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Figure 4 in Peculiarities of seasonal dynamics of net primary production and its microzooplankton grazing in the coastal waters of the Black Sea (Sevastopol region)

Figure 4. Seasonal dynamics of parameters: a – intensity of solar radiation (1) and water temperature (2), b – nitrates (1) and ammonium (2), c – silicates (1) and phosphates (2), c – net primary production (1) and chlorophyll a concentration (2) in station 2.

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Figure 3 in Peculiarities of seasonal dynamics of net primary production and its microzooplankton grazing in the coastal waters of the Black Sea (Sevastopol region)

Figure 3. Seasonal dynamics of parameters: a – relative biomass of diatoms (1) and weighted average volume of phytoplankton cells (2), b – relative biomass of dinoflagellates (1) and coccolithophores (2), c – molar ratios N/P (1) and Si/N (2), d – net phytoplankton growth rate (1) and ratio g/µ (2) in station 1.

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Figure 2 in Peculiarities of seasonal dynamics of net primary production and its microzooplankton grazing in the coastal waters of the Black Sea (Sevastopol region)

Figure 2. Seasonal dynamics of parameters: a – intensity of solar radiation (1) and water temperature (2), b – nitrates (1) and ammonium (2), c – silicates (1) and phosphates (2), c – net primary production (1) and chlorophyll a concentration (2) in station 1.

Fig. 2 in Temporal dynamics of species associations in the parasite community of European eels, Anguilla anguilla, from a coastal lagoon

Fig. 2. Intensity of infection (mean ± SE number of parasites per host, including infected hosts only) of the six most common helminth parasites of eels, Anguilla anguilla, in Comacchio Lagoons, during three sampling periods. Graphs on the right-hand side do not include the 2015–2017 period, as these species were not found during that period. See Table 1 for full species names.

Fig. 4 in Temporal dynamics of species associations in the parasite community of European eels, Anguilla anguilla, from a coastal lagoon

Fig. 4. Pairwise relationships between numbers of parasites per host for the three most common digenean parasites of eels, Anguilla anguilla, in Comacchio Lagoons, across all three sampling periods combined. The line represents the relationship (with 95% confidence intervals) predicted by the generalized linear model; see text. Tick marks indicate partial residuals with either positive (top) or negative values (bottom). See Table 1 for full species names.

Fig. 3 in Temporal dynamics of species associations in the parasite community of European eels, Anguilla anguilla, from a coastal lagoon

Fig. 3. Scatterplots of pairwise relationships between numbers of parasites per host for the three most common digenean parasites of eels, Anguilla anguilla, in Comacchio Lagoons, across all three sampling periods combined. See Table 1 for full species names.

Fig. 1 in Temporal dynamics of species associations in the parasite community of European eels, Anguilla anguilla, from a coastal lagoon

Fig. 1. Abundance (mean number of parasites per host, including non-infected hosts) of the six most common helminth parasites of eels, Anguilla anguilla, in Comacchio Lagoons, during three sampling periods: 2005–2006 (N = 140 eels), 2010–2013 (N = 131), and 2015–2017 (N = 30). Note that some values for the time period 2015–2017 are based on very few fish; see Table 1 for actual numbers and for full species names.

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Fig. 2 in Reptiles of Ecuador: a resource-rich online portal, with dynamic checklists and photographic guides

Fig. 2. Biogeographic regions of Ecuador. Source: https://bioweb.bio (modified from Sierra et al. 1999).

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Fig. 1 in Reptiles of Ecuador: a resource-rich online portal, with dynamic checklists and photographic guides

Fig. 1. Histogram showing the description of reptile species present in Ecuador through time, from Linnaeuss 10th edition of Systema Naturae to the end of 2018. The number of species described per decade is presented above each bar.

Figure 7 in Effect of environmental change after the 2011 tsunami on the population dynamics of Japanese tubesnout Aulichthys japonicus (Gasterosteiformes)

Figure 7. – Photographs showing scraped an ascidian Halocynthia roretzi (A) and an egg mass (B) of the Japanese tubesnout Aulichthys japonicus, which was spawned and developed within the ascidians.

Figure 4 in Effect of environmental change after the 2011 tsunami on the population dynamics of Japanese tubesnout Aulichthys japonicus (Gasterosteiformes)

Figure 4. – Relationship between the occurrence of larvae of Aulichthys japonicus collected from 2012 to 2013 and water temperature (°C).

Figure 3 in Effect of environmental change after the 2011 tsunami on the population dynamics of Japanese tubesnout Aulichthys japonicus (Gasterosteiformes)

Figure 3. – Monthly changes in the number of individuals for larva, juvenile and young Aulichthys japonicus and water temperature collected at the seagrass bed in Namiita beach in 2012.

Figure 6 in Effect of environmental change after the 2011 tsunami on the population dynamics of Japanese tubesnout Aulichthys japonicus (Gasterosteiformes)

Figure 6. – Changes in the surface of the seagrass bed area (m2) since before Tsunami (according to Yamaki, 2009) to 2014.

Figure 3 in Temporal dynamics of the recruitment of glass eels in two valleys of French Polynesia (Tahiti and Moorea Islands)

Figure 3. – Annual monitoring of glass eels recruitment for each of the three species in: A: Moorea; B: Tahiti; C: Moorea and Tahiti, given in number of specimens per month.

Figure 4 in Temporal dynamics of the recruitment of glass eels in two valleys of French Polynesia (Tahiti and Moorea Islands)

Figure 4. – Composition of the recruitment of Anguilla species from Moorea and Tahiti Islands given in percent; * test chiº, p-value <0.001.

Figure 5 in Temporal dynamics of the recruitment of glass eels in two valleys of French Polynesia (Tahiti and Moorea Islands)

Figure 5. – Mean length (in mm) of the glass eel specimens at recruitment, for the three species in Moorea and Tahiti islands; * test chiº, p-value <0.001.

Figure 5 in Effect of environmental change after the 2011 tsunami on the population dynamics of Japanese tubesnout Aulichthys japonicus (Gasterosteiformes)

Figure 5. – Changes of number of Japanese tubesnouts Aulichthys japonicus and ascidians Halocynthia roretzi from 2007 to 2008 and from 2012 to 2016.

Figure 1 in Effect of environmental change after the 2011 tsunami on the population dynamics of Japanese tubesnout Aulichthys japonicus (Gasterosteiformes)

Figure 1. – Location of study area in Okirai Bay and position of the sampling site in Namiita Beach. The white dotted area shows the seagrass bed's area (m2) in August 2014.

Figure 2 in Temporal dynamics of the recruitment of glass eels in two valleys of French Polynesia (Tahiti and Moorea Islands)

Figure 2. – Annual monitoring of glass eels recruitment in the Opunohu River on the Moorea Island and in the Vaituoru River on the Tahiti Island per year, given in number of specimens caught per day.