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Fig. 6. nMDS analysis during high waters and low waters. a and b in Stability and spatio-temporal structure in fish assemblages of two floodplain lagoons of the lower Orinoco River

Fig. 6. nMDS analysis during high waters and low waters. a and b = gill nets sampling; c and d = seine net sampling. Each symbol represents one sample, filled symbols belongs to Las Arhuacas (arh) and those of open symbols to Los Cardonales (car). The dissimilarity between the sampling is approximately proportional to the distance, that is to say to greater distance greater dissimilarity. The abbreviations of the habitats are explained in the Fig. 2.

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Fig. 2 in Stability and spatio-temporal structure in fish assemblages of two floodplain lagoons of the lower Orinoco River

Fig. 2. Percentage distribution abundance and biomass of fish by habitats in each hydrological phase in both lagoons. DW = Descent water, LW = Low water, RW = Raise water and HW = High water. RO = Rocky outcrops, FGF = Flooded grass fields, FF = Floodplain forests, B = Beach, AV = Aquatic vegetation, LZFT = Littoral zone with fallen trunks and LZOW = Littoral zone and open waters.

Fig. 2 in Fish larvae assemblages in two floodplain lakes with different degrees of connection to the Paraná River, Brazil

Fig. 2. Larvae abundances for the different species in Xambrê Lake (a) and Saraiva Lake (b) in Ilha Grande National Park, upper Paraná River, during the three studied spawning seasons.

Fig. 5 in Fish larvae assemblages in two floodplain lakes with different degrees of connection to the Paraná River, Brazil

Fig. 5. Sample scores of retained axes (Axes 1, 2, and 3) from the non-metric multidimensional scaling (NMS) controlling for sites (S1 - Saraiva channel, S2 - Saraiva middle, X1 - Xambrê stream and X2 - Xambrê middle) (a; b) and spawning seasons (I, II and III) (c; d). Variation of mean scores axis for sites (e) and spawning seasons (f) in Ilha Grande National Park, upper Paraná River (s.d. = standard deviation).

Fig. 1 in Influence of environmental parameters on fish assemblage of a Neotropical river with a flood pulse regime, Central Brazil

Fig. 1. Study area located in the lower section of the Mortes River, Bananal floodplain, Central Brazil. The boldface numbers correspond to the stretches sampled.

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Fig. 1 in Influence of environmental variables and anthropogenic perturbations on stream fish assemblages, Upper Paraná River, Central Brazil

Fig. 1. Locations of the sampled sites (dots) in the streams of the Ouvidor River, Goiás State, Brazil. Squares indicate the main cities.

Fig. 4 in Fish larvae assemblages in two floodplain lakes with different degrees of connection to the Paraná River, Brazil

Fig. 4. Variations in mean species richness (number of species) (a), evenness (E) (b) and Shannon Diversity Index (H') (c) of fish larvae per sampling for Xambrê Lake and Saraiva Lake sites (S1 - Saraiva channel, S2 - Saraiva middle, X1 - Xambrê stream and X2 - Xambrê middle) in Ilha Grande National Park, upper Paraná River, during the three studied spawning seasons (s.d. = standard deviation).

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Fig. 4 in Fish assemblages in stream stretches occupied by cattail (Typhaceae, Angiospermae) stands in Southeast Brazil

Fig. 4. (a) Ordination resulting from Nonmetric Multidimensional Scaling Analysis (NMDS) with percent composition by number of feeding items from fishes of six stream stretches (S1-S6) in the dry and wet periods. (b, c, d) Contribution (the larger the circle, the greater the percent composition by number) of Ceratopogonidae larvae (b), Coleoptera larvae (c), and Collembola (d) to the fishes' diet. A stress of 0.08 corresponds to a good ordination with no real prospect of a misleading interpretation (Clarke & Warwick, 2001).

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Fig. 2 in Fish assemblages in stream stretches occupied by cattail (Typhaceae, Angiospermae) stands in Southeast Brazil

Fig. 2. (a) Dendrogram showing species composition similarity among six stream stretches sampled in the dry and wet periods (Jaccard coefficient and UPGMA). (b) Dendrogram showing quantitative similarity among six sampled streams in the dry and wet periods (Bray-Curtis coefficient and UPGMA).

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Fig. 3 in Fish assemblages in stream stretches occupied by cattail (Typhaceae, Angiospermae) stands in Southeast Brazil

Fig. 3. Representation the two first axis of the Canonical Correspondence Analysis, showing the sampled stretches (labelled S1-S6) in the dry and wet periods (circles), species (triangles), and environmental descriptors (arrows). The eigenvalue of axis 1 and axis 2 are 0.26 and 0.16, respectively, displaying 38% of the total inertia (= weighted variance) in the abundances and 68.8% of the variance in the weighted averages and class total of species with respect to the environmental variables. Monte Carlo significance test (4.999 permutations) under the full model option indicate that canonical axes are marginally significant ("F-ratio" = 1.509, P-value = 0.09). To species codes see Table 3.

Fig. 1 in Effects of tourist visitation and supplementary feeding on fish assemblage composition on a tropical reef in the Southwestern Atlantic

Fig. 1. Non-Metric Multi-Dimensional Scaling (MDS) plot of fish assemblages samples of the Picãozinho reef in each of the two studied situations. Dark triangles = PT (presence of tourists) and light triangles = AT (absence of tourists).

Fig. 2 in Comparison of fish assemblages in two littoral habitats in a Neotropical morichal stream in Venezuela

Fig. 2. Non-multi-dimensional scaling (MDS) ordination depicting similarity/dissimilarity of fish assemblages from flooded vegetation (open triangles) and sand bank habitats (inverted closed triangles). Each symbol represents one sampling site. Relative distance among symbols represents the relative similarity/dissimilarity of assemblage composition from the site based on presence/absence data.

Fig. 1 in Comparison of fish assemblages in two littoral habitats in a Neotropical morichal stream in Venezuela

Fig. 1. Location of Caño La Guardia in the southwestern Apure State, Venezuela (Sampling sites are shown by black dots).

Fig. 4 in Diet seasonality and food overlap of the fish assemblage in a pantanal pond

Fig. 4. Niche breadth values to fish assemblage in the Sinhá Mariana pond (Mato Grosso State, Brazil) using Levin's stan- dardized index, during rainy and dry seasons.

Fig. 5 in Diet seasonality and food overlap of the fish assemblage in a pantanal pond

Fig. 5. Values of trophic niche breadth (mean ± standard error) of fish species in the Sinhá Mariana pond (Mato Grosso State, Brazil) during rainy and dry seasons.

Fig. 2 in Simple relationships to predict attributes of fish assemblages in patches of submerged macrophytes

Fig. 2. Correlation coefficients (Pearson's R) obtained from relationships between fish assemblage attributes (a: density; b: species richness) and habitat variables (macrophyte biomass, BIOM; volume, VOL; proportional volume, %VOL). We show correlation results from all patches (All), patches dominated by E. densa and patches dominated by E. najas. All correlations were statistically significant (p <0.05).

Fig. 3 in Diet seasonality and food overlap of the fish assemblage in a pantanal pond

Fig. 3. Dendrogram of diet similarity of the fish assemblage in the Sinhá Mariana pond (Mato Grosso State, Brazil) showing the trophic guilds during rainy (A) and dry (B) seasons. Abbreviations of the species names are showing in table 1.

Fig. 2 in Diet seasonality and food overlap of the fish assemblage in a pantanal pond

Fig. 2. Water level in the in the studied region, Sinhá Mariana pond, Mato Grosso State, Brazil, from March/2000 to February/2001, showing the wet and dry seasons. These dates were provided by Agência Nacional de Águas (ANA).

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Fig. 4 in Fish assemblage structure in tributaries of the Meia Ponte River, Goiás, Brazil

Fig. 4. Mean scores of detrended correspondence analysis (DCA), controlling for seasons (rainy and dry) and positions (upper, intermediate and lower) (a = Axis 1; b = Axis 2).