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164 results for “invasive fish”
Data from: Impact of the invasive alien topmouth gudgeon (Pseudorasbora parva) and its associated parasite Sphaerothecum destruens on native fish species
<p>Two datasets belonging to the paper "Impact of the invasive alien topmouth gudgeon (<i>Pseudorasbora parva</i>) and its associated parasite <i>Sphaerothecum destruens</i> on native fish species" published in Biological Invasions (https://doi.org/10.1007/s10530-019-02114-6), is provided here. The first dataset consists of individual measured and weighed fish per sampled water body. In case a large number (>50) of the same species and length were encountered, a representative number was weighed and measured, and the remaining individuals were only counted. The second dataset consists of parameters related to morphology and water quality, and number of specimens found per fish species, of each sampled water body. Below, methodological information is provided on the study site, the sampling process, and the water sample analysis. For references, see the published paper in Biological Invasions.</p><p> </p><p>Study site</p><p>We selected 54 water bodies (oxbow lakes, shallow lakes and ponds) in river floodplains of the IJssel, Meuse, Nederrijn and Waal River. These water bodies were selected using the following criteria: a) Potential presence of <i>P. parva</i> according to the Dutch National Database Flora and Fauna, b) No permanent hydrological connection with the main stream or a side channel, c) Similarity in habitat characteristics (e.g., depth and surface area, for habitat characteristics per sampling site), d) Suitability for sampling with a seine net. These criteria were set to reduce variance in the fish species composition created by habitat variables, as our aim was to detect effects caused by <i>P. parva</i>. The areas of sampled water bodies ranged from 100 to 80,000 m2. In total 54 sites located in the floodplains were visited and sampled using a seine net (21 m long, 2.4 m high, mesh size 4x4 to 10x10 mm). Fifteen sites could not be sampled sufficiently with this gear type due to high vegetation cover and/or water depth. Hence, 39 sites were included in the analyses of effect on fish assemblages and body condition. The coordinate system used here concerns Amersfoort RD (EPSG: 28992). </p><p> </p><p>Sampling</p><p>Sampling of the fish populations was carried out from October to December 2015. The seine net was used while wading and provided adequate data on juvenile and small fishes in shallow habitats. The sampling area ranged from 0.04 to 82.35% of the surface area of water bodies and was used to calculate fish densities (number of fish m-2). All caught fishes were identified, weighed (accuracy 0.05 g) and their total lengths (TL, from tip of snout to longer caudal fin lobe, accuracy 1 mm) measured in the field. Young of the year (YOY) were distinguished, based on length. Each individual was assigned to being a YOY, based on known YOY thresholds in the Netherlands. Small fishes (<35 mm) were pooled for weighting. In case a large number (>50) of the same species and length were encountered, a representative number was weighed and measured, and the remaining individuals were only counted. Subsequently, the fishes were released. </p><p>Habitat and soil parameters which included coverage percentage of aquatic vegetation, littoral vegetation, and substrate (mud, sand, gravel and rocks), and tree branches in the water were visually estimated. The water transparency (cm) was determined using a Secchi disk (measured vertically). Water temperature (°C), conductivity (μS cm-1) and salinity (PSU) were measured at the site with the use of a Model 30 meter (YSI incorporated). A water sample was taken and at the same day pH and alkalinity (eq l-1) were measured in the laboratory. Water samples in polyethylene bottles were stored in the freezer at a maximum storage time of 75 days until analysis. Metal ions were analysed using an ICP analyser (Thermo Electron corporation IRIS Intrepid ΙΙ XDL). Concentrations of nitrate (NO3-), ammonium (NH4+), phosphate (PO43-), chloride (Cl-) and potassium (K+) were determined using an Auto Analyzer 3 system (Bran and Luebbe, Norderstedt Germany). Physico-chemical data is missing for site 39 due to loss of the sample.</p><p> </p><p>Abstract</p><p>The Asian cyprinid <i>Pseudorasbora parva</i> is considered to be a major threat to native fish communities and listed as an invasive alien species of European Union concern. Our study aims to gain evidence-based knowledge on the impact of both <i>P. parva</i> and it parasite <i>Sphaerothecum destruens</i> on native fish populations by analysing fish assemblages and body condition of individuals of native fish species in floodplain water bodies that were invaded and uninvaded by <i>P</i>. <i>parva</i>. We explored the use of environmental DNA (eDNA) techniques to detect <i>S. destruens</i>. Prevalence of <i>S. destruens</i> in native fish species was assessed. Fish samplings showed significantly negative correlations between the abundance of <i>P. parva</i> and the native <i>Leucaspius delineatus</i>, and <i>Pungitius pungitius</i> and three biodiversity indices of the fish assemblages (Simpson's diversity index, Shannon-Wiener index and evenness). Contrastingly, the abundances of the native <i>Gasterosteus aculeatus</i> and <i>P. parva</i> were positively related. In nearly all isolated water bodies with <i>P. parva</i>, this species is outnumbering native fish species. No effect of <i>P. parva</i> presence was found on body condition of native fish species. <i>Sphaerothecum destruens</i> was demonstrated to occur in both <i>P. parva</i> and <i>G. aculeatus</i>. <i>Gasterosteus aculeatus</i> is suggested to be an asymptomatic carrier that can aid the further spread of <i>S. destruens,.</i> Analysis of eDNA proved to be a promising method for early detection of <i>S. destruens</i>, here showing that <i>S. destruens</i> presence coincided with <i>P. parva</i> presence. The ongoing invasion of both <i>P. parva</i> and <i>S. destruens</i> is predicted to pose a significant risk to native fish communities.</p>
Turning summer into winter: nutrient dynamics, temperature, density dependence, and invasive species drive bioenergetic processes and growth of a keystone coldwater fish
<p>A combination of global changes such as species invasions, climate change, and nutrient pollution have altered ecosystems, food webs, and the bioenergetic processes that control growth. These changes are especially pronounced in freshwater ecosystems and often lead to rapid variation in fish growth and dependent ecosystems services such as fishery yield. Understanding the mechanisms driving growth responses to environmental change is important for interpreting past dynamics and sustainably managing ecosystems. This study uses integrated bioenergetics and growth modeling to understand how nutrient dynamics, species invasions, and changing temperatures have altered growth of the keystone pelagic whitefish (<em>Coregonus</em> <em>wartmanni</em>) in Lake Constance, Germany from 1925 to 2020. Growth variation was modeled by allowing covariates to alter temperature-dependent consumption, while size-specific metabolism varied only with temperature. Consumption and growth increased strongly to a maximum with phosphorous, and this effect was stronger when intraspecific competition (measured as whitefish biomass) was low. Increasing whitefish biomass reduced growth under mesotrophic conditions, but had no effect under oligotrophic conditions. In contrast, increasing competition with invasive three-spined stickleback (<em>Gasteosteus</em> <em>aculeauts</em>) was predicted to reduce growth even under oligotrophic conditions. The invasion has effectively turned summer into winter for whitefish, with older fish ceasing to grow and younger fish losing up to 10% of their body weight during the normal growing season in subsequent years. Warming is predicted to further reduce whitefish growth due to competition with invasive stickleback, which would further alter zooplankton food availability and reduce already low fishery yields. These results demonstrate the importance of considering biotic interactions and synergistic effects in global change studies, as well as the value of mechanistic-based models for understanding effects. Similar growth responses to ecosystem change are likely within and across ecosystems, and bioenergetic models can help understand effects to support informed ecosystem management.</p>
Data for: Differential habitat use of a notorious invasive fish, the round goby, in a translocation-relevant system
<p>Anthropogenic structures can form novel ecosystem niches. Invasive species are often particularly successful in occupying these habitats and utilize them as beachheads for further spread. The invasive round goby (<em>Neogobius melanostomus</em>, Pallas 1814), an inherently bottom-dwelling fish, uses vertical harbour walls as habitat, enabling them to reach boats (i.e. potential translocation vectors). To evaluate the relevance of vertical habitat use for population dynamics and translocation, we exemplary investigated a population of round gobies in a harbour ecosystem. Specifically, we investigated differences in trophic niche characteristics, individual trophic specialization, phenotypic traits, and breeding frequency in wall versus bottom dwelling round gobies. Habitat-characteristic dietary signatures indicated habitat partitioning during the breeding season. Trophic niches overlapped but were clearly distinguishable between the habitats: walls were inhabited by 1.4 times more trophic generalists than specialists, while the bottom was inhabited by 2.1 times more trophic specialists. Breeding frequency was 24 times higher on the walls than on the bottom. After the reproductive season, we found a higher similarity in trophic ecology of gobies inhabiting the two habitats, and differences in abundance, size, and condition. These results are in line with winter migrations to deeper habitats, which are common in round gobies in lentic and marine ecosystems. Our results suggest a high potential for microgeographic adaptation to either horizontal or vertical habitat use in invasive round gobies. We demonstrated that male gobies using the walls during the breeding season are larger and heavier, <span>s</span>uggesting that wall-climbing may select for more competitive individuals. Additionally, the overall abundance of round gobies likely increases with the additional use of vertical habitat space, which may lead to higher propagule pressure. The ability to exploit anthropogenic habitats, and a higher translocation probability of competitive individuals, can contribute to the invasion success of round gobies in anthropogenically influenced aquatic systems.</p>
Fish carcass deposition to suppress invasive lake trout through hypoxia causes limited, non-target effects on benthic invertebrates in Yellowstone Lake
<p class="MsoNormal">Invasive species can have negative effects on native biodiversity and ecosystem function, and suppression is often required to minimize the effects. However, management actions to suppress invasive species may cause negative, unintended effects on non-target taxa. Across the USA, lake trout (<em>Salvelinus namaycush</em>) are invasive in many freshwater ecosystems, reducing native fish abundance and diversity through predation and competition. In an integrated pest management approach, lake trout embryos in Yellowstone Lake, Wyoming are suppressed by depositing lake trout carcasses onto spawning sites; the carcasses reduce dissolved oxygen concentrations as they decay, causing embryo mortality. We conducted a field experiment during one ice-free season at four sites in Yellowstone Lake to investigate the non-target effects of carcass treatment on benthic invertebrates, which could have consequences for native fish diets. While overall invertebrate density and biomass did not respond to carcass treatment, Chironomidae midges and Sphaeriidae fingernail clams decreased in abundance. Carcass treatment altered invertebrate community structure based on density, but not biomass. Carcass treatment to suppress invasive fish embryos has spatially localized, non-target effects on some benthic invertebrate taxa. Given the small spatial extent of carcass treatment within the lake, we conclude it is unlikely that carcass treatment will alter food availability for native fishes.</p>
Data from: Development and validation of targeted environmental DNA (eDNA) metabarcoding for early detection of 69 invasive fishes and aquatic invertebrates
<p>Invasive species are of concern due to their impacts on ecosystems and economies, but they pose significant control challenges. Environmental DNA (eDNA) is a powerful tool in the detection of aquatic organisms at low densities due to high sensitivity and ease of collection. Aquatic eDNA analyses have increased worldwide and are generally either applied to a few target species (quantitative PCR) or for broad taxonomic applications (metabarcoding). Here we describe the development and testing of a hybrid approach that utilized high sensitivity PCR primer sets and high-throughput sequencing (HTS), referred to as <em>targeted metabarcoding</em>, to detect 69 fishes and invertebrates. We identified target species based on reports of globally important invasive species and developed two independent PCR primers for each species (CO1 and a second mtDNA region). We assessed sensitivity and eDNA interference for all 138 primers (2 per species, 69 species) using standard end-point PCR and tested them on 10 eDNA samples spiked with various amounts of one or more of the target species' DNA. The sensitivity of the 138 primer sets ranged between 1.5×10<sup>-5</sup> and 2.64 ng template DNA (mean = 0.069 ng). Primers were also tested for interference effects using plankton eDNA to simulate field conditions. The inclusion of interfering plankton DNA reduced the sensitivity for most primer sets by one or more orders of magnitude (range 0 to 3). Overall, our targeted metabarcoding resulted in the detection of ~ 98% of species in the DNA spiked samples, and, perhaps more importantly, the HTS read count was positively related to the quantity of spiked DNA (P < 0.002). We envision this technique being particularly useful for the early detection of species at low population densities; however, there are diverse applications of targeted metabarcoding for monitoring aquatic community composition and quantifying ecosystem change and health.</p>
Fig. 6 in Reciprocal Predation Between Preserved And Invasive Species: Adult Bombina Bombina Predate Young Whitebaits Of Alien Fish Perccottus Glenii
Fig. 6. Plot for fitted model of initial number of live and predated P. glenii.
Fig. 2. Experimental box with P in Reciprocal Predation Between Preserved And Invasive Species: Adult Bombina Bombina Predate Young Whitebaits Of Alien Fish Perccottus Glenii
Fig. 2. Experimental box with P. glenii and pair of B. bombina.
Fig. 2 in Behavioral Responses Of Salmonid Fingerlings To New Invasive Fish Predator Perccottus Glenii
Fig. 2. Large adult Perccottus glenii male used in the experiment.
Fig. 8 in The Distribution Of The Invasive Fish Amur Sleeper, Rotan Perccottus Glenii Dybowski, 1877 (Osteichthyes, Odontobutidae), In Latvia
Fig. 8. Perccottus glenii, caught in the biotope of Emys orbicularis. Lake Trikartu, Daugavpils.
Fig. 2 in The Distribution Of The Invasive Fish Amur Sleeper, Rotan Perccottus Glenii Dybowski, 1877 (Osteichthyes, Odontobutidae), In Latvia
Fig. 2. The method of fishing Perccottus glenii with the help of a landing net.
Fig. 1 in Drought-associated absence of alien invasive anchorworm, Lernaea cyprinacea (Copepoda: Lernaeidae), is related to changes in fish health
Fig. 1. Map of Nyamiti pan situated on the Phongolo River floodplain.
Figure 1 in Contribution to the knowledge of fish fauna of Kosovo with a special note on some invasive species
Figure 1. Four sampling stations in Badovc Lake (B1, B2, B3, and B4).
Figure 4 in New location, food composition, and parasitic fauna of the invasive fish Pseudorasbora parva (Temminck & Schlegel, 1846) (Cyprinidae) in Poland
Figure 4. Von Bertalanffy growth curve for males and females of stone moroko from Wardynka creek.
Table 1 in America's Most Wanted Fishes: cataloging risk assessments to prioritize invasive species for management action
<p><b>Table 1.</b> List of fish species with high-risk statuses in the conterminous U.S., in the Great Lakes region, and in the state of Florida. Horizontal lines separate families and species for clarity.</p><table><tbody><tr><th>Family Name</th><th>Fish species name</th><th>Conterminous U.S.</th><th>Great Lakes</th><th>Florida</th></tr></tbody><tbody><tr><th>Atherinidae</th><td><i>Atherina boyeri</i> (Risso, 1810)</td><td>X</td><td>X</td><td></td></tr><tr><th>Atherinopsidae</th><td><i>Menidia beryllina</i> (Cope, 1867)</td><td>X</td><td></td><td></td></tr><tr><td><i>Odontesthes bonariensis</i> (Valenciennes, 1835)</td><td>X</td><td></td><td></td></tr><tr><th>Callichthyidae</th><td><i>Hoplosternum littorale</i> (Hancock, 1828)</td><td></td><td></td><td>X</td></tr><tr><th>Centrarchidae</th><td><i>Lepomis microlophus</i> (Günther, 1859)</td><td>X</td><td>X</td><td></td></tr><tr><td><i>Micropterus dolomieu</i> (Lacepède, 1802)</td><td>X</td><td></td><td></td></tr><tr><td><i>Micropterus salmoides</i> (Lacepède, 1802)</td><td>X</td><td></td><td></td></tr><tr><th>Centropomidae</th><td><i>Lates niloticus</i> (Linnaeus, 1758)</td><td>X</td><td></td><td></td></tr><tr><th>Channidae</th><td><i>Channa argus</i> (Cantor, 1842)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Channa marulius</i> (Hamilton, 1822)</td><td></td><td></td><td>X</td></tr><tr><th>Characidae</th><td><i>Pygocentrus nattereri</i> (Kner, 1858)</td><td>X</td><td></td><td></td></tr><tr><th>Cichlidae</th><td><i>Amatitlania nigrofasciata</i> (Günther, 1867)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Astronotus ocellatus</i> (Agassiz, 1831)</td><td>X</td><td></td><td></td></tr><tr><td><i>Cichla kelberi</i> (Kullander & Ferreira, 2006)</td><td>X</td><td></td><td></td></tr><tr><td><i>Cichla ocellaris</i> (Bloch & Schneider, 1801)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Cichlasoma uropthalma</i> (Günther, 1862)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Coptodon rendalli</i> (Boulenger, 1897)</td><td>X</td><td></td><td></td></tr><tr><td><i>Coptodon zilli</i> (Gervais, 1848)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Hemichromis letourneuxi</i> (Sauvage, 1880)</td><td>X</td><td></td><td></td></tr><tr><td><i>Herichthys cyanoguttatus</i> (Baird & Girard, 1854)</td><td>X</td><td></td><td></td></tr><tr><td><i>Oreochromis aureus</i> (Steindachner, 1864)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Oreochromis mossambicus</i> (Peters, 1852)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Oreochromis niloticus</i> (Linnaeus, 1758)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Parachromis managuensis</i> (Günther, 1862)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Pelmatotilapia mariae</i> (Boulenger, 1899)</td><td>X</td><td></td><td></td></tr><tr><td><i>Sarotherodon melanotheron</i> (Rüppell, 1852)</td><td>X</td><td></td><td></td></tr><tr><td><i>Serranochromis robustus</i> (Günther, 1864)</td><td>X</td><td></td><td></td></tr><tr><th>Clariidae</th><td><i>Clarias batrachus</i> (Linnaeus, 1758)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Clarias fuscus</i> (Lacepède, 1803)</td><td>X</td><td></td><td></td></tr><tr><td><i>Clarias gariepinus</i> (Burchell, 1822)</td><td>X</td><td></td><td></td></tr><tr><th>Clupeidae</th><td><i>Alosa aestivalis</i> (Mitchell, 1814)</td><td>X</td><td></td><td></td></tr><tr><td><i>Alosa pseudoharengus</i> (Wilson, 1811)</td><td>X</td><td>X</td><td></td></tr><tr><th>Cobitidae</th><td><i>Misgurnus anguillicaudatus</i> (Cantor, 1842)</td><td>X</td><td></td><td>X</td></tr><tr><th>Cyprinidae</th><td><i>Abramis brama</i> (Linnaeus, 1758)</td><td>X</td><td></td><td></td></tr><tr><td><i>Alburnus alburnus</i> (Linnaeus, 1758)</td><td>X</td><td></td><td></td></tr><tr><td><i>Barbus barbus</i> (Linnaeus, 1758)</td><td>X</td><td></td><td></td></tr><tr><td><i>Carassius auratus</i> (Linnaeus, 1758)</td><td></td><td></td><td>X</td></tr><tr><td><i>Carassius gibelio</i> (Bloch, 1782)</td><td>X</td><td></td><td></td></tr><tr><td><i>Ctenopharyngodon idella</i> (Valenciennes, 1844)</td><td>X</td><td>X</td><td>X</td></tr><tr><td><i>Culter alburnus</i> (Basilewsky, 1855)</td><td>X</td><td></td><td></td></tr><tr><td><i>Cyprinella lutrensis</i> (Baird & Girard, 1853)</td><td>X</td><td></td><td></td></tr><tr><td><i>Cyprinus carpio</i> (Linnaeus, 1758)</td><td>X</td><td>X</td><td>X</td></tr><tr><td><i>Gobio gobio</i> (Linnaeus, 1758)</td><td>X</td><td></td><td></td></tr><tr><td><i>Hypophthalmichthys molitrix</i> (Valenciennes, 1844)</td><td>X</td><td></td><td></td></tr><tr><td><i>Hypophthalmichthys nobilis</i> (Richardson, 1845)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Leuciscus idus</i> (Linnaeus, 1758)</td><td>X</td><td></td><td></td></tr><tr><td><i>Mylopharyngodon piceus</i> (Richardson, 1846)</td><td>X</td><td></td><td></td></tr><tr><td><i>Opsariichthys uncirostris</i> (Temminck & Schlegel, 1846)</td><td>X</td><td></td><td></td></tr><tr><td><i>Pimephales promelas</i> (Rafinsque, 1820)</td><td></td><td></td><td>X</td></tr><tr><td><i>Phoxinus phoxinus</i> (Linnaeus, 1758)</td><td>X</td><td></td><td></td></tr><tr><td><i>Protochondrostoma genei</i> (Bonaparte, 1839)</td><td>X</td><td></td><td></td></tr><tr><td><i>Pseudorasbora parva</i> (Temminck & Schlegel, 1846)</td><td>X</td><td></td><td></td></tr><tr><td><i>Rhodeus amarus</i> (Bloch, 1782)</td><td>X</td><td></td><td></td></tr><tr><td><i>Rutilus aula</i> (Bonparte,1841)</td><td>X</td><td></td><td></td></tr><tr><td><i>Rutilus rutilus</i> (Linnaeus, 1758)</td><td>X</td><td>X</td><td></td></tr><tr><td><i>Scardinius erythrophthalmus</i> (Linnaeus, 1758)</td><td>X</td><td>X</td><td></td></tr><tr><td><i>Tinca tinca</i> (Linnaeus, 1758)</td><td>X</td><td>X</td><td></td></tr><tr><th>Esocidae</th><td><i>Esox lucius</i> (Linnaeus, 1758)</td><td>X</td><td></td><td></td></tr><tr><td><i>Esox masquinongy</i> (Mitchill, 1824)</td><td>X</td><td></td><td></td></tr><tr><th>Gasterosteidae</th><td><i>Gasterosteus aculeatus</i> (Linnaeus, 1758)</td><td>X</td><td>X</td><td></td></tr><tr><th>Gobiidae</th><td><i>Neogobius melanostomus</i> (Pallas, 1814)</td><td>X</td><td>X</td><td></td></tr><tr><td><i>Ponticola platyrostris</i> (Pallas, 1814)</td><td>X</td><td></td><td></td></tr><tr><td><i>Proterorhinus semilunaris</i> (Heckel, 1837)</td><td>X</td><td></td><td></td></tr><tr><th>Heteropneustidae</th><td><i>Heteropneustes fossilis</i> (Bloch, 1794)</td><td>X</td><td></td><td></td></tr><tr><th>Ictaluridae</th><td><i>Ictalurus furcatus</i> (Valenciennes, 1840)</td><td>X</td><td></td><td></td></tr><tr><td><i>Pylodictis olivaris</i> (Rafinesque, 1818)</td><td>X</td><td></td><td></td></tr><tr><th>Loricariidae</th><td><i>Hypostomus plecostomus</i> (Linnaeus, 1758)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Pterygoplichthys anisitsi</i> (Eigenmann & Kennedy, 1903)</td><td></td><td></td><td>X</td></tr><tr><td><i>Pterygoplichthys disjunctivus</i> (Weber, 1991)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Pterygoplichthys multiradiatus</i> (Hancock, 1828)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Pterygoplichthys pardalis</i> (Castelnau, 1855)</td><td>X</td><td></td><td></td></tr><tr><th>Moronidae</th><td><i>Morone americana</i> (Gmelin, 1789)</td><td>X</td><td>X</td><td></td></tr><tr><th>Notopteridae</th><td><i>Chitala ornata</i> (Gray, 1831)</td><td>X</td><td></td><td></td></tr><tr><th>Odontobutidae</th><td><i>Perccottus glenii</i> (Dybowski, 1877)</td><td>X</td><td></td><td></td></tr><tr><th>Osmeridae</th><td><i>Hypomesus nipponensis</i> (McAllister, 1963)</td><td>X</td><td></td><td></td></tr><tr><td><i>Osmerus eperlanus</i> (Linnaeus, 1758)</td><td>X</td><td>X</td><td></td></tr><tr><td><i>Osmerus mordax</i> (Mitchill, 1814)</td><td>X</td><td></td><td></td></tr><tr><th>Osphronemidae</th><td><i>Trichogaster lalius</i> (Hamilton, 1822)</td><td>X</td><td></td><td></td></tr><tr><td><i>Trichopodus trichopterus</i> (Pallas, 1770)</td><td>X</td><td></td><td></td></tr><tr><th>Percidae</th><td><i>Gymnocephalus cernua</i> (Linnaeus, 1758)</td><td>X</td><td>X</td><td></td></tr><tr><td><i>Perca flavescens</i> (Mitchill, 1814)</td><td>X</td><td></td><td></td></tr><tr><td><i>Perca fluviatilis</i> (Linnaeus, 1758)</td><td>X</td><td>X</td><td></td></tr><tr><td><i>Sander lucioperca</i> (Linnaeus, 1758)</td><td>X</td><td></td><td></td></tr><tr><td><i>Sander vitreus</i> (Mitchill, 1818)</td><td>X</td><td></td><td></td></tr><tr><th>Petromyzontidae</th><td><i>Petromyzon marinus</i> (Linnaeus, 1758)</td><td></td><td>X</td><td></td></tr><tr><th>Poeciliidae</th><td><i>Belonesox belizanus</i> (Kner, 1860)</td><td>X</td><td></td><td></td></tr><tr><td><i>Gambusia affinis</i> (Baird & Girard, 1853)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Gambusia holbrooki</i> (Girard, 1859)</td><td>X</td><td></td><td></td></tr><tr><td><i>Poecilia latipinna</i> (Lesueur, 1821)</td><td>X</td><td></td><td></td></tr><tr><td><i>Poecilia reticulata</i> (Peters, 1859)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Poecilia sphenops</i> (Valciennes, 1846)</td><td>X</td><td></td><td>X</td></tr><tr><td><i>Xiphophorus helleri</i> (Heckel, 1848)</td><td>X</td><td></td><td></td></tr><tr><td><i>Xiphophorus variatus</i> (Meek, 1904)</td><td>X</td><td></td><td></td></tr><tr><th>Polypteridae</th><td><i>Polypterus delhezi</i> (Boulenger, 1899)</td><td></td><td></td><td>X</td></tr><tr><th>Pomacentridae</th><td><i>Neopomacentrus cyanomos</i> (Bleeker, 1856)</td><td>X</td><td></td><td></td></tr><tr><th>Potamotrygonidae</th><td><i>Potamotrygon falkneri</i> (Castex & Maciel, 1963)</td><td>X</td><td></td><td></td></tr><tr><td><i>Potamotrygon motoro</i> (Müller & Henle, 1841)</td><td>X</td><td></td><td></td></tr><tr><td><i>Potamotrygon schuhmacheri</i> (Castex, 1964)</td><td>X</td><td></td><td></td></tr><tr><th>Salmonidae</th><td><i>Coregonus albula</i> (Linnaeus, 1758)</td><td>X</td><td></td><td></td></tr><tr><td><i>Coregonus lavaretus</i> (Linnaeus, 1758)</td><td>X</td><td></td><td></td></tr><tr><td><i>Coregonus maraena</i> (Bloch, 1779)</td><td>X</td><td></td><td></td></tr><tr><td><i>Coregonus peled</i> (Gmelin, 1789)</td><td>X</td><td></td><td></td></tr><tr><td><i>Hucho hucho</i> (Linnaeus, 1758)</td><td>X</td><td></td><td></td></tr><tr><td><i>Oncorhynchus kisutch</i> (Walbaum, 1792)</td><td></td><td>X</td><td></td></tr><tr><td><i>Oncorhynchus mykiss</i> (Walbaum, 1792)</td><td></td><td>X</td><td></td></tr><tr><td><i>Oncorhynchus tshawytscha</i> (Walbaum, 1792)</td><td></td><td>X</td><td></td></tr><tr><td><i>Salmo trutta</i> (Linnaeus, 1758)</td><td></td><td>X</td><td></td></tr><tr><th>Scorpaenidae</th><td><i>Pterois miles</i> (Bennett, 1828)</td><td>X</td><td></td><td></td></tr><tr><td><i>Pterois volitans</i> (Linnaeus, 1758)</td><td>X</td><td></td><td></td></tr><tr><th>Siluridae</th><td><i>Silurus glanis</i> (Linnaeus, 1758)</td><td>X</td><td></td><td></td></tr></tbody></table>
Ancestral sperm ecotypes reveal multiple invasions of a non-native fish in northern Europe
For externally fertilising organisms in the aquatic environment, the abiotic fertilisation medium can be a strong selecting force. Among bony fishes, sperm are adapted to function in a narrow salinity range. A notable exception is the family Gobiidae, where several species reproduce across a wide salinity range. The family also contains several wide-spread invasive species. To better understand how these fishes tolerate such varying conditions, we measured sperm performance in relation to salinity from a freshwater and a brackish population within their ancestral Ponto-Caspian region of the round goby, Neogobius melanostomus. These two ancestral populations were then compared to nine additional invaded sites across northern Europe, both in terms of their sperm traits and by using genomic SNP markers. Our results show clear patterns of ancestral adaptations to freshwater and brackish salinities in their sperm performance. Population genomic analyses show that the ancestral ecotypes have generally established themselves in environments that fit their sperm adaptations. Sites close to ports with intense shipping show that both outbreeding and admixture can affect the sperm performance of a population in a given salinity. Rapid adaptation to local conditions is also supported at some sites. Historical and contemporary evolution in the traits of the round goby sperm cells is tightly linked to the population and seascape genomics as well as biogeographic processes in these invasive fishes. Since the risk of a population establishing in an area is related to the genotype by environment match, port connectivity and the ancestry of the round goby population can likely be useful for predicting the species spread.
Predicting the competitive interactions and trophic niche consequences of a globally invasive fish with threatened native species
<p>1. Novel trophic interactions between invasive and native species potentially increase levels of inter-specific competition in the receiving environment. However, theory on the trophic impacts of invasive fauna on native competitors is ambiguous, as while increased inter-specific competition can result in the species having constricted and diverged trophic niches, the species might instead increase their niche sizes, especially in omnivorous species.</p> <p>2. The competitive interactions between an omnivorous invasive fish, common carp Cyprinus carpio, and a tropically analogous native and threatened fish, crucian carp Carassius carassius, were tested using comparative functional responses (CFRs). A natural pond experiment then presented the species in allopatry and sympatry, determining the changes in their trophic (isotopic) niche sizes and positions over four years. These predictive approaches were complemented by assessing their trophic relationships in wild populations.</p> <p>3. CFRs revealed that compared to crucian carp, carp had a significantly higher maximum consumption rate. Coupled with a previous cohabitation growth study, these results predicted that competition between the species is asymmetric, with carp the superior competitor.</p> <p>4. The pond experiment used stable isotope metrics to quantify shifts in the trophic (isotopic) niche sizes of the fishes. In allopatry, the isotopic niches of the two species were similar sized and diverged. Conversely, in sympatry, carp isotopic niches were always considerably larger than those of crucian carp and were strongly partitioned. Sympatric crucian carp had larger isotopic niches than allopatric conspecifics, a likely response to asymmetric competition from carp. However, carp isotopic niches were also larger in sympatry than allopatry. In the wild populations, the carp isotopic niches were always larger than crucian carp niches, and were highly divergent.</p> <p>5. The superior competitive abilities of carp predicted in aquaria experiments were considered to be a process involved in sympatric crucian carp having larger isotopic niches than in allopatry. However, as sympatric carp also had larger niches than in allopatry, this suggests other ecological processes were also likely to be involved, such as those relating to fish prey resources. These results highlight the inherent complexity in determining how omnivorous invasive species integrate into food-webs and alter their structure.</p>
DATA FOR NON-INVASIVE (PHOTO) INDIVIDUAL FISH IDENTIFICATION OF MULTIPLE SPECIES
<p>This paper describes data from five studies focused on the individual fish identification of the same species. The lateral images of five fish species are present in the dataset. The dataset's primary purpose is to provide a data to develop a non-invasive and remote method of individual fish identification using fish skin patterns, which can serve as a substitute for the common invasive fish tagging. The lateral images of the whole fish body on the homogenous background for Sumatra barb, Atlantic salmon, Sea bass, Common carp and Rainbow trout are available with automatically extracted parts of the fish with skin patterns. A different number of individuals (Sumatra barb – 43, Atlantic salmon – 330, Sea bass – 300, Common carp – 32, Rainbow trout - 1849) were photographed by the digital camera Nikon D60 under controlled conditions. The photographs of only one side of the fish with several (from 3 to 20) repetitions were taken. Common carp, Rainbow trout and Sea bass were photographed out of the water. Atlantic salmon was photographed underwater, out of the water, and the eye of the fish was photographed by the microscope camera. Sumatra barb was photographed under the water only. For all species, except Rainbow trout, the data collection was repeated after a different period (Sumatra barb – four months, Atlantic salmon – six months, Sea bass – one month, Common carp – four months) to collect the data for a study of skin patter changes (aging). The development of the method for photo-based individual fish identification was performed on all datasets. The identification accuracy for all species for all periods was 100% using the nearest neighbour classification. Different methods for skin pattern parametrization were used. </p> <p>The dataset can be used to develop remote and non-invasive individual fish identification methods. The studies focused on the discrimination power of the skin pattern can benefit from it. The changes of skin patterns due to fish aging can be explored from the dataset.</p>
Can cryptic female choice prevent invasive hybridization in external fertilizing fish?
<p>Polyandrous mating systems result in females mating with multiple males, generating opportunities for strong pre-mating and post-mating sexual selection. Polyandry also creates the potential for unintended matings and subsequent sperm competition with hybridizing species. Cryptic female choice allows females to bias paternity towards preferred males under sperm competition and may include conspecific sperm preference when under hybridization risk. The potential for hybridization becomes particularly important in context of invasive species that can novelly hybridize with natives, and by definition, have evolved allopatrically. We provide the first examination of conspecific sperm preference in a system of three species with the potential to hybridize: North American native Atlantic salmon (<em>Salmo salar</em>) and brook char (<em>Salvelinus fontinalis</em>), and invasive brown trout (<em>Salmo trutta</em>) from Europe. Using naturalized populations on the island of Newfoundland, we measured changes in sperm swimming performance, a known predictor of paternity, to determine the degree of modification in sperm swimming to female cues related to conspecific sperm preference. Compared to water alone, female ovarian fluid, in general, had a pronounced effect and changed sperm motility (by a mean of 53%) and swimming velocity (mean 30%), but not linearity (mean 6%). However, patterns in the degree of modification suggest there is no conspecific sperm preference in the North American populations. Furthermore, female cues from both native species tended to boost the sperm of invasive males more than their own. We conclude that cryptic female choice via ovarian fluid mediated sperm swimming modification is too weak in this system to prevent invasive hybridization and is likely insufficient to promote or maintain reproductive isolation among the native North American species. </p>
Data for: Differential habitat use of a notorious invasive fish, the round goby, in a translocation-relevant system
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Ecological performance of native and invasive benthic freshwater fishes under elevated temperature
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