Isotopic Overlap of Invasive and Native Consumers in the Food Web of Lake Trasimeno (Central Italy)

Simple Summary

An in-depth study of the feeding habits characterizing bioinvaders may provide key information on the magnitude of their impacts on recipient communities. Specifically, if invaders’ trophic niche is superimposed on that of native species, interspecific competition may increase, resulting in negative consequences for the competing species; alternatively, trophic niche divergence may occur, facilitating the invaders’ integration into the community. In the present study, the analysis of carbon and nitrogen stable isotopes was used to investigate the trophic overlap of native and non-indigenous consumers. We found a generally low degree of isotopic overlap in both the invertebrate and fish assemblage, a condition that may facilitate coexistence and, in turn, limit the strength of invaders’ impact. The only exception was the Louisiana crayfish Procambarus clarkii, which was demonstrated to interact with a wide spectrum of native invertebrate species, confirming the necessity of guaranteeing appropriate measures of control and mitigation of its ecological impacts.

Abstract

An advanced characterization of the trophic niche of non-indigenous species (NIS) may provide useful information on their ecological impact on invaded communities. Here, we used carbon and nitrogen stable isotopes to estimate pairwise niche overlaps between non-indigenous and native consumers in the winter food web of Lake Trasimeno (central Italy). Overall, a relatively low pairwise overlap of isotopic niches was observed between NIS and native species. The only exception was the Louisiana crayfish Procambarus clarkii, which showed a relatively high and diffuse overlap with other native invertebrates. Our findings highlighted a high niche divergence between non-indigenous and native species in Lake Trasimeno, suggesting a potentially low degree of interspecific competition that may facilitate coexistence and, in turn, limit the strength of impacts. The divergent results obtained for the Louisiana crayfish indicate that additional control measures for this invasive species are needed to mitigate its impact on the Lake Trasimeno system.

1. Introduction

The introduction and establishment of non-indigenous species (NIS hereafter) represents one of the most important anthropogenic threats to the biodiversity, functioning, and integrity of freshwater ecosystems [1,2]. This is particularly evident when NIS establish themselves and become invasive, altering the structure and functions of recipient communities and whole ecosystems and ultimately causing environmental and economic harm [3,4,5,6].

A growing body of evidence is accumulating on the negative impacts of bioinvaders in both lentic and lotic environments, but an overwhelming majority of these investigations are focused on the effects of single species or single taxonomic groups [7]; see also the studies used for the meta-analyses performed by, e.g., [8,9,10,11]. In freshwater environments, however, repeated introductions may take place, resulting in a generalized occurrence of multispecific NIS assemblages [12,13]. Multiple invaders are recognized to exert a wide spectrum of cumulative effects, from synergistic to negligible to antagonistic [14,15,16,17]; yet, compared with plant species, multiple animal invasions have generally received less attention, in particular in freshwater ecosystems [18]. The establishment of invasive consumers necessarily implies a “rewiring” of trophic interactions directly through predation or indirectly through competition [19,20,21,22,23]. From this perspective, the study of interspecific feeding interactions at a whole-food-web scale may provide important insights into the combined ecological effects and impacts of multiple invaders on native species.

In the present study, we focused on Lake Trasimeno, a laminar basin in central Italy characterized by a diverse assemblage of non-indigenous species of fish and invertebrates [24]. The investigation was performed in winter with the aim of estimating the trophic overlap between NIS and native species and to assess their potential for competition. If trophic resources are limiting, NIS establishment within a recipient community can generally result in increased interspecific competition; this may ultimately be reflected in competitive exclusion and local extinction of the inferior competitor or, alternatively, in trophic niche divergence, which would facilitate the integration of invaders and their coexistence with indigenous species [25,26,27]. Here, we conjectured a generally high degree of trophic overlap and potential for competition between native and non-indigenous consumers, given the occurrence of highly invasive species in both the invertebrate and fish assemblages of the lake (see further in the next sections). However, in temperate lakes, the abundances of primary producers, intermediate consumers, and top predators undergo strong seasonal fluctuations with minima generally observed in winter; see, e.g., [28,29,30] for Lake Trasimeno. Accordingly, an alternative hypothesis was that the low abundances and metabolic requirements of native and non-indigenous consumers in the colder season should correspond to conditions of weak competitive interactions and reduced trophic overlap [31,32]. We tested these hypotheses using stable isotope analysis (SIA). This methodology has in the last decades gained huge popularity in the study of aquatic food webs and the assessment of the response of marine and freshwater ecosystems to anthropogenic pressures, including bioinvasions [33,34]. In recent years, methods for estimating trophic niche space—conventionally relying on direct observations and stomach content analysis—have improved by integrating SIA-based approaches (“isotopic niche” in [35,36]). The δ¹³C and δ¹⁵N values of living organisms vary at both an inter- and intraspecific level; accordingly, consumers will occupy a different isotopic space depending on the resources they exploit, making an organism’s isotopic niche a useful proxy of its trophic niche [37,38]. Carbon and nitrogen stable isotopes were measured in winter in fish, invertebrates, and basal resources collected from a littoral site of the lake. We generated Bayesian standard ellipse areas of each species representing relative niche widths in the isotopic space, and pairwise overlaps were computed. In addition, the mean proportional overlap between the native and non-indigenous assemblages (all species combined) was used as a metric for estimating the cumulative influence of the latter on the transfer of energy and matter in the lacustrine food web [39,40,41].

2. Materials and Methods

2.1. Site Description

This study was performed in Lake Trasimeno (43.133283° N, 12.100064° E, central Italy; Figure 1). The basin is the largest laminar lake in Italy (124 km², average depth: 4.7 m, maximum depth: 6.3 m). It is located 257 m above sea level, it has a single artificial effluent, and it is fed by several ephemeral creeks. Given the relatively small extension of the watershed (396 km²), its hydrological regime is driven by precipitation, and strong seasonal and interannual oscillations in water level and chemistry are observed [42,43]. Further details on the lake’s morphometric and hydrological characteristics are provided in Ludovisi and Gaino [42] and in Bresciani et al. [44].

The lake is included in a regional natural park within the Natura 2000 European network. The littoral zones are generally muddy and dominated by common reeds (Phragmites australis (Cav.) Trin. ex Steud.), with dense beds of aquatic macrophytes of the genera Myriophyllum, Stuckenia, and Vallisneria extending in summer especially along the southern coasts of the lake [45]. The native macroinvertebrate community includes a diverse assemblage of annelid, mollusk, insect, and crustacean taxa [46]. Conversely, the assemblage of native fish species currently comprises only five species, i.e., Esox cisalpinus Bianco & Delmastro 2011, Anguilla anguilla Linneus 1758, Tinca tinca Linnaeus 1758, Scardinius erythrophthalmus Linnaeus, 1758, and Squalius squalus Bonaparte 1837. Two additional species, Sarmarutilus rubilio Bonaparte 1837 and Cobitis bilineata Canestrini 1865, are considered to be extinct since the 1970s [46,47].

Phytoplankton are characterized by wide seasonal fluctuations and are dominated in summer by the cyanophyceans Cylindrospermopsis spp., whereas in winter, chlorophyceans of the genera Hyaloraphidium and Scenedesmus together with cyanophyceans of the genus Leptolyngbya represent the most abundant taxa [48,49]. Similarly, remarkable seasonal variations characterize the abundance and composition of the zooplankton, dominated in summer by the cladoceran Daphnia galeata Sars 1864 and by copepods of the genus Cyclops in winter [48,50,51]. During the last century, the lacustrine community has been drastically altered by the introduction of several NIS of different origins (

Table 1. Non-indigenous invertebrate and fish species currently occurring in Lake Trasimeno. Information on the years of first record were collated from [24,53,54,55,56].

Group	Species	Year of First Record
Invertebrates	Branchiura sowerbyi Beddard 1892	<2000
	Dikerogammarus villosus Sowinsky 1894	2017
	Dreissena polymorpha Pallas 1771	1999
	Physella acuta Draparnaud, 1805 #	<1900
	Procambarus clarkii Girard 1852	2000
	Sinanodonta woodiana Lea 1834	2017
Fish	Alburnus arborella Bonaparte 1841	1975
	Ameiurus melas Rafinesque 1820	1984
	Atherina boyeri Risso 1810	1920
	Carassius auratus Linneus 1758	1990
	Ctenopharyngodon idella Valenciennes 1844 *	1986
	Cyprinus carpio Linneus 1758 #	Roman age
	Gambusia holbrooki Girard 1859	1927
	Knipowitschia panizzae Verga 1841	1976
	Lepomis gibbosus Linneus 1758	1926
	Micropterus salmoides Lacépède 1802	1990
	Perca fluviatilis Linneus 1758	1911
	Pomatoschistus canestrinii Ninni 1883	1988
	Pseudorasbora parva Temminck and Schlegels 1825	1999
	Sabanejewia larvata De Filippi 1859	1970
	Silurus glanis Linneus 1758 *	Unconfirmed

* Nonreproductive population. # Given the time since introduction, here, the species was considered autochthonous.

). They comprise invertebrates (e.g., the decapods Procambarus clarkii and Dikerogammarus villosus, the bivalves Dreissena polymorpha and Sinanodonta woodiana, and the tubificid Branchiura sowerbyi) and 15 species of fish, including Ameiurus melas, Carassius auratus, Lepomis gibbosus, Micropterus salmoides, and Perca fluviatilis [24,47,52].

2.2. Sample Collection and Laboratory Procedures

In early February 2018, fish and crayfish were captured by fishers operating fyke nets in Sant’Arcangelo, a locality in the southern sector of the lake (43.089788° N, 12.156246° E). Nets were located at an approximate distance of 50 m from the coast at a depth of 2–2.5 m. Collected specimens were transferred to the laboratory in refrigerated containers (4 °C), where they were euthanized by thermal shock (−80 °C for 10 min), identified to the lowest taxonomic level possible, and enumerated. Subsequently, a ruler was used to determine to the nearest mm the total standard length of fish specimens (i.e., from the tip of the snout to the posterior end of the last vertebra); a caliper was used to measure in mm the total length of crustacean individuals from the tip of the rostrum to the end of the telson.

For stable isotope analysis, the dorsal muscle tissue of fish and the caudal muscle of crustaceans was dissected from each specimen using a ceramic scalpel, dried (60 °C, >1 week), and powdered using a mortar and a pestle. Subsequently, subsamples (0.8 ± 0.02 mg, mean ± 1 SE) were pressed into Ultra-Pure tin capsules (Costech Analytical Technologies, Valencia, CA, USA) and analyzed using an elemental analyzer connected to an isotope ratio mass spectrometer (Thermo Scientific Flash EA 1112, Waltham, MA, USA and Delta Plus XP, Suzhou, China, respectively). Isotopic contents were expressed in conventional δ unit notation as ‰ deviations from international standards:

$${\mathsf{\delta }}^{13}\mathrm{C} \mathrm{o}\mathrm{r} {\mathsf{\delta }}^{15}\mathrm{N}=\left[\left({\mathrm{R}}_{\mathrm{s}\mathrm{a}\mathrm{m}\mathrm{p}\mathrm{l}\mathrm{e}}/{\mathrm{R}}_{\mathrm{s}\mathrm{t}\mathrm{a}\mathrm{n}\mathrm{d}\mathrm{a}\mathrm{r}\mathrm{d}}\right)-1\right]\times 1000$$

(1)

where R = ¹³C/¹²C or ¹⁵N/¹⁴N. Pee Dee belemnite (PDB) limestone carbonate and atmospheric nitrogen (N₂) were used as standards for carbon and nitrogen isotope ratios, respectively. Analytical precision based on the standard deviation of replicates of internal standards (International Atomic Energy Agency IAEA-NO-3 for δ¹⁵N and IAEA-CH-6 for δ¹³C) was 0.2‰ for both δ¹⁵N and δ¹³C.

Invertebrates were collected in a shallow embayment (approximate depth = 1 m) situated in front of the area where fish and crayfish were sampled. Details of the location are provided in Mancinelli et al. [57], while information on the sampling procedures are included in Mancini et al. [58] and Ludovisi et al. [59]. In brief, the embayment has muddy bottoms and artificial rocky shores, characterized in winter by accumulations of decaying plant material, including P. australis leaf litter and mixed detritus of macrophytes belonging to the genera Myriophyllum, Potamogeton, and Vallisneria. At the time of the sampling, in the embayment, the temperature and dissolved oxygen concentration of surficial water (depth = 10–12 cm) were 12.3 ± 0.2 °C and 9.8 ± 0.8 mg L⁻¹, respectively (mean ± 1 SE, n = 3; YSI^® 556 MPS, Yellow Springs, OH, USA). A handheld pond net (mesh size = 1 mm) was swept five times in floating leaf litter accumulations to capture macroinvertebrates; additional specimens were collected by hand from rocks and artificial hard substrata. Samples were subsequently placed in Falcon tubes or in other plastic buckets containing filtered lake water. Samples of the superficial sediment layer (3 replicates) were collected using a methacrylate core (400 mm length, 114 mm ∅) driven into the sediment to a depth of approximately 10 cm and were then transferred to plastic bags.

All samples were transported in refrigerated containers (4 °C) to the laboratory, where invertebrates were identified to the lowest taxonomic level, enumerated, kept in distilled water for 12 h to clear gut contents, and eventually euthanized by thermal shock (−80 °C for 10 min). The total length of each individual was determined to the nearest 0.1 mm either using a digital caliper for palaemonids (see Results (Section 3)) or a stereo microscope (Nikon^® SMZ1270, Tokyo, Japan) equipped with a CCD camera for the remaining taxa. For gastropods, the maximum shell length was measured. Subsequently, the caudal muscle of each palaemonid was dissected and dried (60 °C, >1 week); all the remaining invertebrates were dried whole with the exclusion of gastropods, which had their shells removed. Sediment samples were wet-sieved on a 1 mm screen; invertebrates retained in the sieve were collected and processed according to the procedures already described.

The isotopic data obtained in the present investigation were complemented with those published in Mancini et al. [58] and Ludovisi et al. [59]. They were performed at the same location as this study and include δ¹³C and δ¹⁵N values of benthic invertebrates and zooplankton. The study by Ludovisi et al. [59] was carried out in 2018 and coincided with the present investigation, while that of Mancini et al. [58] was performed in February 2016. The isotopic characteristics of the components of the food web at the study site were assumed to have remained unchanged between the sampling years. The assumption was tested for a subset of invertebrate species (Appendix A; see the next section).

2.3. Data Analysis

In general, all statistical analyses were carried out in the R statistical environment v. 4.2.2 [60]. For univariate analyses, data were checked for normality and homoscedasticity (Shapiro–Wilks and Levene’s tests, respectively) and log- or square root-transformed if required. When significant effects were detected by ANOVA tests, post hoc bivariate comparisons were performed using Tukey HSD tests. Bivariate relationships were tested using Pearson’s coefficient of correlation, while F-tests were used to verify differences between slopes or intercepts.

To preliminarily verify whether the invertebrate taxa sampled in 2016 and 2018 (Appendix A) differed significantly between years in their isotopic values and CN contents, a Euclidean distance similarity matrix of Z-scaled δ¹³C, δ¹⁵N, and total carbon and nitrogen (both expressed as %) values was calculated. Subsequently, a type III (partial) permutational analysis of variance [61] (PERMANOVA hereafter) with 9999 permutations was performed using the function adonis in the vegan package v. 2.6-2 [62] with “species” and “year” as the fixed and random factors, respectively. Since no significant effects were detected (see Results), the two isotopic datasets were cumulated and treated in further analyses as one.

Independently from the sampling date, the tissues of several invertebrates and fish showed C:N ratios > 3.5 (Appendix A), indicating a significant contribution of lipids to the tissues’ carbon pool [63]. Since lipids are depleted in ¹³C compared to proteins and carbohydrates and can significantly bias δ¹³C estimations [64], samples with a C:N ratio > 3.5 had their δ¹³C values mathematically corrected for lipid content [63].

Isotopic niche overlaps for non-indigenous and native consumers were estimated using the SIBER package v. 2.1.6 [65]; consumers’ standard ellipse area (SEA, expressed in ‰²) was used as a measure of the core population isotopic niche [66]. Given the different number of specimens per taxon included in the analyses (Appendix A), we calculated a sample-size-corrected version (SEA_c hereafter) [66] representing the core (40%) isotopic niche area and allowing for robust comparisons across species of varying sample sizes. SEA_c estimations were used for illustrative purposes; for interspecific statistical comparisons, we calculated the Bayesian equivalent SEA_B of SEA_c [66] using 100,000 posterior iterations of SEA_c to compute credible intervals. Specifically, pairwise contrasts were performed by calculating the probability that the SEA_B of one species was different from that of a second one with a probability of at least 95% [66].

SEA_c estimations were further used to calculate interspecific isotopic niche overlaps. They were determined assuming negligible competitive interactions between invertebrate and fish consumers; in addition, for each of the two groups, overlaps were calculated between NIS and native species as well within NIS and native assemblages separately.

Overlaps between two species were expressed as the % ratio of the estimated overlap itself and the sum of the nonoverlapping area of the ellipses for each species [66], a measure conceptually consistent with other classical symmetric indices, such as Pianka’s niche overlap index O [67]. Overlaps were considered significant when the shared isotopic space between species was >60%, a criterion identical to that used by Schoener for his dietary overlap index [68].

3. Results

3.1. Invertebrates

Invertebrate taxa sampled in 2016 and 2018 (Appendix A) showed negligible between-year variations in their isotopic values (PERMANOVA, factor “year”: Pseudo-F_1,72 = 0.79, P_{Monte Carlo} = 0.44; interaction factor “species × year”: Pseudo-F_5,61 = 0.3, P_{Monte Carlo} = 0.97). Additionally, post hoc taxon-specific comparisons highlighted negligible temporal differences (min t = 1.16, P_{Monte Carlo} = 0.27 for P. clarkii). Accordingly, the data collected during the two sampling occasions were cumulated and treated as a single dataset containing isotopic measurements for a total of 163 specimens belonging to 14 invertebrate taxa (Appendix A). Their mean δ¹³C values varied considerably between −25.6 in the zebra mussel D. polymorpha and −14.1 in the pond shrimp P. antennarius (Figure 2).

The isopod Asellus aquaticus and the leech Erpobdella octoculata were the most depleted and enriched in ¹⁵N, respectively (Figure 2; 5.2 ± 0.8 vs. 10.2 ± 0.2, mean ± 1 SD). Overall, invertebrates showed significant interspecific differences in isotopic composition (PERMANOVA, Pseudo-F_13,162 = 26.3, P_{Monte Carlo} = 0.0001); this result was generally confirmed by further post hoc bivariate comparisons (

Table A2. PERMANOVA post hoc bivariate comparisons performed on δ¹³C and δ¹⁵N values of invertebrate consumers. Monte Carlo-corrected probability values (P_{Monte Carlo}) are reported. Significant P_{Monte Carlo} values are indicated in bold. Codes in parentheses refer to those reported in column headings.

Taxon	1	2	3	4	5	6	7	8	9	10	11	12	13
Anodonta anatina (1)
Asellus aquaticus (2)	0.0002
Branchiura sowerbyi (3)	0.02	0.0009
Chironomus plumosus (4)	0.0003	0.0003	0.13
Dikerogammarus villosus (5)	0.0001	0.0001	0.0001	0.0001
Dreissena polymorpha (6)	0.0001	0.0001	0.0001	0.0001	0.0001
Echinogammarus veneris (7)	0.01	0.0004	0.03	0.12	0.0001	0.0001
Erpobdella octoculata (8)	0.0001	0.0001	0.0001	0.0001	0.0001	0.0001	0.0007
Erythromma sp. (9)	0.0001	0.0001	0.0001	0.0001	0.09	0.0001	0.0001	0.0001
Ischnura sp. (10)	0.0001	0.0002	0.0001	0.0001	0.08	0.0001	0.0004	0.0001	0.45
Palaemonetes antennarius (11)	0.0001	0.0001	0.0001	0.0001	0.002	0.0001	0.0001	0.0001	0.0001	0.0001
Physella acuta (12)	0.15	0.001	0.02	0.02	0.0001	0.0001	0.02	0.0013	0.0001	0.0001	0.0001
Procambarus clarkii (13)	0.17	0.07	0.31	0.49	0.0001	0.0001	0.51	0.03	0.07	0.19	0.001	0.12
Zooplankton (14)	0.49	0.002	0.44	0.17	0.0001	0.0001	0.05	0.0001	0.0001	0.0001	0.0001	0.18	0.29

in Appendix B). Noticeable exceptions were Chironomus plumosus vs. Branchiura sowerbyi and Echinogammarus veneris and, most importantly, Procambarus clarkii vs. a taxonomically heterogeneous assemblage including most of the invertebrates with the exclusion of Dikerogammarus villosus, Dreissena polymorpha, and Physella acuta (Table A2 in Appendix B).

In Figure 3, the sample-size-corrected standard ellipse areas (SEA_c) of invertebrate consumers are illustrated, while numerical values are reported in

Table 2. SEAc and SEA_B of invertebrate consumers expressed as ‰². For SEA_B, modal values and the corresponding 95% confidence intervals (in italics) are included.

Taxon	SEAc	SEAB	95%
Anodonta anatina	0.28	0.26	0.09	0.49
Asellus aquaticus	0.74	1.04	0.44	1.56
Branchiura sowerbyi	0.36	0.35	0.19	0.67
Chironomus plumosus	0.08	0.08	0.03	0.16
Dikerogammarus villosus	2.79	2.83	2.09	3.63
Dreissena polymorpha	0.23	0.23	0.09	0.42
Echinogammarus veneris	4.93	4.49	2.91	7.26
Erpobdella octoculata	0.2	0.21	0.06	0.39
Erythromma sp.	0.36	0.35	0.17	0.58
Ischnura sp.	0.07	0.08	0.04	0.22
Palaemonetes antennarius	1.72	1.56	0.56	3.02
Physella acuta	4.55	4.69	1.48	8.03
Procambarus clarkii	16.78	16.93	9.68	25.28
Zooplankton	1.12	1.09	0.27	2.08

together with the respective Bayesian estimates (SEA_B). Overall, modal SEA_B and SEA_c values were in good agreement, and the latter always fell within SEA_B 95% confidence intervals. The robustness of Bayesian estimations against potential biases related to variations in sample size was corroborated by the negligible relationship observed between SEA_B values and the number of specimens analyzed for each taxa (Pearson r = 0.27, p = 0.35, d.f. = 12).

Isotopic niche areas varied across the different taxa by a factor > 100 (Table 2). Among NIS, P. clarkii showed the highest SEA_B value (16.9‰²), one order of magnitude larger than D. villosus (2.8‰²). B. sowerbyi and D. polymorpha, conversely, were characterized by the lowest SEA_B estimations (0.3 and 0.2‰², respectively). Bivariate comparisons indicated significant differences in isotopic niche areas among all the taxa with the exclusion of B. sowerbyi and D. polymorpha (probability tests, B. sowerbyi ≠ D. polymorpha: p = 0.48; p > 0.95 for all the remaining comparisons). Similar to what was observed for NIS, native invertebrates showed a high heterogeneity in their modal SEA_B estimations (Table 2); P. acuta showed the largest value, close to that of E. veneris (4.7 and 4.5‰², respectively; probability test p = 0.62). In turn, they were significantly different from SEA_B values determined for both P. clarkii and D. villosus (probability tests, p always > 0.95). In contrast, Ischnura sp. and C. plumosus showed the smallest SEA_B (0.1‰²). Erythromma sp., A. anatina, and E. octoculata showed areas ranging between 0.3 and 0.2‰² (p < 0.95 for all bivariate comparisons), whereas for a second taxonomically heterogeneous group including P. antennarius, zooplanktonic crustaceans, and A. aquaticus, the estimated areas ranged between 1.6 and 1‰² (p < 0.95 for all bivariate comparisons).

SEA_c and SEA_B percent overlaps between NIS and native invertebrate species were generally low and well below the critical limit of 60% (Figure 4; see

Table A4. Interspecific overlaps in SEA_c and modal SEA_B values of non-indigenous and native invertebrate taxa. For the sake of succinctness, values lower than 0.01‰² are reported as “<0.01”. Percent overlaps are reported for both metrics; those lower than 1% are reported as “<1%”. For SEA_B modal values, 95% confidence intervals are included in italics.

NIS	Native	Overlap (SEAc)	% Overlap (SEAc)	Overlap (SEAB)	% Overlap (SEAB)	95% CI
Branchiura sowerbyi	Chironomus plumosus	<0.01	<1%	<0.01	<1%	<1%	<1%
	Echinogammarus veneris	0.07	1.36	0.08	1.37	1.19	1.54
	Physella acuta	0.13	2.75	0.08	1.96	<1%	4.35
Dikerogammarus villosus	Erythromma sp.	0.32	11.36	0.39	9.44	9.43	9.46
	Ischnura sp.	0.07	2.66	0.11	2.87	2.62	2.93
Dreissena polymorpha	Anodonta anatina	<0.01	<1%	<0.01	<1%	<1%	<1%
	Zooplankton	<0.01	<1%	<0.01	<1%	<1%	<1%
Procambarus clarkii	Asellus aquaticus	<0.01	<1%	<0.01	<1%	<1%	<1%
	Echinogammarus veneris	3.02	16.15	4.82	17.94	11.99	24.58
	Erpobdella octoculata	<0.01	<1%	<0.01	<1%	<1%	<1%
	Erythromma sp.	0.36	2.12	0.44	1.77	1.74	1.81
	Ischnura sp.	0.07	<1%	0.13	<1%	<1%	<1%
	Physella acuta	1.35	6.74	2.26	8.45	8.34	8.57

in Appendix C for modal SEA_B values and the respective 95% confidence intervals). The mean of nonzero SEA_c and SEA_B % overlaps was 3.3% and 3.4%, respectively, with values ranging between a minimum approximating 0% for P. clarkii vs. A. aquaticus and a maximum of 16 (SEA_c)–18% (SEA_B) for P. clarkii vs. E. veneris. Noticeably, the mean % overlap among native species was 7.1% and 6.4% (SEA_c and SEA_B % overlaps, respectively), with values ranging between a minimum approximating 0% for E. veneris vs. A. aquaticus and a maximum of 35.2 (SEA_c)–30.8% (SEA_B) for E. veneris vs. P. acuta (Figure 4;

Table A5. Interspecific overlaps in SEA_c and modal SEA_B values of native invertebrate taxa. For the sake of succinctness, values lower than 0.01‰² are reported as “<0.01”. Percent overlaps are reported for both metrics; those lower than 1% are reported as “<1%”. For SEA_B modal values, 95% confidence intervals are included in italics.

Native	Native	Overlap (SEAc)	% Overlap (SEAc)	Overlap (SEAB)	% Overlap (SEAB)	95% CI
Echinogammarus veneris	Asellus aquaticus	<0.01	<1%	<0.01	<1%	<1%	<1%
	Chironomus plumosus	<0.01	<1%	<0.01	<1%	<1%	<1%
Erpobdella octoculata	Asellus aquaticus	<0.01	<1%	<0.01	<1%	<1%	<1%
	Echinogammarus veneris	<0.01	<1%	<0.01	<1%	<1%	<1%
Ischnura sp.	Erythromma sp.	0.02	5.79	0.03	6.02	3.31	8.45
Physella acuta	Chironomus plumosus	0.08	1.86	0.07	1.15	0.05	3.49
	Echinogammarus veneris	2.47	35.21	3.16	30.95	22.84	42.12
Zooplankton	Anodonta anatina	0.24	20.38	0.27	18.12	10.22	26.04
	Chironomus plumosus	0.05	3.88	0.05	4.01	2.33	5.86
	Physella acuta	0.22	4	0.14	3.74	2.72	5.15

in Appendix C).

Beside E. veneris, P. clarkii showed overlaps > 1% also with P. acuta (8.4%) and with Erythromma sp. (1.8%), while D. villosus overlapped with dragonfly nymphs (i.e., 9.4% with Ischnura sp. and 2.9% with Erythromma sp.). Other NIS showed negligible overlaps with native taxa; however, P. clarkii showed a relatively high SEA_B % overlap with D. villosus of 15.8% (8.4–21.3%, 95% CI; Figure 4;

Table A6. Interspecific overlaps in SEAc and modal SEAB values of non-indigenous invertebrate taxa. For the sake of succinctness, values lower than 0.01‰2 are reported as “<0.01”. Percent overlaps are reported for both metrics; those lower than 1% are reported as “<1%”. For SEAB modal values, 95% confidence intervals are included in italics.

NIS	NIS	Overlap (SEAc)	% Overlap (SEAc)	Overlap (SEAB)	% Overlap (SEAB)	95% CI
Procambarus clarkii	Branchiura sowerbyi	<0.01	<1%	<0.01	<1%	<1%	<1%
	Dikerogammarus villosus	2.73	16.22	3.59	15.83	10.38	19.28

in Appendix C), indicating a potential interaction.

3.2. Fish

Isotopic analyses were performed on a total of 140 specimens belonging to 12 fish taxa (

Table A1. List of invertebrate and fish consumers sampled in the present study and in Mancini et al. [58]. The number of collected specimens is reported; for each taxon, the mean C:N ratio is included (±1 SE), together with the C:N ratio range, the mean length of individuals in mm (±1 SE), and the individual length range in mm. * = Shell length of bivalves.

Taxon	2018	2016	Total	Mean C:N	C:N Range	Mean Length	Length Range
Invertebrates
Anodonta anatina *	---	5	5	7.66 ± 0.61	7.04–8.32	99.7 ± 13.88	87–116
Asellus aquaticus	5	---	5	3.99 ± 1.12	2.77–5.78	8.47 ± 2.06	6.7–11.8
Branchiura sowerbyi	3	3	6	5.53 ± 0.23	5.22–5.75	46.83 ± 19.05	29–77
Chironomus plumosus	3	3	6	6.58 ± 0.39	6.14–7.09	5.8 ± 1.89	3.3–8.2
Dikerogammarus villosus	54	---	54	4.96 ± 0.45	4.31–5.9	12.71 ± 4.64	5.4–20.2
Dreissena polymorpha *	---	8	8	4.65 ± 0.36	4.28–5.21	17.63 ± 5.93	10–26
Echinogammarus veneris	16	4	20	5.52 ± 0.9	4.39–8.03	7.37 ± 1.14	5.3–9.3
Erpobdella octoculata	3	3	6	4.25 ± 0.24	3.89–4.51	14.17 ± 4.49	7–19
Erythromma sp.	12	---	12	3.94 ± 0.17	3.66–4.18	14.52 ± 1.59	12.4–16.5
Ischnura sp.	6	---	6	3.74 ± 0.09	3.61–3.86	9.11 ± 1.34	7.5–11.5
Palaemonetes antennarius	4	2	6	3.85 ± 0.15	3.67–4.08	17.33 ± 3.88	12–22
Physella acuta *	6	---	6	4.41 ± 0.33	4.04–4.87	9.5 ± 3.08	6–14
Procambarus clarkii	12	6	18	3.18 ± 0.25	2.33–3.46	97.26 ± 24.84	15–125
Zooplankton	---	5	5	7.49 ± 0.32	7.23–8.01	---	---
Fish
Ameiurus melas	6	---	6	3.15 ± 0.05	3.09–3.24	188.75 ± 6.18	184–197
Anguilla anguilla	6	---	6	4.89 ± 1.92	3.75–8.44	401.25 ± 40.49	370–460
Atherina boyeri	21	---	21	3.13 ± 0.32	2.45–3.65	62.95 ± 13.95	35–80
Carassius auratus	15	---	15	3.16 ± 0.13	2.94–3.39	203.87 ± 94.52	91–312
Cyprinus carpio	6	---	6	3.2 ± 0.2	2.93–3.43	326.83 ± 100.75	240–480
Esox cisalpinus	8	---	8	3.12 ± 0.02	3.07–3.14	308.38 ± 74.41	222–412
Lepomis gibbosus	26	---	26	3.3 ± 0.05	3.21–3.45	76.5 ± 13.37	45–95
Micropterus salmoides	7	---	7	3.14 ± 0.1	3.06–3.29	183.86 ± 17.14	165–210
Perca fluviatilis	19	---	19	3.19 ± 0.08	3.03–3.33	145.16 ± 32.06	58–205
Scardinius erythrophthalmus	8	---	8	3.11 ± 0.1	2.96–3.24	143.43 ± 22.45	120–182
Squalius squalus	8	---	8	3.29 ± 0.12	3.04–3.48	99.67 ± 46.65	53–150
Tinca tinca	10	---	10	3.23 ± 0.1	3.18–3.46	243.25 ± 45.96	160–300

, Appendix A). In general, they showed significant interspecific differences in isotopic composition (PERMANOVA, Pseudo-F_11,139 = 50.9, P_{Monte Carlo} = 0.001). The highest δ¹⁵N values were observed in Micropterus salmoides together with Perca fluviatilis, Esox cisalpinus, and Ameiurus melas, the latter two species showing negligible isotopic differences (

Table A3. PERMANOVA post hoc bivariate comparisons performed on δ¹³C and δ¹⁵N values of fish consumers. Monte Carlo-corrected probability values (P_{Monte Carlo}) are reported. Significant P_{Monte Carlo} values are indicated in bold. Codes in parentheses refer to those reported in column headings.

Taxon	1	2	3	4	5	6	7	8	9	10	11
Ameiurus melas (1)
Anguilla anguilla (2)	0.002
Atherina boyeri (3)	0.001	0.001
Carassius auratus (4)	0.001	0.35	0.002
Cyprinus carpio (5)	0.001	0.02	0.005	0.03
Esox cisalpinus (6)	0.94	0.001	0.001	0.001	0.001
Lepomis gibbosus (7)	0.001	0.001	0.001	0.001	0.001	0.001
Micropterus salmoides (8)	0.01	0.001	0.001	0.001	0.001	0.003	0.001
Perca fluviatilis (9)	0.05	0.001	0.001	0.001	0.001	0.05	0.001	0.04
Scardinius erythrophthalmus (10)	0.001	0.25	0.002	0.91	0.02	0.001	0.001	0.001	0.001
Squalius squalus (11)	0.001	0.04	0.002	0.11	0.47	0.001	0.001	0.001	0.001	0.17
Tinca tinca (12)	0.001	0.43	0.001	0.007	0.002	0.001	0.001	0.001	0.001	0.01	0.002

, Appendix B). The remaining species clustered in a group characterized by a lower enrichment in ¹⁵N and generally showing significant interspecific variations, with some notable exceptions represented by Carassius auratus vs. Cyprinus carpio, Scardinius erythrophthalmus, and Anguilla anguilla, the latter two characterized by negligible isotopic differences (Table A3, Appendix B). Lepomis gibbosus had δ¹⁵N values consistent with those characterizing this second group but with δ¹³C values significantly more enriched (Figure 2 and Table A3, Appendix B).

In Figure 5, the sample-size-corrected standard ellipse areas (SEA_c) of invertebrate consumers are illustrated, while numerical values are reported in

Table 3. SEAc and SEA_B of fish consumers expressed as ‰². For SEA_B, modal values and the corresponding 95% confidence intervals (in italics) are included.

Taxon	SEAc	SEAB	95%
Ameiurus melas	0.22	0.27	0.15	0.38
Anguilla anguilla	4.92	3.84	1.65	5.94
Atherina boyeri	1.29	1.18	0.74	1.87
Carassius auratus	2.12	1.91	1.16	2.39
Cyprinus carpio	0.29	0.24	0.11	0.65
Esox cisalpinus	0.02	0.02	0	0.03
Lepomis gibbosus	3.98	3.77	2.47	5.65
Micropterus salmoides	0.93	0.82	0.37	2.01
Perca fluviatilis	2.23	2.02	1.28	3.25
Scardinius erythrophthalmus	0.79	0.62	0.29	1.38
Squalius squalus	1.57	1.35	0.93	2.17
Tinca tinca	4.87	4.15	2.12	6.25

together with the respective Bayesian estimates (SEA_B). As observed for invertebrates, modal SEA_B and SEA_c estimations were in good agreement, and the latter were always included within SEA_B 95% confidence intervals. The robustness of Bayesian estimations against potential biases related with variations in sample size was confirmed by the negligible relationship observed between SEA_B values and the number of specimens analyzed for each taxa (Pearson r = 0.38, p = 0.21, d.f. = 10).

In general, SEA_B values varied across the different taxa by one order of magnitude (Table 3). Among NIS, L. gibbosus and A. melas were characterized by the largest and smallest areas (3.8 and 0.3‰², respectively), while P. fluviatilis, C. auratus, A. boyeri, and M. salmoides showed intermediate values ranging between 2 and 0.8‰². Bivariate comparisons indicated significant differences with a probability > 95% in the SEA_B of all the species with the exception of P. fluviatilis vs. C. auratus and A. boyeri vs. M. salmoides (probability tests, max p = 0.73 for the comparison P. fluviatilis ≠ C. auratus). Native fish varied in SEA_B values by a factor > 100, ranging between maxima of 4.2 and 3.8‰² observed for Tinca tinca and A. anguilla, respectively, and a minimum of 0.02‰² characterizing E. cisalpinus. S. squalus, S. erythrophthalmus, and C. carpio showed intermediate values ranging between 1.4 and 0.2‰²; all fish taxa showed significant interspecific differences in SEA_B values with the exception of T. tinca and A. anguilla (probability test, p = 0.56).

SEA_c and SEA_B percent overlaps between NIS and native fish species were generally higher than those observed for invertebrates (Figure 6, see

Table A7. Interspecific overlaps in SEA_c and modal SEA_B values of non-indigenous and native fish taxa. For the sake of succinctness, values lower than 0.01‰² are reported as “<0.01”. Percent overlaps are reported for both metrics; those lower than 1% are reported as “<1%”. For SEA_B modal values, 95% confidence intervals are included in italics.

NIS	Native	Overlap (SEAc)	% Overlap (SEAc)	Overlap (SEAB)	% Overlap (SEAB)	95% CI
Ameiurus melas	Anguilla anguilla	<0.01	<1%	<0.01	<1%	<1%	<1%
	Cyprinus carpio	<0.01	<1%	<0.01	<1%	<1%	<1%
	Esox cisalpinus	<0.01	2.73	<0.01	2.32	1.54	3.03
	Scardinius erythrophthalmus	<0.01	<1%	<0.01	<1%	<1%	<1%
	Squalius squalus	<0.01	<1%	<0.01	<1%	<1%	<1%
Atherina boyeri	Anguilla anguilla	0.53	9.24	0.89	10.44	8.09	12.81
	Cyprinus carpio	<0.01	<1%	<0.01	<1%	<1%	<1%
	Esox cisalpinus	<0.01	<1%	<0.01	<1%	<1%	<1%
	Scardinius erythrophthalmus	<0.01	<1%	<0.01	<1%	<1%	<1%
	Squalius squalus	0.34	13.28	0.29	12.59	7.82	14.52
Carassius auratus	Anguilla anguilla	1.4	24.79	1.67	23.7	21.27	26.23
	Cyprinus carpio	0.04	1.69	0.05	2.21	1.06	3.51
	Esox cisalpinus	<0.01	<1%	<0.01	<1%	<1%	<1%
	Scardinius erythrophthalmus	0.65	29.02	0.63	25.1	22	32.17
	Squalius squalus	0.62	20.32	0.75	18.46	17.66	22.54
	Tinca tinca	0.06	<1%	0.08	<1%	<1%	1.31
Micropterus salmoides	Anguilla anguilla	<0.01	<1%	<0.01	<1%	<1%	<1%
	Cyprinus carpio	<0.01	<1%	<0.01	<1%	<1%	<1%
	Esox cisalpinus	<0.01	<1%	<0.01	<1%	<1%	<1%
	Scardinius erythrophthalmus	<0.01	<1%	<0.01	<1%	<1%	<1%
	Squalius squalus	<0.01	<1%	<0.01	<1%	<1%	<1%
Perca fluviatilis	Anguilla anguilla	<0.01	<1%	<0.01	<1%	<1%	<1%
	Cyprinus carpio	<0.01	<1%	<0.01	<1%	<1%	<1%
	Esox cisalpinus	<0.01	<1%	<0.01	<1%	<1%	<1%
	Scardinius erythrophthalmus	<0.01	<1%	<0.01	<1%	<1%	<1%
	Squalius squalus	<0.01	<1%	<0.01	<1%	<1%	<1%
	Tinca tinca	<0.01	<1%	<0.01	<1%	<1%	<1%

in Appendix D for modal SEA_B values and the respective 95% confidence intervals), yet they were always below the 60% threshold. The mean of nonzero SEA_c and SEA_B % overlaps was 3.8% and 3.6%, respectively, with values ranging between a minimum approximating 0% for M. salmoides vs. E. cisalpinus and a maximum of 25.1 (SEA_B)–29% (SEA_c) for C. auratus vs. S. erythrophthalmus. Similar to what was observed for invertebrates, the mean % overlap among native species was higher than that determined between NIS and native taxa, i.e., 7.5% and 6.2% (SEA_c and SEA_B % overlaps, respectively), with values ranging between a minimum approximating 0% for E. cisalpinus vs. S. erythrophthalmus, S. squalus, and A. anguilla and a maximum of 18.1 (SEA_B)–22.9% (SEA_c) for A. anguilla vs. S. squalus (Figure 6;

Table A8. Interspecific overlaps in SEA_c and modal SEA_B values of native fish taxa. For the sake of succinctness, values lower than 0.01‰² are reported as “<0.01”. Percent overlaps are reported for both metrics; those lower than 1% are reported as “<1%”. For SEA_B modal values, 95% confidence intervals are included in italics.

Native	Native	Overlap (SEAc)	% Overlap (SEAc)	Overlap (SEAB)	% Overlap (SEAB)	95% CI
Anguilla anguilla	Cyprinus carpio	0.29	5.89	0.31	5.05	3.56	6.36
	Esox cisalpinus	<0.01	<1%	<0.01	<1%	<1%	<1%
	Scardinius erythrophthalmus	0.77	15.54	0.69	10.71	8.02	16.25
	Squalius squalus	1.21	22.88	1.28	18.14	16.07	23.24
	Tinca tinca	1.04	11.85	0.97	11.33	8.12	12.38
Scardinius erythrophthalmus	Esox lucius	<0.01	<1%	<0.01	<1%	<1%	<1%
	Cyprinus carpio	0.02	1.72	<0.01	1.6	1.25	1.93
Squalius squalus	Esox lucius	<0.01	<1%	<0.01	<1%	<1%	<1%
	Cyprinus carpio	0.15	8.66	0.08	7.21	5.53	9.43
	Scardinius erythrophthalmus	0.31	15.12	0.37	12.62	11.72	14.89
Tinca tinca	Scardinius erythrophthalmus	0.04	<1%	0.07	1.05	<1%	1.16

in Appendix D). Noticeably, the mean of nonzero SEA_c and SEA_B % overlaps among NIS was 2.9% and 3.7%, respectively, with values ranging between a minimum approximating 0% for A. melas vs. C. auratus and A. boyeri and a maximum of 13.1 (SEA_c)–18.8% (SEA_B) for C. auratus vs. A. boyeri (Figure 6;

Table A9. Interspecific overlaps in SEA_c and modal SEA_B values of non-indigenous fish taxa. For the sake of succinctness, values lower than 0.01‰² are reported as “<0.01”. Percent overlaps are reported for both metrics; those lower than 1% are reported as “<1%”. For SEA_B modal values, 95% confidence intervals are included in italics.

NIS	NIS	Overlap (SEAc)	% Overlap (SEAc)	Overlap (SEAB)	% Overlap (SEAB)	95% CI
Atherina boyeri	Ameiurus melas	<0.01	<1%	<0.01	<1%	<1%	<1%
Carassius auratus	Ameiurus melas	<0.01	<1%	<0.01	<1%	<1%	<1%
	Atherina boyeri	0.39	13.1	0.61	18.77	12.02	20.58
Micropterus salmoides	Ameiurus melas	<0.01	<1%	<0.01	<1%	<1%	<1%
	Atherina boyeri	<0.01	<1%	<0.01	<1%	<1%	<1%
	Carassius auratus	<0.01	<1%	<0.01	<1%	<1%	<1%
Perca fluviatilis	Ameiurus melas	0.13	5.56	0.27	7.59	4.54	7.66
	Micropterus salmoides	0.29	10.26	0.34	10.69	8.09	12.33
	Atherina boyeri	<0.01	<1%	<0.01	<1%	<1%	<1%
	Carassius auratus	<0.01	<1%	<0.01	<1%	<1%	<1%

in Appendix D).

4. Discussion

Of the two contrasting hypotheses originally formulated in this study, only the second received support from the data, as the results indicated that a low potential trophic overlap occurs between non-indigenous and native consumers in the winter food web of Lake Trasimeno. The average percent overlap, measured using either conventional sample-size-corrected standard ellipse areas (SEAc) or Bayesian standard ellipse areas (SEA_B), was below 4% for both the invertebrate and the fish assemblage. Additionally, pairwise % overlaps estimated between NIS and native species were below 16% for invertebrates and 30% for fish, far from the 60% critical threshold generally acknowledged to be related to active competitive interactions, e.g., [68,69]. The highest overlaps were observed among invertebrates for the Louisiana crayfish P. clarkii and to a minor extent for the killer shrimp D. villosus, while the goldfish C. auratus was characterized by the highest and most diffuse overlaps with native fish species. These findings have general theoretical implications but deserve to be discussed while focusing also on a species-specific perspective.

4.1. General Considerations

The low overlap indices observed between NIS and native consumers indicates that low potential competition occurs and that a stable coexistence equilibrium takes place in both the invertebrate and fish assemblages. In addition, it suggests that NIS play important functional roles in the flux of energy and matter from basal to higher trophic levels and have become pivotal in supporting the whole food web of Lake Trasimeno.

Mutual coevolution shapes competitors’ niches in natural communities [70]; accordingly, coexisting species should exhibit relatively low overlap in resource utilization; alternatively, if competition for limited resources is ongoing, a high niche overlap should occur [70,71,72]. In the context of bioinvasions, this latter scenario generally characterizes non-indigenous populations in their post-introduction and early-establishment phases, generally coupled with anomalously high abundances, e.g., [73]. The duration of coexistence with native species in the recipient food web is considered a key factor driving relevant ecological and evolutionary processes [74,75], as short-term coexistence between NIS and native species with a similar trophic ecology may induce high niche overlaps [76,77]. In contrast, long-term coexistence (>10 years) has been shown to be paralleled by shifts in diet and habitat segregations with important consequences for competitors’ trophic interactions [78,79,80,81]. Here, no significant relationships were observed in, e.g., the time since the introduction of NIS in Lake Trasimeno and their mean overlaps with native species (Pearson r = −0.21, p = 0.59, d.f. = 8). Indeed, for invertebrates as well as for fish, the observed low overlaps can be partially explained by differences in trophic habits; however, even focusing on species belonging to the same trophic guild, such as filter-feeding bivalves (D. polymorpha vs. A. anatina), detritivorous amphipods and isopods (D. villosus vs. E. veneris and A. aquaticus), or predatory fish (M. salmoides vs. E. cisalpinus), negligible or very limited overlaps have been observed, with larger overlaps determined within native- or NIS-only assemblages. The relatively long invasion history experienced by the Lake Trasimeno community can be hypothesized as the main determinant of the limited isotopic overlaps observed here. Among invertebrates, D. villosus can be considered an exception, as it appeared in 2017, whereas the remaining species were introduced around 2000 or earlier (Table 1); among fish, the most recent introductions were C. auratus and M. salmoides in 1990. Thus, it is plausible that the low overlap observed in the isotopic space may result from the peculiar conditions of relatively low abundance and metabolic requirements of both native and non-indigenous consumers taking place in Lake Trasimeno during the cold season as well as from long-term phenomena of adaptation and partitioning of the available resources in order to reduce competition and promote coexistence. Other factors related with, e.g., life history and geographic origin of NIS, cannot be excluded, as they have been indicated to play a role in freshwater communities characterized by multiple invasions [82].

Interestingly, the low overlap between NIS and native consumers suggests a high diversification in the contribution of both invertebrate and fish species to the channelling of matter and energy from basal resources to higher trophic levels. In other words, NIS appear to have acquired in the years after their introduction and establishement a structural as well as a functional role in the food web of Lake Trasimeno. For island ecosystems, the eradication of invasive species has been indicated to exert unquestionable benefits to the extant native biota, but empirical observations have also shown that these benefits can vary widely and unpredictably, and that adverse consequences may take place due to the disruption of the novel functional relationships generated by the invaders’ “surprise effects” in [83,84,85,86]. Thus, for Lake Trasimeno, this may have important implications from a management perspective: with the exclusion of P. clarkii and C. auratus, both showing low but diffuse overlaps with native species, any mitigation strategy based, e.g., on the reduction in the abundance of a NIS should also take into consideration a variation in the functioning of the food web.

4.2. Species-Specific Issues

Procambarus clarkii was shown to have the largest nichecluding among the invertebrate species included in this study, confirming the results of other isotopic investigations performed in both lentic and lotic environments [82,87]. Current information on the trophic ecology of this omnivorous species mostly pertains to food selection and dietary overlap with other crayfish species [88,89,90,91]; only recently, Wu and colleagues [92] verified in a Chinese reservoir a substantial resource overlap between P. clarkii and native crustaceans and gastropods, indicating the potential for the crayfish to exert negative impacts through competition. Here, P. clarkii overlapped with a number of native species, including the amphipod E. veneris and the gastropod P. acuta. Further comparative studies on the trophic niche of the crayfish are needed, specifically addressing potential competitive interactions with representatives of the detritivorus guild, native as well non-indigenous; here, P. clarkii showed a relatively high overlap also with the killer shrimp D. villosus. Indeed, while investigations based on conventional gut content analysis suggest similarity in dietary habits [93,94], the results of the only isotopic study including these two species, does not lend support to this view [82]; thus, to date, the nature and strength of the interaction between P. clarkii and D. villosus remain virtually unexplored.

Among fish taxa, the pumpkinseed Lepomis gibbosus was characterized by a large niche, yet no overlaps occurred with other fish species, either native or non-indigenous. The species was characterized by δ¹³C values far more enriched than those characterizing other fish species (Figure 2) yet are fully consistent with a group of potential invertebrate prey including D. villosus, P. antennarius, and the dragonfly nymphs Erithromma sp. and Ischnura sp. L. gibbosus is known to have paleomonids, Odonata larval stages, and D. villosus as common items in its diet, yet it is also recognized as an active predator of the zebra mussel D. polymorpha [95,96,97,98,99]. Here, isotopic values and niche position suggest that the invasive bivalve does not contribute significantly to the diet of L. gibbosus, at least in winter. It is worth noting that the specimens of L. gibbosus analyzed in this study had a relatively small size, with a standard length ranging between 45 and 95 mm (Appendix A, Table A1). Mollusks become a significant component of the diet of the pumpkinseed only for individuals larger than 80–90 mm, e.g., [99]; thus, it is plausible that the pattern observed here might testify to a size-related dietary shift associated with a number of additional factors linked to, e.g., ontogeny or prey availability.

Carassius auratus showed a relatively high and diffuse overlap with a number of native species, such as S. erythrophthalmus and S. squalus, and to a lower extent with A. anguilla, all known to feed mainly on benthic invertebrates [100,101,102]. C. auratus has zooplanktivorous habits yet is able to shift to a benthivorous diet depending on resource availability [103,104,105]. In Lake Trasimeno, given the low abundance of zooplankton in winter months [29,106], it is likely that C. auratus modified its trophic habits, converging towards those characterizing native benthivorous species. A similar trophic shift may have occurred also for Atherina boyeri, showing a diffuse overlap with S. squalus, S. erythrophthalmus, C. auratus, and other benthivorous predators such as C. carpio and T. tinca [107,108]. Freshwater populations of A. boyeri are known to feed mainly on zooplankton, yet depending on size, prey availability, and local conditions, an important component of their diet in freshwater and transitional environments may be represented by benthic invertebrates such as amphipods and chironomids [109,110] see also [111,112] for confirmative examples from transitional environments.

Noticeably, E. cisalpinus, the only native piscivorous predator occurring in Lake Trasimeno, showed a negligible overlap with other introduced predators such as P. fluviatilis and M. salmoides, both showing significantly higher δ¹⁵N values than E. cisalpinus. In contrast, a relatively high overlap was observed between E. cisalpinus and A. melas. In winter months, the benthivorous A. melas may shift to piscivory, e.g., [113], while Crustacea may become a significant component of the diet of pikes, in particular for small-sized specimens [114,115,116]. Thus, given the relatively small size of E. cisalpinus individuals analyzed in the present study (222–412 mm standard length range; Appendix A, Table A1), it can be hypothesized that its diet converged towards that of A. melas, resulting in the observed high overlap.

5. Conclusions

The present study was carried out in winter, and additional analyses may provide a more advanced resolution of species interactions as affected by seasonal variation in, e.g., abundance and trophic habits. In addition, the location where invertebrate and fish consumers were sampled can be considered representative of the littoral benthic environments of the southern sectors of Lake Trasimeno [45]. However, given the 53 km long coastline of the basin [43], future analyses should include multiple locations to account for, e.g., local variations in the availability of basal resources such as primary producers [117,118] and how these influence the isotopic niches of consumers. Nonetheless, this investigation provided a first assessment of the potential for competition between non-indigenous and native invertebrates and fish currently occurring in Lake Trasimeno, indicating that isotopic approaches may represent a powerful tool for disentangling the complexity of the trophic interactions characterizing the food web of the lake, providing at the same time useful information for future actions of management and mitigation of the impact of non-indigenous species.