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Article

Gastropod Assemblages Associated with Habitat Heterogeneity and Hydrological Shifts in Two Shallow Waterbodies

by
Jasna Lajtner
1,*,
Anna Kozak
2,
Maria Špoljar
1,
Natalia Kuczyńska-Kippen
2,
Tvrtko Dražina
1,
Mirela Sertić Perić
1,
Ines Tkalčec
1,
Sanja Gottstein
1 and
Ivana Zrinščak
1
1
Department of Biology, Faculty of Science, University of Zagreb, Rooseveltov trg 6, 10000 Zagreb, Croatia
2
Mickiewicz University, Uniwersytetu Poznańskiego 6, 61‐614 Poznan, Poland
*
Author to whom correspondence should be addressed.
Water 2022, 14(15), 2290; https://doi.org/10.3390/w14152290
Submission received: 27 June 2022 / Revised: 20 July 2022 / Accepted: 21 July 2022 / Published: 22 July 2022
(This article belongs to the Special Issue Functioning of Small Water Bodies)
Browse Figures
Versions Notes

Abstract

:
We aimed to determine the effects of water level and habitat heterogeneity on gastropod fauna in the littoral zone, and the differentiation of functional feeding guilds (FFG) of gastropods. Two periods were analyzed: 2012 (low water level, LWL) and 2013 (high water level, HWL) in the littoral zone of two shallow waterbodies (Sutla backwater, NW Croatia). Waterbody S1, covered with Ceratophyllum demersum, was sampled in the macrophyte stands, and the littoral benthal area, while waterbody S2, without macrophytes, was sampled only in the littoral benthal area. It was observed discovered that among the macrophyte stands in S1, gastropods were significantly more abundant during LWL. The same trend was observed in the littoral benthal area of S2. In contrast, gastropod abundance was higher in the littoral benthal area of S1 during HWL. Comparing gastropods in the two waterbodies, the abundance in S1 was ten times higher than in S2. The most abundant species was Gyraulus parvus, which accounted for 51–92% of the gastropods observed among the macrophytes of S1 and 86% in the adjacent benthic zone. Among the FFG groups, grazers (particularly those feeding on gymnamoebae and rotifers) had the largest proportion, followed by shredders feeding on small pieces of macrophytes. In our research, we indicate the important role of microhabitat diversity and submerged macrophytes as a rich food source for gastropods and safe shelter from predators.

1. Introduction

Shallow water bodies (SWB) are unique freshwater ecosystems that have long been neglected in limnological research, despite their great contribution to overall biodiversity, including phyto- and zooplankton, macrophytes, benthos, nekton, amphibians, and waterbirds [1,2,3,4]. These ecosystems, regardless of their poor morphological features, are particularly vulnerable to global climate changes, including hydrological regimes that cause frequent and significant fluctuations in water levels [2,5,6,7], which is one of the most important aspects of limnology research in our time. The fluctuations in water level and occasional lack of water may alter several environmental conditions such as light availability, but they can also affect the occurrence and distribution of aquatic organisms, including submerged macrophytes [8,9,10] or various animals [11]. The littoral zone of the SWB is of critical ecological importance for aquatic food webs, being the main site for secondary production [12], enhancing habitat complexity and thus providing high diversity and abundance of invertebrates that support specific ecosystem functions, e.g., nutrient retention and water cycling [13,14]. The littoral zone is subjected to frequent and extreme water level fluctuations that often result in changes in the functioning of shallow ecosystems, such as modifications in water transparency [15,16,17], macrophyte cover [7], nutrient levels [7], and food resources [18,19]. All these shifts will influence habitat function, nutrition quality and availability, reproduction, and general life cycle conditions for littoral communities [5,7,20].
Among the macroinvertebrates inhabiting the benthal area of SWB, there are more records of the occurrence of insect larvae [7,21,22,23] and crustaceans [2,24,25] than of gastropod mollusks, although they play a significant role in the macroinvertebrate community in the SWB [26] and are a particularly important element in the production and transformation of detritus [27]. When sufficient calcium ions are available, gastropod assemblages in lakes are regulated primarily by fish and crayfish predation; assemblages in shallow, fishless ponds are mainly regulated by competition, whereas gastropod assemblages in temporary ponds are largely influenced by the frequency and extent of desiccation [28,29].
In littoral food webs, gastropods may primarily affect epiphyton (detritus, bacteria, algae, fungi, protozoa, and metazoans), while rarely consuming live macrophytes [30,31,32,33,34]. Accordingly, the distribution of macrophytes in the littoral zone is critical for both gastropods and ecosystem functioning, and the role of gastropods is multifaceted. Submerged macrophytes with complex architecture provide a greater surface area for epiphyton, which leads to greater food source [35,36,37,38] and habitat availability, in addition to increased protection from visual predators and diversification of suitable sites for oviposition [39]. Conversely, several studies have confirmed that gastropods can promote macrophyte growth by grazing light-limiting vegetation, which indirectly leads to changes in nutrient regeneration [26,40,41]. All of this may also be reflected in total biomass, abundance, and richness of macroinvertebrates, which are significantly higher in submerged vegetation than in emergent and floating vegetation e.g., [5,37]. Habitat type is often stated as a factor that influences species distribution of gastropods, besides e.g., substrate composition, meteorological and physiographical factors, environmental tolerance, or anthropogenic disturbance [42,43].
Compared to lakes with low water level fluctuations, lakes with high water level fluctuations may have the following characteristics: (i) significantly coarser-grained littoral substrates with lower macrophyte cover, and (ii) greater proportions of omnivorous benthic invertebrates in the littoral zone, in addition to (iii) a generally altered taxonomic and trophic structure of benthic consumers and a more homogeneous benthic invertebrate assemblage [16]. Gastropod response to hydrologic stress (i.e., water level fluctuations) and their trophic interactions are poorly studied in SWB. Lakes with low water level fluctuations have been proven to host greater numbers of pulmonate (non-operculate) gastropod taxa, while lakes with high water level fluctuations have few gastropods [16]. In intermediate or deep habitats, gastropods are mostly represented by prosobranchs (operculate taxa) (e.g., Bithynia tentaculata, Viviparus viviparus), which are more resistant to desiccation and drought [16,44].
In this study, we analyzed gastropod assemblages and their role in food webs in two SWB (S1 with submerged macrophytes and S2 without macrophytes) during summer in two consecutive years (2012, 2013) that differed in hydrological regime. According to Špoljar et al. [7], lower precipitation and lower water levels (LWL) were recorded in 2012, while higher water levels (HWL) were measured in both SWB in 2013. The primary objectives of this study were to assess gastropod assemblages during periods of LWL and HWL, considering: (i) habitat heterogeneity of the littoral zone, (ii) epiphyton as a food source, and (iii) fish as predators. The results of this study will help highlight gastropods as an important link in trophic interactions and as indicators of water quality in SWB. They will also provide a basis for using gastropods as indicator organisms responding to potential changes in SWB functioning due to water level fluctuations.

2. Materials and Methods

2.1. Study Area

This study was conducted in NW Croatia (about 30 km from Zagreb) in the littoral zone of the Sutla River backwater. The Sutla backwater is a natural water body connected to the Sutla River and divided into two barely connected basins: (a) the upper basin (S1) covered by submerged macrophytes dominated by Ceratophyllum demersum, and (b) the lower basin (S2) without macrophyte stands (Figure 1). These basins differed in their morphometry, water transparency, and macrophyte cover. The study area has been described in detail in previous studies [2,7].

2.2. Macroinvertebrates and Epiphyton Sampling and Biocoenotical Analyses

Samples were collected monthly, from July to September (in Roman numerals: July VII, August VIII, September IX), in 2012 and 2013. Triplicate samples of macroinvertebrates (i.e., macrozoobenthos) were collected at each water body (S1 and S2) in the littoral zone. We used the following sampling protocol: first, we measured environmental parameters in the field and collected samples for analysis of water physicochemical parameters; second, we collected macroinvertebrates from among macrophytes in S1 and from the littoral benthal area of both waterbodies S1 and S2; and third, we collected fish by electrofishing.
In both waterbodies, littoral benthos (i.e., littoral benthic macroinvertebrates), including gastropods, were sampled using a Surber sampler (25 × 25 cm frame; 300 μm mesh size) and preserved in 75% ethanol. In S1, macroinvertebrates were additionally sampled within macrophytes and macrophyte epiphyton. Sampling was performed by cutting the submerged portion of the macrophytes at a length of 10 to 15 cm (2 stems in triplicate for macroinvertebrates, and the same sampling protocol for epiphyton). Macrophytes were placed in a plastic bag filled with ambient water and transported to the laboratory in a cooler. Gastropods and macroinvertebrates were isolated from stems manually or under a stereomicroscope, and all animals were preserved in 75% ethanol. For epiphyton collection, stems were scraped with a small brush, and biocenotic microscopic analyses were performed on the live material several hours after sampling. The stems of C. demersum were dried (to constant mass) at 104 °C for 24 h. Abundance of gastropods among macrophytes and epiphyton (i.e., zooperiphyton: Gymnamoeba, Testacea, Ciliophora, Rotifera) was expressed as the number of individuals per 1 g of dried mass of Ceratophyllum (Ind. g−1 DM), while abundance of gastropods, and macroinvertebrates in littoral benthos was expressed as the number of individuals per square metre (Ind. m−2).
All macroinvertebrate samples were analyzed under an Olympus SZ61 stereomicroscope (Hamburg, Germany; 10× to 40× magnification). Epiphyton samples were divided into groups according to the higher taxonomic levels (Gymnamoeba, Testacea, Ciliophora, Rotifera) and counted using the Opton-Axiovert 35 microscope (Carl Zeiss Jena, 100× to 400×). Gastropods were identified to species level based on Glöer [45] and classified into functional feeding groups (FFG) based on their feeding preferences as shredders (SHR), grazers (GRA), passive filterers (PFIL), detritivores (DET), and others (OTH) according to Moog [46].

2.3. Environmental Parameters

The analyses of environmental parameters for both years 2012 and 2013 have already been described in detail in previous studies [2,7]. During the summer period in each year, environmental data did not indicate a significant difference between two SWB, S1 and S2 (Mann-Whitney, p > 0.05), thus we indicated those values as average for both SWB during the summer season at LWL and HWL, respectively. Physicochemical water parameters [water temperature (Temp), dissolved oxygen concentration (DO) and pH] were measured with a portable pH and dissolved oxygen meter (Hach HQ30d, Loveland, CO, USA); electrical conductivity (EC) with a portable conductivity meter (Hach sensION 5, Loveland, CO, USA); pelagic water transparency (Trans) with a Secchi disc (zSD) to determine the environmental characteristics of the SWB. Macrophyte cover was expressed as a percentage (MC, %). An additional 1-litre water sample was collected at each site (and stored at 4 °C) for laboratory analysis of chemical parameters and food sources (algae, detritus). Total nitrogen (TN) and total phosphorus (TP) were determined according to APHA [47] and dissolved organic matter (DOM) was determined by estimating chemical oxygen demand, COD(Mn) [48]. Phytoplankton (based on chlorophyll a) and particulate organic matter (based on POM) concentrations were considered as possible food sources for the littoral community. Chlorophyll a (Chl a) concentration (a proxy for phytoplankton biomass) was analyzed using an ethanol extraction method [49] in plankton (µg L−1) and in epiphyton (µg g−1 DM). POM was evaluated as ash-free dry mass (AFDM), calculated as the difference between the mass of the water sample after drying at 104 °C (to constant mass) and its mass after ashing at 600 °C/6 h.

2.4. Data Analysis

The parameters analyzed were not normally distributed and could not be normalized by common transformations [50], so we used non-parametric tests. The Mann–Whitney U test was applied to test differences in environmental variables between years (2012 vs. 2013), and the Kruskal–Wallis test and accompanying post-hoc multiple comparisons were used to test differences in gastropod abundance among years and habitats.
Multivariate similarity analysis (ANOSIM) was used to identify differences or similarities in water depth and other environmental variables between the two years studied, while SIMPER analysis was used to calculate the contribution of each gastropod species (%) to dissimilarity between LWL (2012) and HWL (2013) years [7]. Interactions between selected environmental parameters and food resources LL—leaf litter; ML—macrophyte litter; macrophyte coverage—MC; fish length—Fish; particulate organic matter in benthos—POMb; macrozoobenthos excluding gastropods—MZB; chlorophyll a concentration in epiphyton—Echl; epiphyton abundance of Gymnamoeba—EGam, Testacea—ETest, Ciliophora—ECili, Rotifera—ERot; abundances of the gastropod species (Fc—Ferrissia californica; Hc—Hippeutis complanatus; Gc—Gyraulus crista; Gp—Gyraulus parvus; Gt—Galba truncatula; Pa—Physella acuta; Ra—Radix auricularia; Vp—Valvata piscinalis) and gastropod functional feeding groups (FFG) at each study site (S1 and S2) were analyzed by canonical correspondence analysis (CCA) or redundancy analysis (RDA) using the Canoco 4.5 program [51]. The statistical significance of the analyzed correlations was tested using the Monte Carlo permutation test (499 permutations). For all statistical tests, a p-value of 0.05 was used as an indicator of statistical significance.

3. Results

3.1. Environmental Variables

For summer environmental conditions, when the research took place, the preceding winter and spring hydrometeorological conditions were crucial. There was a total of 219 mm more precipitation in the second year of examination [2013 (total 1201 mm)] than in the first year [2012 (total 982 mm)]. The average water depth in summer 2013 was up to 0.4 m higher than in 2012 (Mann–Whitney U test, p < 0.05). Macrophyte cover in S1 was significantly (20%) higher in 2012 compared to 2013 (Mann–Whitney U test, Z = 2.09 p < 0.05). Due to the observed decrease in macrophyte cover, POM and Chl a, and the increase in TP, environmental conditions differed significantly between LWL and HWL (ANOSIM, r = 0.872, p < 0.002) during the summer periods in SWB, S1, and S2 (Table 1). The NMDS analysis also clearly separated LWL from HWL, based on the measured environmental variables (Figure 2).
At an increased water level, chlorophyll a in epiphyton over macrophyte in S1 was significantly reduced to 5.964 ± 3.425 µg Chl a g−1 DM in comparison to its value at LWL, 52.125 ± 33.177 µg Chl a g−1 DM (Mann–Whitney U test, Z = 3.09 p < 0.05).

3.2. Gastropod Assemblage

During the research, a total of eight gastropod species were recorded—pulmonate Ferrissia californica (Rowell, 1863), Galba truncatula (O. F. Müller, 1774), Gyraulus crista (Linnaeus, 1758), G. parvus (Say, 1817), Hippeutis complanatus (Linnaeus, 1758), Physella acuta (Draparnaud, 1805), Radix auricularia (Linnaeus, 1758), and prosobranch Valvata piscinalis (O. F. Müller, 1774). Three of them, F. californica, G. parvus, and P. acuta, are alien invasive species. The most common is the family Planorbidae (F. californica, G. crista, G. parvus and H. complanatus), followed by Lymnaeidae (G. truncatula and R. auricularia), while Physidae (P. acuta) and Valvatidae (V. piscinalis) are families represented by only one species.
At waterbody S1, a total of six species of freshwater gastropods were detected within macrophytes: F. californica, G. crista, G. parvus, H. complanatus, P. acuta, and R. auricularia (Figure 3). Total abundance was significantly higher (Kruskal–Wallis test, H = 9.48, p < 0.03) in the LWL period, which was directly related to the abundance of G. parvus, 9 ± 12 Ind. g−1 DW in LWL and 4 ± 3 Ind. g−1 DW in HWL, respectively. The species H. complanatus had the lowest abundance in both periods. Abundances of F. californica and R. auricularia were similar during both hydrological periods. Abundance of G. crista and P. acuta was low, but higher during the HWL period, but these differences were not statistically significant (Mann–Whitney U test, p > 0.05).
Seven gastropod species were discovered in the littoral benthal area of S1 (Figure 4a). In addition to the species already mentioned within macrophytes, G. truncatula and V. piscinalis were also discovered in the benthal area of S1. A significantly higher abundance of gastropods was discovered during the HWL period (LWL up to 150 Ind. m−2, HWL up to 600 Ind. m−2, Figure 4a). The Kruskal–Wallis test (H = 3.86, p < 0.05) indicated that gastropod abundance differed between the two years studied with different hydrological regimes, with gastropods being more abundant in the macrophyte-covered littoral during HWL. In both periods (LWL and HWL), the abundance of G. parvus was the highest (61 ± 54 and 483 ± 325 Ind. m−2, respectively). Abundances of F. californica and G. crista were equal (ca. 45 Ind. m−2 and 3 Ind. m−2, respectively), R. auricularia was most abundant in the LWL period, and P. acuta in the HWL period.
In waterbody S2, a total of seven gastropod species were discovered in the littoral benthal area (Figure 4b). While V. piscinalis was not detected in S1, F. californica was not detected in S2. The highest numbers of all species were recorded during the LWL period, with V. piscinalis and H. complanatus having the highest abundance. The exception was P. acuta, which was equally abundant during both periods. Gastropod abundance did not differ significantly (Kruskal–Wallis test, H = 1.34, p > 0.05), between LWL and HWL. The gastropod abundance in the littoral benthal area was significantly lower in S2 than in S1 (Kruskal–Wallis test, H = 3.65, p < 0.05).
The difference in total gastropod abundance was statistically significant (Kruskal–Wallis test, H = 7.67, p < 0.05) when we compared LWL and HWL; this was primarily due to the high abundance of G. parvus during HWL (Kruskal–Wallis test, H = 10.73, p < 0.02). The SIMPER analysis was used to identify the littoral benthic taxa that were responsible for the greatest differences between the LWL and the HWL period (Table 2). It was discovered that the species G. parvus was a primary contributor to assemblage structure in both periods. Together with the aforementioned species, R. auricularia and F. californica played a significant role in structuring the assemblages during LWL, while P. acuta and H. complanatus were characteristic representatives during the HWL period. The SIMPER test indicated that the assemblages of LWL and HWL were quite dissimilar (average dissimilarity = 78.50). Table 2 indicates that the HWL assemblages were better defined and had higher internal similarity (average similarity = 22.23) than the LWL (average similarity = 10.84).

3.3. Gastropod Functional Feeding Groups

When analyzing the composition of FFG in macrophyte stands of S1, grazers dominated in both time periods, followed by shredders (Figure 5). Abundance values for all groups were higher in the LWL period, except for detritivores, whose values were very low in both periods.
In the littoral benthal area of S1 (Figure 6a) grazers also dominated in both periods, but in contrast to the macrophyte stands, the number of all groups was significantly higher in the HWL season, and there were no detritivores.
At site S2 (Figure 6b), a significantly higher abundance of all FFG was recorded during the LWL period. Grazing gastropods dominated in both periods, but the numbers of shredders, detritivores, and others were equal.
An analysis of relationships among sampling sites, physicochemical variables, and gastropod abundance was also performed. In the macrophyte stands of S1 (Figure 7), the first two axes of the RDA analysis explained 98% of the variance in gastropod interactions (Axis 1: 56%, Axis 2: 42%). The RDA results indicated that the most important food sources for gastropods were Rotifera (ERot: F = 12.28, p = 0.038), and Gymnamoebae (EGam: F = 31.68, p = 0.032). According to the CCA results for the littoral benthal area, the first two axes explained 78% of the variance (Axis 1: 52%, Axis 2: 26%, Figure 8). Waterbodies differed as demonstrated in Figure 8, indicating that the gastropod community in the littoral benthal area of S1 was significantly influenced by macrophyte litter (ML: F = 2.42, p = 0.012), while gastropods in the littoral benthal area of S2 were primarily influenced by leaf litter (LL: F = 1.00, p = 0.0422). RDA analysis of gastropod FFG composition (Figure 9) indicates that macrophyte cover (MC) increased the number of gastropod shredders and grazers, while particulate organic matter in the benthos (POMb) was significantly positively correlated with the number of gastropod detritivores. In S1, small fish dominated and coexisted with gastropods, while the presence of larger fish in S2 negatively affected the gastropod abundance and, consequently, FFG composition.

4. Discussion

Environmental conditions in ponds and other small waterbodies are far less stable than in lakes and can be profoundly altered by comparatively minor pressures or small changes in the environment [16,20,52,53]. The fluctuations of the water level may greatly affect the functioning of the water body and therefore have an impact on the whole food web. In our study conducted on a Sutla backwater, NW Croatia, it was ascertained that the rise in water level in 2013, caused primarily by high precipitation in the autumn of 2012 and winter of 2013 [2,7], had a strong impact on overall environmental conditions, particularly a 20% reduction in macrophyte cover in one (S1) of the two examined waterbodies.
The results of our study clearly suggest that extreme weather events not only determine environmental conditions, but also gastropod assemblage in small water bodies, which are closely associated with macrophytes and sediments due to their manner of feeding and habitat requirements. During the HWL period, a decrease in diversity and abundance was observed in the littoral benthal area of macrophyte-free waterbody S2 and within the macrophyte stands of macrophyte-covered waterbody S1. In contrast, gastropod abundance increased in the second site of the macrophyte-covered waterbody S1—in the littoral benthal area. These results are consistent with previous studies reporting that gastropods in lakes with large water level fluctuations are subjected not only to direct physical disturbance, but also to significant trophic stress due to reductions in macrophyte biomass and diversity, which create a favorable food base for gastropods [52,54].
All the species identified in our study are typical for shallow waters and the littoral zone of lakes, in addition to floodplains and wetlands with high trophy levels [45], which confirms both the trophic state and the shallow character of the Sutla waterbodies [2,7]. We demonstrated that during the study, pulmonate gastropods dominated, particularly G. parvus, while only V. piscinalis was observed among prosobranch gastropods. A similar composition was detected by Jezidžić [55], who conducted malacological surveys in the Kopački Rit area at sites with well-developed aquatic vegetation. This author reports that pulmonate gastropods from the family Lymnaeidae are the most represented in the number of species and their abundance, and the highest abundance was observed on submerged vegetation (C. demersum), as opposed to emergent and floating plant beds. Lodge et al. [28] note that prosobranchs are absent from ponds and smaller lakes that dry out in summer, or lakes with poor oxygen conditions. Prosobranchs were also absent in small ponds during the water-filled period [56]. It is possible that prosobranchs are outcompeted by pulmonates in water bodies where fish predation levels are low or fish predators are absent. Indeed, when predators are abundant in the environment, prosobranchs with thick shells survive, whereas pulmonates with thin shells do not [28].
The significantly higher abundance of gastropods in S1 compared to S2 SWB during the two hydrological periods can be explained by the greater heterogeneity of habitats in S1 caused by the cover of the complex macrophyte C. demersum. This suggests that gastropods use the macrophytes as a safe shelter from potential predators, particularly fish, and that the cover of macrophytes is an important food source for gastropods in addition to other micro- and macroinvertebrates [2,7]. Namely, the leaves of C. demersum form bowl-shaped whorls that are close together, particularly near the top of the stem. This may provide additional protection and a stable attachment surface particularly for gastropods being the largest organisms of the epiphytic fauna [57].
Considering the Ceratophyllum stand in S1, the observed decline in gastropod abundance during the HWL was primarily a result of the decline in the abundance of the dominant pulmonate species G. parvus. According to Lorencova et al. [58] this North American planorbid gastropod was reported from Europe (Germany) in the 1970s, but it is possible that this species was introduced to Europe several centuries earlier and described as a species of G. laevis. Recent molecular research has indicated that G. parvus and G. laevis are indeed members of the same species-level clade, with the former taking nomenclatural precedence [58]. Possible routes of dispersal included freshwater ballast in the holds of transcontinental ships [59] or migratory waterfowl [60]. Since then, it has spread to Central and Western Europe, where it mostly lives in artificial and highly modified habitats in shallow standing waters of different sizes with rich vegetation, mostly in reservoirs or artificial water bodies in gardens, with few competing species [58,61]. In our study, it can be assumed that the lower abundance of G. parvus is directly affected by the reduction of macrophytes in the HWL. Additionally, this species likely has a strong preference for macrophyte habitats, as it feeds preferentially by scraping epiphyton and shredding macrophyte tissue and leaves [45,46].
Comparing the gastropod abundance in the littoral benthal area between LWL and HWL, the opposite trends were observed in the studied SWB, namely an increase in S1 and a decrease in S2. After the water level increased in S1, the decrease in macrophyte cover likely resulted in a loss of habitat for the dominant G. parvus specimens, and they chose the adjacent littoral benthos, which was rich in macrophyte detritus, as an alternative habitat. This sediment was also observed to be a suitable habitat for other macroinvertebrates in the same SWB [7]. In contrast, in macrophyte-free S2, the decreasing trend in gastropod abundance and diversity with the water rise could be explained by differences in habitat heterogeneity. During LWL, occasional tree branches and roots, in addition to ecotonal vegetation, were partially submerged and likely allowed gastropods to inhabit such organic epiphyton-covered surfaces. Concurrently, these vegetation fragments, along with leaf litter, contributed to the increase in diversity and abundance in S1 during LWL. Decreasing abundance and diversity in S2 during HWL may be associated with flooding of the ecotone zone and adjacent vegetation (primarily grass) as an important habitat for pulmonate gastropods. Thus, the flooding period reduces the habitat and diversification of the gastropod community. Generally, the remaining muddy substrate during the HWL was an unfavorable environment (e.g., lack of epiphyton) for their life in S2. Consistent with our results, there are records of decreases in the abundance of Chilina ovalis G. B. Sowerby I, 1838 in the muddy sediment of the Queule River Estuary, in the south-central region of Chile [62].
The occurrence of alien species is often regarded as one of the major threats to biodiversity, both on a local and global scale. Therefore, it is important to monitor communities of freshwater organisms to assess their taxonomic affiliation and changes in the abundance of alien species. We observed three alien invasive species: F. californica, P. acuta, and the previously mentioned G. parvus. Two of these species, P. acuta and F. californica, are also native to North America [63,64,65,66,67], similarly to G. parvus. The possible pathway of introduction for these three species into the studied SWB is human activities (e.g., fish stocking), but spread by animals (particularly birds) should not be excluded. The abundance of P. acuta and F. californica suggests that these species have significant influence in structuring the assemblage in the littoral benthos of both SWB, particularly during HWL. The species P. acuta is known to be one of the most effective and spectacular invaders among freshwater gastropods [66], and in our study it indicated an increasing trend of abundance and a higher proportion of the gastropod assemblage during HWL (LWL 12%, HWL 23%) compared to F. californica (LWL 13%, HWL 15%). Like other invaders, both species displayed resistance to stressors. The rising water levels in our study resulted in an increase in their abundance and more uniform species composition. From a biogeographic perspective, molluscan invasions lead to homogenization of faunas, the extinction of sensitive endemic species, and changes in the biotic composition of invaded ecosystems [65,66,67,68,69].
Not only single species will react to changes in the environmental conditions. Very often, a functional group, which is a set of organisms that share similar characteristics within a community, will also reveal a strong response. As mentioned, the analyses of FFG were performed based on their feeding preferences as suggested by Moog [46], according to which one species can be classified into several groups. Species such as G. parvus, G. crista, and H. complanatus are primarily grazers but could be classified as shredders as well; F. californica is a shredder and grazer in the same ratio; P. acuta was primarily a grazer but is also shredder and detritivore; R. auricularia is a shredder and grazer in the same ratio while to a lesser extent detritivore; V. piscinalis is a detritivore [46]. The decrease in the numbers of grazers and shredders among macrophytes in S1 during HWL is directly related to the decrease in the abundance of G. parvus. The same explanation can be applied to the increasing number of grazers and shredders due to HWL in the littoral benthal area in S1. The decreasing numbers of shredders and grazers in S2 in HWL are a consequence of the absence of G. parvus, G. crista and H. complanatus, while the decreasing abundance of R. auricularia and the absence of V. piscinalis result in fewer detritivores. These results were also confirmed by the RDA analysis, which indicated that macrophyte stands increased the number of gastropod shredders and grazers, while particulate organic matter in the benthic area was significantly positively correlated with the number of gastropod detritivores. According to the CCA analysis in the macrophyte stands of S1, the most important food sources for gastropods were Rotifera and Gymnamoebae. It is known that these groups are common and abundant in epiphytic assemblages of freshwaters [7,70]. In contrast, CCA results indicate that macrophyte litter in the littoral benthal area of S1 and leaf litter in the littoral benthal area of S2 significantly influenced the gastropod assemblages.
It is important to emphasize that through analyzing the percentages of FFG, it is evident that the ratios of individual FFG remained exactly the same in the littoral benthal area of both SWB. Minor discrepancies were observed only in S1 among macrophytes, where there was a slight decrease in grazers and others, while there has been an increase in detritivores and shredders. These changes can be attributed to higher abundances of P. acuta and R. auricularia.
Although all gastropod species observed during the study in both SWB are very small (shell width for planorbids and shell length for other species are less than 5 mm), we can assume that small-sized fish in S1 did not consume gastropods. Therefore, the abundance of gastropods was significantly higher in S1 than in S2, where larger-sized fish species, including carp, which can effectively feed on snails, predominated.
Finally, we can conclude that both methods of assessing environmental conditions using the taxonomic approach and functional diversity of gastropod assemblages may be useful tools that can be applied for monitoring changes in ecosystem functions in the SWB that are influenced by water level fluctuations.

Author Contributions

Conceptualization, J.L., M.Š.; methodology, J.L., M.Š.; validation, J.L, A.K., M.Š., N.K.-K., T.D., M.S.P., I.T., S.G. and I.Z.; formal analysis, J.L., M.Š., T.D., M.S.P. and A.K.; investigation, J.L., M.Š., T.D. and I.Z.; writing—original draft preparation, J.L., T.D., M.Š., M.S.P. and N.K.-K.; writing—review and editing, J.L, A.K., M.Š., N.K.-K., T.D., M.S.P., I.T., S.G. and I.Z.; visualization, J.L., A.K. and S.G. All authors have read and agreed to the published version of the manuscript.

Funding

This research received no external funding.

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

Not applicable.

Acknowledgments

We thank the anonymous reviewers for their useful comments to improve the manuscript.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Castro, B.B.; Antunes, S.C.; Pereira, R.; Soares, A.M.V.M.; Gonçalves, F. Rotifer community structure in three shallow lakes: Seasonal fluctuations and explanatory factors. Hydrobiologia 2005, 543, 221–232. [Google Scholar] [CrossRef]
  2. Špoljar, M.; Dražina, T.; Lajtner, J.; Duić Sertić, M.; Radanović, I.; Wallace, R.L.; Matulić, D.; Tomljanović, T. Zooplankton assemblage in four temperate shallow waterbodies in association with habitat heterogeneity and alternative states. Limnologica 2018, 71, 51–61. [Google Scholar] [CrossRef]
  3. Kozak, A.; Celewicz-Gołdyn, S.; Kuczyńska-Kippen, N. Cyanobacteria in small water bodies: The effect of habitat and catchment area conditions. Sci. Total Environ. 2019, 646, 1578–1587. [Google Scholar] [CrossRef]
  4. Kuczyńska-Kippen, N.; Špoljar, M.; Mleczek, M.; Zhang, C. Elodeids, but not helophytes, increase community diversity and reduce trophic state: Case study with rotifer indices in field ponds. Ecol. Indic. 2021, 128, 107829. [Google Scholar] [CrossRef]
  5. Cremona, F.; Planas, D.; Lucotte, M. Biomass and composition of macroinvertebrate communities associated with different types of macrophyte architectures and habitats in a large fluvial lake. Fund. Appl. Limnol. 2008, 171, 119–130. [Google Scholar] [CrossRef]
  6. Fan, Z.; Wang, Z.; Li, Y.; Wang, W.; Tang, C.; Zeng, F. Water Level Fluctuation under the Impact of Lake Regulation and Ecological Implication in Huayang Lakes, China. Water 2020, 12, 702. [Google Scholar] [CrossRef] [Green Version]
  7. Špoljar, M.; Sertić Perić, M.; Wang, H.; Zhang, C.; Kuczyńska-Kippen, N.; Fressl, J.; Ercegovac, Z. Does the size structure of the littoral community reflect water level fluctuations in shallow waterbodies? Ecol. Indic. 2021, 132, 108330. [Google Scholar] [CrossRef]
  8. Blindow, I. Long- and short-term dynamics of submerged macrophytes in two shallow eutrophic lakes. Freshw. Biol. 1992, 28, 15–27. [Google Scholar] [CrossRef]
  9. Van Geest, G.J.; Coops, H.; Scheffer, M.; van Nes, E.H. Long transients near the ghost of a stable state in eutrophic shallow lakes with fluctuating water levels. Ecosystems 2007, 10, 37–47. [Google Scholar] [CrossRef] [Green Version]
  10. Mjelde, M.; Hellsten, S.; Ecke, F. A water level drawdown index for aquatic macrophytes in Nordic lakes. Hydrobiologia 2013, 704, 141–151. [Google Scholar] [CrossRef]
  11. Kuczyńska-Kippen, N.; Nagengast, B.; Celewicz-Gołdyn, S.; Klimko, M. Zooplankton community structure within various macrophyte stands of a small water body in relation to seasonal changes in water level. Oceanol. Hydrobiol. Stud. 2009, 38, 125–133. [Google Scholar] [CrossRef]
  12. Vadeboncoeur, Y.; Steinman, A.D. Periphyton Function in Lake Ecosystems. Sci. World J. 2002, 2, 1449–1468. Available online: https://academic.oup.com/bioscience/article/52/1/44/291662?login=true (accessed on 7 June 2022). [CrossRef] [Green Version]
  13. Carmignani, J.R.; Roy, A.H. Ecological impacts of winter water level drawdowns on lake littoral zones. Aquat. Sci. 2017, 79, 803–824. [Google Scholar] [CrossRef] [Green Version]
  14. Bolpagni, R.; Poikane, S.; Laini, A.; Bagella, S.; Bartoli, M.; Cantonati, M. Ecological and Conservation Value of Small Standing-Water Ecosystems: A Systematic Review of Current Knowledge and Future Challenges. Water 2019, 11, 402. [Google Scholar] [CrossRef] [Green Version]
  15. Water Resources in Europe in the Context of Vulnerability: EEA 2012 State of Water Assessment; EEA Report no. 11/2012; European Environment Agency: Copenhagen, Denmark, 2012; p. 92.
  16. Evtimova, V.V.; Donohue, I. Water-level fluctuations regulate the structure and functioning of natural lakes. Freshw. Biol. 2016, 61, 251–264. [Google Scholar] [CrossRef]
  17. Bill, A.R. Effects of Lake Water Level Fluctuations on Macrophytes and Littoral Macroinvertebrates. Doctoral Thesis, University of Stirling, Scotland, UK, 2020. Available online: https://dspace.stir.ac.uk/handle/1893/31954#.Ym0sPNpBxPY (accessed on 25 March 2022).
  18. Strayer, D.L.; Findlay, S.E.G. Ecology of freshwater shore zones. Aquat. Sci. 2010, 72, 127–163. [Google Scholar] [CrossRef] [Green Version]
  19. O’Leary, S.J.; Wantzen, K.M. Flood pulse effects on benthic invertebrate assemblages in the hypolacustric interstitial zone of Lake Constance. Int. J. Limnol. 2012, 48, 267–277. [Google Scholar] [CrossRef] [Green Version]
  20. Gownaris, N.J.; Rountos, K.J.; Kaufman, L.; Kolding, J.; Lwiza, K.M.M.; Pikitch, E.K. Water level fluctuations and the ecosystem functioning of lakes. J. Great Lakes Res. 2018, 44, 1154–1163. [Google Scholar] [CrossRef]
  21. Briers, R.A.; Biggs, J. Indicator taxa for the conservation of pond invertebrate diversity. Aquat. Conserv. Mar. Freshw. Ecosyst. 2003, 13, 323–330. [Google Scholar] [CrossRef]
  22. Ruggiero, A.; Céréghino, R.; Figuerola, J.; Marty, P.; Angélibert, S. Farm ponds make a contribution to the biodiversity of aquatic insects in a French agricultural landscape. C. R. Biol. 2008, 331, 298–308. [Google Scholar] [CrossRef]
  23. Vilenica, M.; Pozojević, I.; Vučković, N.; Mihaljević, Z. How suitable are man-made water bodies as habitats for Odonata? Knowl. Manag. Aquat. Ecosyst. 2020, 421, 13. [Google Scholar] [CrossRef]
  24. de los Rios-Escalante, P.; Roa, G. Species assemblages of zooplanktonic crustaceans in mountain shallow ponds of Chile (Parque Cañi). Zoologia 2010, 27, 81–86. [Google Scholar] [CrossRef] [Green Version]
  25. Barbiero, R.P.; Rudstam, L.G.; Watkins, J.M.; Lesht, B.M. A cross-lake comparison of crustacean zooplankton communities in the Laurentian Great Lakes, 1997–2016. J. Great Lakes Res. 2019, 45, 672–690. [Google Scholar] [CrossRef]
  26. Lombardo, P.; Cooke, G.D. Resource use and partitioning by two co-occuring freshwater gastropod species. Arch. Hydrobiol. 2004, 159, 229–251. [Google Scholar] [CrossRef]
  27. Kołodziejczyk, A. Occurrence of gastropoda in the lake littoral and their role in the production and transformation of detritus. II. Ecological activity of snails. Ekol. Pol. 1984, 32, 469–492. [Google Scholar]
  28. Lodge, D. Selective grazing on periphyton: A determinant of freshwater gastropod microdistributions. Freshw. Biol. 1986, 16, 831–841. [Google Scholar] [CrossRef]
  29. Stickle, W.B.; Carrington, E.; Hayford, H. Seasonal changes in the thermal regime and gastropod tolerance to temperature and desiccation stress in the rocky intertidal zone. J. Exp. Mar. Biol. 2017, 488, 83–91. [Google Scholar] [CrossRef]
  30. Brönmark, C. Interactions between Epiphytes, Macrophytes and Freshwater Snails. J. Moll. Stud. 1989, 55, 299–311. Available online: https://www.jstor.org/stable/4219655 (accessed on 16 February 2022). [CrossRef]
  31. Cardoso, L.D.S.; Marques, D.D.M. Structure of the zooplankton community in a subtropical shallow lake (Itapeva Lake-South of Brazil) and its relationship to hydrodynamic aspects. Hydrobiologia 2004, 518, 123–134. [Google Scholar] [CrossRef]
  32. Špoljar, M.; Dražina, T.; Ostojić, A.; Miliša, M.; Gligora Udovič, M.; Štafa, D. Bryophyte communities and seston in a karst stream (Jankovac Stream, Papuk Nature Park, Croatia). Ann. Limnol. 2012, 481, 125–138. [Google Scholar] [CrossRef] [Green Version]
  33. Dražina, T.; Korša, A.; Špoljar, M.; Maguire, I.; Klobučar, G. Epifauna of native and alien freshwater crayfish species (Crustacea: Decapoda): A host-specific community? Freshw. Sci. 2018, 37, 593–604. [Google Scholar] [CrossRef]
  34. Zhang, C.; Huang, Y.; Špoljar, M.; Zhang, W.; Kuczyńska-Kippen, N. Epiphyton dependency of macrophyte biomass in shallow reservoirs and implications for water transparency. Aquat. Bot. 2018, 150, 46–52. [Google Scholar] [CrossRef]
  35. Lombardo, P.; Cooke, G.D. Consumption and preference of selected food types by two freshwater gastropod species. Arch. Hydrobiol. 2002, 155, 667–685. [Google Scholar] [CrossRef]
  36. Messyasz, B.; Kuczyńska-Kippen, N.; Nagengast, B. The epiphytic communities of various ecological types of aquatic vegetation of five pastoral ponds. Biologia 2009, 64, 88–96. [Google Scholar] [CrossRef]
  37. Walker, P.D.; Wijnhoven, S.; van der Velde, G. Macrophyte presence and growth form influence macroinvertebrate community structure. Aquat. Bot. 2013, 104, 80–87. [Google Scholar] [CrossRef]
  38. Lv, T.; Guan, X.; Fan, S.; Hanm, C.; Gao, Z.; Liu, C. Snail communities increase submerged macrophyte growth by grazing epiphytic algae and phytoplankton in a mesocosm experiment. Ecol. Evol. 2022, 12, e8615. [Google Scholar] [CrossRef]
  39. Kloskowski, J.; Nieoczym, M.; Stryjecki, R. Between-habitat distributions of pond tadpoles and their insect predators in response to fish presence. Hydrobiologia 2020, 847, 1343–1356. [Google Scholar] [CrossRef] [Green Version]
  40. Martin, T.H.; Crowder, L.B.; Dumas, C.F.; Burkholder, J.M. Indirect effects of fish on macrophytes in Bays Mountain Lake: Evidence for a littoral trophic cascade. Oecologia 1992, 89, 476–481. [Google Scholar] [CrossRef]
  41. Zębek, E.; Szymańska, U. Gastropods and perophytic algae relationships in the vicinity of a small hydroelectric plant on the Pasleka River in norteast Poland. Arch. Pol. Fish. 2014, 22, 69–80. [Google Scholar] [CrossRef]
  42. Bae, M.-J.; Park, Y.-S. Key Determinants of Freshwater Gastropod Diversity and Distribution: The Implications for Conservation and Management. Water 2020, 12, 1908. [Google Scholar] [CrossRef]
  43. Moisez, E.; Spilmont, N.; Seuront, L. Microhabitats choice in intertidal gastropods is species-, temperature- and habitat-specific. J. Therm. Biol. 2020, 94, 102785. [Google Scholar] [CrossRef] [PubMed]
  44. Evtimova, V.V.; Donohue, I. Quantifying ecological responses to amplified water level fluctuations in standing waters: An experimental approach. J. Appl. Ecol. 2014, 51, 1282–1291. [Google Scholar] [CrossRef]
  45. Glöer, P. The Freshwater Gastropods of the West-Palaearctis: Identification Key, Anatomy, Ecology, Distribution; Biodiversity Research Lab: Hetlingen, Germany, 2019. [Google Scholar]
  46. Moog, O. Fauna Aquatica Austriaca, Edition 2002. In Wasserwirtschaftskataster; Moog, O., Ed.; Bundesministerium für Land- und Forstwirtschaft, Umwelt und Wasserwirtschaft: Vienna, Austria, 2002. [Google Scholar]
  47. APHA Standard Methods for the Examination of Water and Wastewater, 20th ed.; American Public Health Association: Washington, DC, USA, 1998.
  48. Špoljar, M.; Dražina, T.; Habdija, I.; Meseljević, M.; Grčić, Z. Contrasting zooplankton assemblages in two oxbow lakes with low transparencies and narrow emergent macrophyte belts (Krapina River, Croatia). Int. Rev. Hydrobiol. 2011, 96, 175–190. [Google Scholar] [CrossRef]
  49. Nusch, E.A. Comparison of different methods for chlorophyll and phaeopigment determination. Arch. Für Hydrobiol. 1980, 14, 14–36. [Google Scholar]
  50. Sokal, R.R.; Rohlf, F.J. Biometry: The Principles and Practice of Statistics in Biological Research, 3rd ed.; W.H. Freeman: New York, NY, USA, 1995. [Google Scholar]
  51. ter Braak, C.J.F.; Smilauer, P. CANOCO Reference Manual and CanoDraw for Windows User’s Guide: Software for Canonical Community Ordination (Version 4.5); Microcomputer Power: Ithaca, NY, USA, 2002. [Google Scholar]
  52. Wantzen, K.M.; Junk, W.J.; Rothhaupt, K.-O. An extension of the floodpulse concept (FPC) for lakes. Hydrobiologia 2008, 613, 151–170. [Google Scholar] [CrossRef] [Green Version]
  53. Gownaris, N.J.; Pikitch, E.K.; Aller, J.Y.; Kaufman, L.S.; Kolding, J.; Lwiza, K.M.M.; Obiero, K.O.; Ojwang, W.O.; Malala, J.O.; Rountos, K.J. Fisheries and water level fluctuations in the world’s largest desert lake. Ecohydrology 2017, 10, e1769. [Google Scholar] [CrossRef]
  54. Mastrantuono, L.; Solimini, A.G.; Nõges, P.; Bazzanti, M. Plant-associated invertebrates and hydrological balance in the large volcanic Lake Bracciano (Central Italy) during two years with different water levels. Hydrobiologia 2008, 599, 143–152. [Google Scholar] [CrossRef]
  55. Jezidžić, L. Freshwater Snails (Gastropoda) as Indicators of Čonakut Channel Trophic Level in Kopački Rit. Master Thesis, Department of Biology, University J. J. Strossmayer in Osijek, Osijek, Croatia, 2010; p. 89. Available online: https://www.bib.irb.hr/544611 (accessed on 26 April 2022). (In Croatian).
  56. Pip, E. The ecology of freshwater gastropods in the central Canada region. Nautilus 1986, 100, 56–66. [Google Scholar]
  57. Cattaneo, A.; Galanti, G.; Gentinetta, S.; Romo, S. Epiphytic algae and macroinvertebrates on submerged and floating-leaved macrophytes in an Italian lake. Freshw. Biol. 1998, 39, 725–740. [Google Scholar] [CrossRef]
  58. Lorencová, E.; Beran, L.; Nováková, M.; Horsáková, V.; Rowson, B.; Hlaváč, J.Č.; Nekola, J.C.; Horsák, M. Invasion at the population level: A story of the freshwater snails Gyraulus parvus and G. laevis. Hydrobiologia 2021, 848, 4661–4671. [Google Scholar] [CrossRef]
  59. Ville, S.P. Shipping in the Port of Newcastle, 1780–1800. J. Transp. Hist. 1988, 9, 60–77. [Google Scholar] [CrossRef]
  60. Van Leeuwen, C.H.A.; Van Der Velde, G.; Van Lith, B.; Klaassen, M. Experimental quantification of long distance dispersal potential of aquatic snails in the gut of migratory birds. PLoS ONE 2012, 7, e32292. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  61. Beran, L.; Horsák, M. Gyraulus parvus (Mollusca: Gastropoda) in the Czech Republic. Acta Soc. Zool. Bohem. 2002, 66, 81–84. [Google Scholar]
  62. Quijón, P.A.; Contreras, H.; Jaramillo, E. Population Biology of the Intertidal Snail Chilina ovalis Sowerby (Pulmonata) in the Queule River Estuary, South-Central Chile. Estuaries Coasts 2001, 24, 69–77. [Google Scholar] [CrossRef]
  63. Walther, A.C.; Burch, J.B.; Foighil, D.Ó. Molecular phylogenetic revision of the freshwater limpet genus Ferrissia (Planorbidae: Ancylinae) in North America yields two species: Ferrissia (Ferrissia) rivularis and Ferrissia (Kincaidilla) fragilis. Malacologia 2010, 53, 25–45. [Google Scholar] [CrossRef]
  64. Marrone, F.; Lo Bruto, S.; Arculeo, M. Cryptic invasion in Southern Europe: The case of Ferrissia fragilis (Pulmonata: Ancylidae) Mediterranean populations. Biologia 2011, 663, 484–490. [Google Scholar] [CrossRef] [Green Version]
  65. Vecchioni, L.; Marrone, F.; Arculeo, M.; Arizza, V. Are there autochthonous Ferrissia (Mollusca, Planorbidae) in the Palaearctic? Molecular evidence of a widespread North American invasion of the Old World. Eur. Zool. J. 2017, 84, 411–419. [Google Scholar] [CrossRef]
  66. Vinarski, M.V. The history of an invasion: Phases of the explosive spread of the physid snail Physella acuta through Europe, Transcaucasia and Central Asia. Biol. Invasions 2017, 19, 1299–1314. [Google Scholar] [CrossRef]
  67. Spyra, A.; Cieplok, A.; Strzelec, M.; Babczyńska, A. Freshwater alien species Physella acuta (Draparnaud, 1805)-A possible model for bioaccumulation of heavy metals. Ecotoxicol. Environ. Saf. 2019, 185, 109703. [Google Scholar] [CrossRef]
  68. Cowie, R. Invertebrate invasions on Pacific Islands and the replacement of unique native faunas: A synthesis of the land and freshwater snails. Biol. Invasions 2001, 3, 119–136. [Google Scholar] [CrossRef]
  69. Strayer, D.L. Alien species in fresh waters: Ecological effects, interactions with other stressors, and prospects for the future. Freshw. Biol. 2010, 55, 152–174. [Google Scholar] [CrossRef]
  70. Kuczyńska-Kippen, N.; Pronin, M. Diversity and zooplankton species associated with certain hydroperiods and fish state in field ponds. Ecol. Indic. 2018, 90, 171–178. [Google Scholar] [CrossRef]
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Figure 1. Map with the location of the two studied shallow water bodies of the Sutla River backwater (S1—with submerged macrophytes covered littoral and S2—without macrophytes) and the ground-plan of the investigated water bodies with marked positions of sampling points in the littoral zone.
Figure 1. Map with the location of the two studied shallow water bodies of the Sutla River backwater (S1—with submerged macrophytes covered littoral and S2—without macrophytes) and the ground-plan of the investigated water bodies with marked positions of sampling points in the littoral zone.
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Figure 2. Non-metric multidimensional scaling (NMDS) ordination based on differences in summer environmental conditions in 2012 (LWL) and in 2013 (HWL). Explanation of symbol codes plotted in the diagram: e.g., S112IX refers to S1—shallow water body, 12—year 2012, roman numerals indicate the months.
Figure 2. Non-metric multidimensional scaling (NMDS) ordination based on differences in summer environmental conditions in 2012 (LWL) and in 2013 (HWL). Explanation of symbol codes plotted in the diagram: e.g., S112IX refers to S1—shallow water body, 12—year 2012, roman numerals indicate the months.
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Figure 3. Gastropod abundance within the macrophyte stands of S1. Abbreviations of species names are given in Materials and Methods.
Figure 3. Gastropod abundance within the macrophyte stands of S1. Abbreviations of species names are given in Materials and Methods.
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Figure 4. Gastropod abundance in the littoral benthal area of S1 (a) and S2 (b). Abbreviations of species names are given in Materials and Methods.
Figure 4. Gastropod abundance in the littoral benthal area of S1 (a) and S2 (b). Abbreviations of species names are given in Materials and Methods.
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Figure 5. Gastropod functional feeding groups within the macrophyte stands of S1. Abbreviations are provided in Materials and Methods.
Figure 5. Gastropod functional feeding groups within the macrophyte stands of S1. Abbreviations are provided in Materials and Methods.
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Figure 6. Gastropod functional feeding groups in the littoral benthal area of S1 (a) and S2 (b). Abbreviations are provided in Materials and Methods.
Figure 6. Gastropod functional feeding groups in the littoral benthal area of S1 (a) and S2 (b). Abbreviations are provided in Materials and Methods.
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Figure 7. RDA-plot illustrating relationships among sampling sites, physicochemical variables, and gastropod abundance within the macrophyte stands at S1. Abbreviations are provided in Materials and Methods.
Figure 7. RDA-plot illustrating relationships among sampling sites, physicochemical variables, and gastropod abundance within the macrophyte stands at S1. Abbreviations are provided in Materials and Methods.
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Figure 8. CCA-plot indicating relationships among sampling sites, physicochemical variables, and abundance of common gastropod species in the littoral benthal areas of S1 and S2. Abbreviations are provided in Materials and Methods.
Figure 8. CCA-plot indicating relationships among sampling sites, physicochemical variables, and abundance of common gastropod species in the littoral benthal areas of S1 and S2. Abbreviations are provided in Materials and Methods.
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Figure 9. RDA-plot illustrating relationships among sampling sites, physicochemical variables, and functional feeding guilds of gastropods in the littoral benthal area of S1 and S2. Abbreviations are provided in Materials and Methods.
Figure 9. RDA-plot illustrating relationships among sampling sites, physicochemical variables, and functional feeding guilds of gastropods in the littoral benthal area of S1 and S2. Abbreviations are provided in Materials and Methods.
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Table
Table 1. Mean and standard deviation (SD) of the physicochemical parameters during the study period. Temperature—water temperature; DO—dissolved oxygen concentration; EC—electrical conductivity; DOM—dissolved organic matter; POM—particulate organic matter; TN—total nitrogen concentration; TP—total phosphorous concentration; Chl a—chlorophyll concentration.
Table 1. Mean and standard deviation (SD) of the physicochemical parameters during the study period. Temperature—water temperature; DO—dissolved oxygen concentration; EC—electrical conductivity; DOM—dissolved organic matter; POM—particulate organic matter; TN—total nitrogen concentration; TP—total phosphorous concentration; Chl a—chlorophyll concentration.
Mean ± SD
VariableLWLHWL
Temperature (°C)23.2 ± 4.819.7 ± 3.0
DO (mg O2 L−1)6.8 ± 2.75.9 ± 1.3
pH8.33 ± 0.707.95 ± 0.35
EC (µS cm−1)485.8 ± 159.5430.5 ± 124.3
DOM (mg O2(Mn) L−1)17.0 ± 3.821.5 ± 5.6
POM (µg L−1 (×10−3))6.395 ± 6.21513.503 ± 18.404
TN (mg N L −1)0.896 ± 0,3270.399 ± 0.113
TP (mg P L−1)0.362 ± 0.0860.318 ± 0.026
Chl a (µg L−1)27.528 ± 18.54926.668 ± 34.119
Table
Table 2. Results of SIMPER analysis for gastropod assemblage during LWL and HWL of investigated waterbodies in S1 and S2 littoral benthal area. Av. Ab.—average abundance of specific species; Av. Sim.—average similarity of specific species; Contrib. (%)—percentage of contribution for specific species in the assemblage.
Table 2. Results of SIMPER analysis for gastropod assemblage during LWL and HWL of investigated waterbodies in S1 and S2 littoral benthal area. Av. Ab.—average abundance of specific species; Av. Sim.—average similarity of specific species; Contrib. (%)—percentage of contribution for specific species in the assemblage.
SpeciesAv. Ab.Av. Sim.Contrib. (%)
LWL
Gyraulus parvus2.045.7252.8
Radix auricularia1.231.4513.35
Ferrissia californica1.271.4213.12
Physella acuta0.91.2611.62
HWL
Gyraulus parvus3.027.1632.21
Physella acuta1.645.1723.24
Hippeutis complanatus1.313.515.75
Ferrissia californica1.693.2214.47
Radix auricularia1.13.1814.32
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Lajtner, J.; Kozak, A.; Špoljar, M.; Kuczyńska-Kippen, N.; Dražina, T.; Sertić Perić, M.; Tkalčec, I.; Gottstein, S.; Zrinščak, I. Gastropod Assemblages Associated with Habitat Heterogeneity and Hydrological Shifts in Two Shallow Waterbodies. Water 2022, 14, 2290. https://doi.org/10.3390/w14152290

AMA Style

Lajtner J, Kozak A, Špoljar M, Kuczyńska-Kippen N, Dražina T, Sertić Perić M, Tkalčec I, Gottstein S, Zrinščak I. Gastropod Assemblages Associated with Habitat Heterogeneity and Hydrological Shifts in Two Shallow Waterbodies. Water. 2022; 14(15):2290. https://doi.org/10.3390/w14152290

Chicago/Turabian Style

Lajtner, Jasna, Anna Kozak, Maria Špoljar, Natalia Kuczyńska-Kippen, Tvrtko Dražina, Mirela Sertić Perić, Ines Tkalčec, Sanja Gottstein, and Ivana Zrinščak. 2022. "Gastropod Assemblages Associated with Habitat Heterogeneity and Hydrological Shifts in Two Shallow Waterbodies" Water 14, no. 15: 2290. https://doi.org/10.3390/w14152290

APA Style

Lajtner, J., Kozak, A., Špoljar, M., Kuczyńska-Kippen, N., Dražina, T., Sertić Perić, M., Tkalčec, I., Gottstein, S., & Zrinščak, I. (2022). Gastropod Assemblages Associated with Habitat Heterogeneity and Hydrological Shifts in Two Shallow Waterbodies. Water, 14(15), 2290. https://doi.org/10.3390/w14152290

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