaido in Japan, where winters average -4 to -12 °C (Kimura 2004).
Although our forest communities differed significantly in host composition, there were no differences in the proportion of D. suzukii between the forest communities. Drosophila suzukii accounted for 86% of the drosophilids caught during our study period. Recent snapshot studies of trap catches in forests also showed a high proportion of D. suzukii. In a survey in native riparian and non-riparian chestnut forest patches in northwestern Spain in August, D. suzukii accounted for 30% and 27% of the drosophilids caught in beer traps (Maceda-Veiga et al. 2021). Kremmer et al. (2017) reported 56% D. suzukii of the summed trap catches across natural habitat and crops in February (baited with apple cider vinegar). Studies in agricultural areas similar to our sites in terms of trapping period, climate and sampling method do not confirm D. suzukii as the most abundant taxon: D. suzukii accounted for 7% in Apulia, Italy (Antonacci et al. 2017), 11% in Kansas, USA (but baited with mashed banana; Gleason et al. 2019), and 18% in Washington, USA) (but some unmanaged habitats included; Bahder et al. 2016). Several factors could have caused these differences. First, agricultural and forested areas differ in biotic and abiotic factors, and species composition thus also differs (Burla and Bächli 1991). The assemblages of drosophilids, excluding D. suzukii, trapped in these agricultural areas were dominated by domestic species (distributed worldwide), while native species dominated in our area. Similarly, the occurrence of controphics, such as other insects, vertebrates or mould, and the occurrence of predators differ. Second, competition between D. suzukii and native species might be different in the two habitat types, due to differences in the occurrence of ecologically related species and available resources. Third, different measures taken to control the fly in agricultural fields might have reduced the populations of D. suzukii. However, these measures usually also affect other drosophilids. Fourth, forests can be expected to be the preferred habitat of D. suzukii, resulting in high overall proportions. Numerous forest fruits are suitable for the development of D. suzukii, due to its wide host niche (Little et al. 2020), and forests may offer preferred climatic conditions for D. suzukii, especially higher humidity Tochen et al. 2016;Eben et al. 2018).
Unlike in our study, surveys of drosophilid assemblages from trapping studies in various habitats in Asia, where D. suzukii is native or has been established for many years, do not show D. suzukii to be a dominant species: its proportion in relation to other drosophilids is reported to be up to 0.02 (e.g. Kaneko and Tokumitsu 1969;Toda 1992;Hirai et al. 2000;Guruprasad et al. 2010) and reached a value of 0.05 in a study in Korea (Lee 1964). Parasitisation is, however, an important mortality factor for drosophilid larvae (Janssen et al. 1988;Fleury et al. 2009), and the abundance of potential hosts is one factor determining the evolution of parasitoid host use (Novković et al. 2012). The degree of parasitisation is much higher in native populations (Torchin et al. 2003). The expected lower parasitisation of D. suzukii could be one of the main factors contributing to its frequent occurrence outside its native range, as escape from natural enemies can explain the success of introduced species (Keane 2002;Shea 2002).

Impact on native drosophilids
Our trap catches revealed that the abundance of D. suzukii was significantly negatively associated with the abundance of other drosophilids. Its dominance indicates a superiority over the native species. The heavily sclerotised, serrated ovipositor serves as a competitively unique trait (Karageorgi et al. 2017;Silva-Soares et al. 2017). Besides the capability of using a wider range of substrates for oviposition, we propose that the broader temporal niche of resource use is a competitive advantage. Drosophila suzukii can use substrates for oviposition earlier than other drosophilid species. Consequently, oviposition by D. suzukii induces substrate decay, rendering the substrate time-limited for the larval development of other fruit pulp consumers. While ripe fruits are inherently a temporally limited resource, this limitation is probably enhanced in forests compared with agricultural areas, because the fleshy fruits of wild plants are usually much smaller than those of cultivated plants. However, oviposition of D. suzukii on long-lasting larval habitats such as cultivated fruits may allow further use by other drosophilids (Rombaut et al. 2017; but see Entling and Hoffmann 2020).
Furthermore, D. suzukii may outcompete native drosophilids, due to different development times. This might lead to different competitiveness in forests and agriculture. Cold adaptation in Drosophila to colonise temperate climates appears to be associated with longer development times (Santos et al. 2006;Kinzner et al. 2018), and cosmopolitan human commensals ("domestic species") such as D. melanogaster, which originated in central equatorial Africa (Lachaise and Silvain 2004), have comparatively short development times (Markow and O'Grady 2005a). In laboratory experiments, it has been found that the presence of D. melanogaster on the substrate significantly reduced adult D. suzukii emergence, reflecting a difference in minimum development time (7 days for D. melanogaster and 11 days for D. suzukii at 25 °C; (Dancau et al. 2017;Shaw et al. 2018). Presumably, the presence of D. suzukii reduces native drosophilid emergence as well. Coexistence of drosophilids across food-limited resource patches is facilitated by aggregation over patches (eggs in clutches of more than one egg, as well as non-random distributions of ovipositing females), which creates partial refuges and allows inferior species to exist (Rosewell et al. 1990;Jaenike and James 1991;Sevenster and Alphen 1996;Rohlfs and Hoffmeister 2003). In addition, parasitism facilitates the coexistence of drosophilid species (Mitsui and Kimura 2000a). However, as an invasive species, D. suzukii is expected to be exposed to lower pressure from parasitoids (Torchin et al. 2003), resulting in larger populations. Unlike other drosophilids, D. suzukii has been shown not to aggregate over patches (Mitsui et al. 2006). Therefore, we suggest that it may exclude and outcompete other drosophilids in the exploitation of resource patches, which is supported by our results: higher abundance of D. suzukii was associated with lower abundance of other drosophilids.

Potential impact on host plants
Piercing of the skin of undamaged fruit by D. suzukii provides an entry point for infestation by pathogens, and inoculated microbes can act as a jump-start for decay.
Microbes that infect fruits have been hypothesised to make fruits unattractive to vertebrate frugivores that potentially compete for fruit pulp (Janzen 1977;Ruxton et al. 2014). Just as humans respond to infested fruit with rejection, birds have been shown to prefer intact fruit to infested fruit (e.g. Manzur and Courtney 1984;Jordano 1987;Borowicz 1988;Buchholz and Levey 1990;Cipollini and Stiles 1993;Traveset et al. 1995;but see Valburg 1992). Attacks by D. suzukii alter the attractiveness of the fruit because it changes the chemical composition and visual cues, such as colour, shape and reflective patterns. Since the choice of fruits by birds depends on visual perception (Schaefer and Ruxton 2011), we assume that attacks on fruits by D. suzukii could reduce the attractiveness for birds, resulting in reduced seed dispersal. This is because many host plants of D. suzukii rely especially on frugivorous birds for dispersal (Garcia et al. 2010). Negative effects on seeds are unexpected because attacks occur after seed set.
In the field, when we observed symptoms of fruit decay after D. suzukii attacks, we noticed that fruit decay progressed at very different rates among plant species, which may be due to their different compounds and compositions. For example, the bright red fruits of Lonicera alpigena were found to change into dry, brown fruit mummies (rotten fruits) within a short time, while fruits of Prunus padus had hardly any symptoms of decay and hung intact on the bushes for more than 40 days without decaying. On Prunus padus, a significant reduction in the number of emerged D. suzukii adults and a significant delay in the larval-pupal development time was detected when compared with Prunus avium (Alhmedi et al. 2019), where oviposition by D. suzukii is known to trigger microbial development (Ayyanath et al. 2018). Because larval development depends on the development of microbes (Sang 1956;Schwarz et al. 2014;Hamby and Becher 2016), decay within a short time indicates a strong response of microbial growth and development and better host suitability to D. suzukii offspring development. Among the fruit traits we studied, we found that the pulp sugar content determined the severity of the symptoms of decay after an attack by D. suzukii. The rapid decomposition of simple carbohydrates leads to rapid microbial growth (Zhao et al. 2020), explaining why more severe symptoms of decay were evident at higher sugar levels. Nutrient levels deplete over time as microbes and larvae consume the resources, so rapid fruit decay after an attack by D. suzukii means a loss of resources for other frugivores.

Conclusion
Almost half of the 39 studied forest plant species showed attack rates by D. suzukii of > 50%, with a high percentage showing severe symptoms of fruit decay after egg deposition. This may lead to reduced fruit consumption by vertebrate seed dispersers. Drosophila suzukii is a damaging agent for plants, and if the fly reproduces in large numbers, dispersal agents and host plants may both suffer. Besides the direct effect of parasitism of forest fruits by D. suzukii, leading to competition with other frugivorous species, the indirect effect of disrupting seed-dispersal mutualisms can have farreaching consequences for ecosystems. With ongoing climate change, these potentially severe ecological impacts might be amplified in temperate forests, as higher average and winter temperatures will most likely lead to shorter generation times and lower winter mortality, which will eventually further increase the pressure on forest fruits and the competitiveness of D. suzukii over native drosophilids.