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Figure 3 in A simplistic water body-specific risk assessment model for zebra mussel (Dreissena polymorpha) establishment based on physicochemical characteristics
Figure 3. Salinity-based zebra mussel establishment risk categorization of 133 Texas water bodies. Major water bodies not included in this study due to lack of TCEQ water quality data are shown for context of the study extent.
Figure 1 in A simplistic water body-specific risk assessment model for zebra mussel (Dreissena polymorpha) establishment based on physicochemical characteristics
Figure 1. Calcium-based zebra mussel establishment risk categorization of 85 Texas water bodies. Areas to the east of the Whittier et al. (2008) calcium risk delineation were predicted by that study to have ≤ 12 mg/l calcium (i.e., minimal establishment risk); this delineation is shown to demonstrate level of agreement with that study. Major water bodies not included in this study due to lack of TCEQ water quality data are shown for context of the study extent. The Cypress, Sabine, and Neches River basins referenced in the text are the three East Texas basins with predominantly minimal risk water body categorizations.
Figure 3 in Effects of temperature on mortality of quagga mussels (Dreissena bugensis) exposed to potassium chloride and copper-based molluscicides in high conductivity waters
Figure 3. Comparison of measured mortality for adult mussels exposed to copper at 10 °C and copper concentrations over time for Experiment 1b (A), which had 50% less biomass and lower mean specific conductivity than Experiment 4 (C) with log-logistic dose-response model fits. Colored bands are 95% confidence intervals and points are mortality values from replicate bioboxes. Measured copper concentrations in bioboxes for B) Experiment 1b and D) Experiment 4. Solid horizontal lines are target concentrations, dashed horizontal lines are mean concentration over the entire experiment duration.
Figure 2 in Effects of temperature on mortality of quagga mussels (Dreissena bugensis) exposed to potassium chloride and copper-based molluscicides in high conductivity waters
Figure 2. Measured mortality for adult mussels exposed to KCl at A) 10 °C, B) 18 °C, and C) 22 °C with log-logistic doseresponse model fits. Colored bands are 95% confidence intervals and points are mortality values from replicate bioboxes.
Figure 1 in Effects of temperature on mortality of quagga mussels (Dreissena bugensis) exposed to potassium chloride and copper-based molluscicides in high conductivity waters
Figure 1. Variation in specific conductivity in A) Lake Piru and B) control bioboxes within experimental periods. Specific conductivity from moderate conductivity Lake Ontario and Minnesota lakes (≈ 300 µS/cm; Moffitt et al. 2016; Luoma et al. 2018) is provided for reference.
Figure 5 in Effects of temperature on mortality of quagga mussels (Dreissena bugensis) exposed to potassium chloride and copper-based molluscicides in high conductivity waters
Figure 5. Comparison of measured mortality for adult mussels exposed to copper at 10 °C and copper concentrations over time for Experiment 1a (A), which received only a single dose of copper and Experiment 1b, which included refreshed copper treatments (C) with log-logistic dose-response model fits. Colored bands are 95% confidence intervals and points are mortality values from replicate bioboxes. Measured copper concentrations in bioboxes for B) Experiment 1a (without refresh) and D) Experiment 1b (with refresh). Solid horizontal lines are target concentrations, dashed horizontal lines are mean concentration over the entire experiment duration.
Figure 4 in Effects of temperature on mortality of quagga mussels (Dreissena bugensis) exposed to potassium chloride and copper-based molluscicides in high conductivity waters
Figure 4. Measured mortality for adult mussels exposed to copper (Earthtec QZ®) at A) 10 °C, C) 18 °C, and E) 22 °C with loglogistic dose-response model fits. Colored bands are 95% confidence intervals and points are mortality values from replicate bioboxes. Measured copper concentrations in bioboxes at B) 10 °C, D) 18 °C, and F) 22 °C. Solid horizontal lines are target concentrations, dashed horizontal lines are mean concentration over the entire experiment duration.
Figure 2 in Environmental DNA as a tool to help inform zebra mussel, Dreissena polymorpha, management in inland lakes
Figure 2. The mean number of cycles needed to detect DNA of zebra mussels from water samples collected at the surface, mid-column and bottom of Lake Minnetonka directly above a known zebra mussel population. A lower number of cycles indicates a greater amount of DNA. Bars represent the 95% confidence intervals.
Figure 3 in Environmental DNA as a tool to help inform zebra mussel, Dreissena polymorpha, management in inland lakes
Figure 3. Structural Equation Model for zebra mussels in two lakes near Alexandria, Minnesota: Lake Le Homme Dieu (A) and Maple Lake (B). Nodes are environmental DNA copy numbers of zebra mussel DNA (eDNA), habitat, depth, lake and ash-free dry weight (AFDW). AFDW is log(AFDW + 0.1). eDNA is log(copy number eDNA + 0.1). Numbers next to a line between two nodes represents the correlation between the two nodes. The r2 values in boxes correspond % variance of dependent variable explained by the independent variable. Values with an asterisk (*) indicate significant correlation between nodes. Our significance level was established at α ≤ 0.05.
Figure 4. A cove with shallow water near Ponte Porton with 14 in Populations of Microcondylaea bonellii (Férussac 1827), Unionidae - an european freshwater mussel at rapid decline - and Unio mancus in Istria, Croatia
Figure 4. A cove with shallow water near Ponte Porton with 14 individuals of Microcondylaea bonellii (26.9.2009).
Figure 3 in Populations of Microcondylaea bonellii (Férussac 1827), Unionidae - an european freshwater mussel at rapid decline - and Unio mancus in Istria, Croatia
Figure 3. Numbers of shells of Unio mancus (blue) and Microcondylaea bonelli at the different sites (red).
Fig. 2 and 3 in Populations of Microcondylaea bonellii (Férussac 1827), Unionidae - an european freshwater mussel at rapid decline - and Unio mancus in Istria, Croatia
Fig. 2 and 3 give the results of my surveys in river Mirna in 2009 to 2016. In the upper part of the river from the city of Buzet to the confluence with Butoniga the artificially straightened riverbed is dominated by coarse gravel and shows ± rapid current. Although Microcondylaea was recorded from this part of the river near Istarske Teplice (Fischer 1999) no shells or living specimens were found actually. Populations of Unio mancus were mainly found in tributaries like Bračana and drenches, less frequently in the riverbed of upper Mirna. Between 2009 and 2016 the Mirna-riverbed was reconstructed in several places, eroded banks with coves and fine sand substrate were replaced by blocks of stone and the riverbed straightened again. Thus many suitable habitats and eventually existing mussels-populations were destroyed, so much the worse as heavy machines were driving in the riverbed over many weeks for the construction works and mobilized the substrate, which led to high accumulations of fine sediment in the lower part of the river, especially in parts with low current and coves which were inhabited by Microcondylaea.
Figure 1 in Populations of Microcondylaea bonellii (Férussac 1827), Unionidae - an european freshwater mussel at rapid decline - and Unio mancus in Istria, Croatia
Figure 1. Map of known living populations of Microcondylaea bonelli in Slovenia (grey) and Italy (yellow) from http://art17.eionet.europa.eu/article17/reports2012/species/summary/. Populations in Croatia (red) added by the author.
Figure 10 in A taxonomic revision of fossil freshwater pearl mussels (Bivalvia: Unionoida: Margaritiferidae) from Pliocene and Pleistocene deposits of Southeastern Europe
Figure 10. Fossil-calibrated multi-locus ultrametric chronogram of the Margaritiferidae (after Lopes-Lima et al. (2018) with our additions). Bars indicate 95% confidence intervals of the estimated divergence times between lineages (Ma). Black numbers near nodes are mean ages (Ma). Stratigraphic chart according to the International Commission on Stratigraphy, 2015. Fossil species under discussion are in red. We illustrated a putative phylogenetic placement of fossil species, i.e. Pseudunio flabellatus (Goldfuss, 1837) comb. rev. as a stem lineage (MRCA of P. auricularius - P. homsensis clade) and P. flabellatiformis (Grigorowitch-Beresowski, 1915) comb. rev. as an extinct lineage (red branch with X-shaped terminal mark indicating an extinction event in the Late Pleistocene) related to P. auricularius and P. homsensis.
Figure 8 in A taxonomic revision of fossil freshwater pearl mussels (Bivalvia: Unionoida: Margaritiferidae) from Pliocene and Pleistocene deposits of Southeastern Europe
Figure 8. Teeth morphology of recent and fossil Pseudunio taxa: A) P. auricularius from the Indre River near Huismes commune, Loire Basin, France (SMF, voucher no. 307623); B) P. homsensis from the Nahr al-Kabir al-Janoubi River near Harida, Syria (SMF, voucher no. 83160); C) P. flabellatiformis comb. rev. from the Sucleia outcrop, paleoDniester River valley, Middle Pleistocene, Moldova (RMBH, voucher no. Sc1). Scale bars = 10 mm. Photos: Artem A. Lyubas and Ilya V. Vikhrev.
Figure 7 in A taxonomic revision of fossil freshwater pearl mussels (Bivalvia: Unionoida: Margaritiferidae) from Pliocene and Pleistocene deposits of Southeastern Europe
Figure 7. Shells of the recent Pseudunio homsensis (Lea, 1865): A) Orontes River near Homs, Syria (SMF, voucher no. 4450); B) Orontes River near Homs, Syria (SMF, voucher no. 345464); C) Orontes River near Homs, Syria (SMF, voucher no. 15263); D) Nahr al-Kabir al-Janoubi River near Harida, Syria (SMF, voucher no. 83160) E) Nahr al-Kabir al-Janoubi River near Tell Kalat, Syria (SMF, voucher no. 5156); F) Orontes River near Homs, Syria (SMF, voucher no. 4548). Scale bar = 20 mm. Photos: Ilya V. Vikhrev.
Figure 4 in A taxonomic revision of fossil freshwater pearl mussels (Bivalvia: Unionoida: Margaritiferidae) from Pliocene and Pleistocene deposits of Southeastern Europe
Figure 4. Subfossil shells of Pseudunio flabellatiformis (Grigorowitch-Beresowski, 1915) comb. rev. from the outcrop of the Middle Pleistocene riverine deposits near Sucleia village, paleo-Dniester River valley, Transnistria, Moldova: A) specimen no. 1 (RMBH); B) specimen no. Sc1 (RMBH); C) specimen no. Sc5 (RMBH); D) specimen no. Sc8 (RMBH); E) specimen no. Sc12 (RMBH); F) specimen no. Sc13 (RMBH). Scale bar = 20 mm. Photos: Artem A. Lyubas.
Figure 6 in A taxonomic revision of fossil freshwater pearl mussels (Bivalvia: Unionoida: Margaritiferidae) from Pliocene and Pleistocene deposits of Southeastern Europe
Figure 6. Shells of the recent Pseudunio auricularius (Spengler, 1793): A) Indre River near Huismes commune, Loire Basin, France (SMF, voucher no. 307623); B) Ebro River near Cenicero, La Rioja, Spain (MNCN, voucher no. 15.07/197); C) Loire River upstream of Champtoceaux commune, Maine-et-Loire, France (SMF, voucher no. 307850); D) Garonne River, France (MNCN, voucher no. 15.07/178); E) Indre River near Huismes commune, Loire Basin, France (SMF, voucher no. 307623); F) Ebro River near Amposta city, Tarragona, Spain (MNCN, voucher no. 15.07/10366). Scale bar = 20 mm. Photos: Artem A. Lyubas & Ilya V. Vikhrev.
Figure 5 in A taxonomic revision of fossil freshwater pearl mussels (Bivalvia: Unionoida: Margaritiferidae) from Pliocene and Pleistocene deposits of Southeastern Europe
Figure 5. Scatter plot of PCA based on the shell measurements of our Pseudunio sample from the Sucleia locality and the type series of fossil nominal taxa from the Speya and Blizhniy Khutor localities (Chepalyga, 1964, 1965). The component 1 and component 2 accounted for 98.8% and 1.0% of the total variance, respectively.
Figure 3 in A taxonomic revision of fossil freshwater pearl mussels (Bivalvia: Unionoida: Margaritiferidae) from Pliocene and Pleistocene deposits of Southeastern Europe
Figure 3. Distribution ranges of Pseudunio taxa. The range of each species is illustrated based on the corresponding river drainages: 1 – former range of P. auricularius based on fossil and recent records (Araujo and Moreno, 1999; Araujo and Ramos, 2001; Prie et al., 2018); 2 – range of P. homsensis based on recent records (Vikhrev et al., 2017); 3 – range of P. marocanus based on recent records (Lopes-Lima et al., 2018); 4 – former range of P. flabellatiformis with its synonyms (M. moldavica syn. nov., M. robusta robusta syn. nov., M. robusta speensis syn. nov., and M. robusta tirassica syn. nov.) based on fossil records (Bogatchev, 1961; Chepalyga, 1964, 1965, 1967; Bolotov et al., 2016). Stars indicate records of P. flabellatiformis from the Pliocene (blue) and Pleistocene (red) deposits of Southeastern Europe (Bogatchev, 1961; Chepalyga, 1964, 1965, 1967; Bolotov et al., 2016).
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Allen Brain Atlas
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DANDI Archive for NWB datasets
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International Brain Laboratory public data
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OpenNeuro
OpenNeuro is a free, open platform for sharing neuroimaging datasets, with public search, dataset pages, and download paths for web, S3, DataLad, and the OpenNeuro CLI.