Large freshwater migratory fish species commonly require complex habitats to complete their life cycle (Winemiller, 2005). These species have been increasingly affected by anthropogenic impacts, mainly river damming promoted by hydropower plants (Agostinho et al., 2007). Rivers formatted by a cascade of reservoirs are particularly harmful for long-distance migratory fish (Pelicice et al., 2018), once they can reduce or even prevent migration during downstream-upstream movements (Khedkar et al., 2014; Pelicice et al., 2015). Dams can cause substantial disruption to river systems and fish communities (Dudgeon et al., 2006; Vörösmarty et al., 2010) by fragmenting and reducing available habitat for local populations. This scenario favors a reduction of the effective population size, an increase in the genetic drift and inbreeding, and a consequent genetic diversity reduction (Yamamoto et al., 2004; Bessert, Ortí, 2008). Genetic diversity has been recognized as one of the three major levels of biodiversity (McNeely et al., 1990). It constitutes a primordial material for evolutionary change over time, and it is fundamental for species adaptation and conservation (Meffe, 1990; Carroll, Fox, 2008; Allendorf et al., 2013). Therefore, the species persistence depends on the ability of its populations to adapt in response to anthropogenic and habitat disturbances (Oro, 2020).
Natural populations are dynamic systems and the life-history of a given species has a great influence on both the genetic diversity level and its spatial distribution (Selander, Kaufman, 2012). Freshwater migratory fish species, for example, have been frequently associated with a panmictic population model, showing high genetic diversity distributed in a single large population (Sivasundar et al., 2001; Garcez et al., 2011; Aguirre-Pabón et al., 2013; Ferreira et al., 2017). However, this is not a general rule, and in several case studies, the genetic diversity has been shown partitioned in the structured population (e.g., Hatanaka et al., 2006; Sanches et al., 2007). Different mechanisms, such as isolation by space associated to the presence of physical barriers (Sekine et al., 2002) or homing behavior (Batista, Alves-Gomes, 2006; Carvajal-Vallejos et al., 2014), and isolation by time during spawning season (Braga-Silva, Galetti Jr., 2016; Ribolli et al., 2017), can lead to population structuring indeed.
Since hydropower dams can have a huge influence on long-distance migratory fish, we hypothesized that a reduction in the genetic diversity across a longitudinal down to upstream gradient along a dammed river would occur, as well as higher inbreeding rates in populations from fragmented and isolated river stretches. To test both hypotheses, we adopted as a study model the long-migratory fish Salminus brasiliensis (Cuvier, 1816), inhabiting the Middle and Upper Uruguay River. This rheophilic fish, known as Dourado or “river king”, is an important fishery resource for the local communities of the Upper Uruguay River, where the reduction in fishing catches, probably due to human impacts, such as fragmentation, habitat reduction and overfishing, have already been reported (Schork, Zaniboni-Filho, 2017).
Overall, we used microsatellite markers to assess contemporary genetic diversity and population structure for S. brasiliensis populations from dammed and non-dammed river stretches. Microsatellites have been widely spread used for genetic studies, and they have already been successfully used to evaluate the impact of fragmentation on connectivity among fish populations (Valenzuela‐Aguayo et al., 2020). We also simulated future scenarios to evaluate the long-term viability of the species. We expect that populations located in a river stretch free of anthropic fragmentation will present higher contemporary genetic diversity and greater long-term viability in comparison with the populations from the dammed upstream river stretches.
Material and methods
Study area. The Uruguay River is the youngest watershed of the major La Plata basin and is mainly covered with Precambrian and Paleozoic rocks of the Brazilian Shield (Albert, Reis, 2011). This geological formation distinguishes the Upper Uruguay from the other rivers of the La Plata basin, running in a valley embedded without marginal lagoons, with a series of pools and rapids, standing out two important geographical features. The ancient Augusto César Gorge canyon (popularly known as “step ant”; Fig. 1A), situated in the upper section, was flooded by the reservoir of the Itá hydroelectric dam in 1999; and the Yucumã (or Moconá) falls, located in the upper boundary of the middle section of the Uruguay River, dropping of 12 m and forming waterfalls with approximately 1800 m long, the widest in South America (Fig. 1B) (Zaniboni-Filho, Schulz, 2003).
The geological formation of the Upper Uruguay River has high hydroelectric potential, and currently, the main river course is fragmented by four large hydroelectric dams: Barra Grande (completed in 2005), Machadinho (completed in 2002), Itá (completed in 2000), and Foz do Chapecó (completed in 2010), while Middle Uruguay still presents dam-free stretches of the river (Fig. 1).
Sampling. We collected 108 adult individuals of S. brasiliensis at five distinct areas (Fig. 1): downstream Barra Grande dam and upstream Machadinho dam (Pop1 – sampled between 2003–2012, n = 12); upstream Itá dam and downstream Machadinho dam (Pop2 – 2006–2011, n = 29); downstream Itá and upstream Foz do Chapecó dam (Pop3 – 2010–2011, n = 23); downstream Foz do Chapecó and upstream Yucumã falls (Pop4 – 2010–2011, n = 25); and downstream Yucumã falls (Pop5 – 2010–2011, n = 19). In each sampling year, fish samples were collected throughout the year (not considering reproductive season or floods and droughts periods). Sampling was mostly conducted using hooks and long lines. The fish were not anesthetized for collection in the field because after removing the fin fragment, the individuals were immediately released into the river. Few individuals were caught using gill nets and were discarded when dead or kept as voucher. Voucher of S. brasiliensis from the Upper Uruguay River was deposited in the fish collection of Museu de Zoologia da Universidade Estadual de Londrina, Brazil (MZUEL 15570). Fragments of the caudal fin were removed, identified, and preserved in 95% ethanol.
FIGURE 1| Study area of Salminus brasiliensis populations in the Uruguay River basin, southern Brazil. A. Picture of Canyon Agusto César Gorge, Upper Uruguay River (acquired rights); B. Picture of Yucumã our Moconá Falls (google font: https://7mar.com.ar/mocona). Salminus brasiliensis (personal picture).
DNA isolation and microsatellite amplification. Total DNA was obtained from caudal fin clips following a salt extraction method (Aljanabi, Martinez, 1997). Polymerase chain reactions (PCR) were performed using eleven polymorphic microsatellite loci [Sfra02, Sfra10, Sfra13, Sfra03, Sfra04, Sfra18, Sfra14, Sfra05, Sfra15 (Rossini et al., 2011), Sh05 (Silva, Hilsdorf, 2011), and BoM2 (Barroso et al., 2003)]. PCRs were carried out following the M13-labelled primer protocol (Schuelke, 2000), in 10 µL mixes containing 30 ng of template DNA, 1X of GoTaq® Colorless Master Mix 2X (Promega); 8 pmol of M13 primer with FAM, TET or HEX label; 8 pmol of forward primer and 2 pmol of reverse primer (this latter with an M13 sequence tail). PCR conditions used 5 min at 94°C, followed by 35 cycles of 45 sec at 95°C, 45 sec at the original primer annealing temperature (Barroso et al., 2003; Rossini et al., 2011; Silva, Hilsdorf, 2011), and 45 sec at 72ºC; 10 cycles of 30 sec at 94°C, 45 sec at 53°C; and a final cycle of 10 min at 72°C. Genotyping was carried out in a MegaBace 1000 automatic sequencer (GE Healthcare Life Science), and alleles were scored using Fragment Profiler Software Suite v1.2 (GE Healthcare Life Science) with ET-ROX 550-R (size standard between 50 and 550 bp).
Genetic diversity analysis. All genetic diversity analyses were carried out within and between the five sampled populations (Pop1, Pop2, Pop3, Pop4, and Pop5), representing the scenario of river stretches as population groups. By creating pooled samples by river stretch, our aim was to assess the genetic diversity of populations from dammed riverscape without connections, which would allow gene flow events. Null alleles, allelic dropout, and stuttering were investigated using Micro-Checker v2.3 (Van Oosterhout et al., 2004). The number of alleles per locus (A), expected (He), and observed (Ho) heterozygosity, effective number of alleles (Ae), and deviations from Hardy-Weinberg equilibrium (HWE) were calculated in GenAlex v6.5 (Peakall, Smouse, 2012), adjusting for significance with sequential Bonferroni corrections (Rice, 1989). Linkage disequilibrium (LD) between pairs of loci was computed in Genepop v1.2 (Raymond, Rousset, 1995). Inbreeding coefficient (FIS) (Weir, Cockerham, 1984) and allelic richness (Ar; Leberg, 2002) were performed in FSTAT v2.9 (Goudet, 2001). The linkage disequilibrium method and parametric confidence intervals based on the chi-square approximation (Waples, 2006) were implemented in the analysis with a minimum allele frequency of 0.05 and without frequency restriction (data not shown).
The contemporary effective population size (Ne) for each population was estimated from data on Linkage Disequilibrium (LD) using the NeEstimator 1.31 software (Do et al., 2014). Considering that Ne can be underestimated when sample size is small and/or uneven (Waples, 2006; Peel et al., 2013), we standardized the sample size up to 30 individuals for all populations, using the Hybridlab software (Nielsen et al., 2006). This software creates new individuals (genotypes) randomly based on the allele frequencies within each sampled population, and it has been used to simulate new individuals for conservation management (Castilho et al., 2012; Yokogawa et al., 2013).
In addition, we simulated the effects of hypothetical population bottleneck scenarios on the genetic diversity in the future using the BOTTLESIM 2.6 software (Kuo, Janzen, 2003). Selection, migration, and mutation are not included in the simulation model (Kuo, Janzen, 2003). The only evolutionary force considered is genetic drift, an appropriate assumption for populations located between dams or natural barriers. Despite this limitation, the method has been used as a conservation approach for the most diverse taxa (Lippé et al., 2006; Moraes et al., 2017; Reid-Anderson et al., 2019; Dai et al., 2020). We estimated the genetic diversity through the estimated effective number of alleles and estimated expected heterozygosity of S. brasiliensis for the next 100 years. Using both the allelic frequency data and the empirical population size (Ne), we ran simulations with 100%, 75% and 50% of the empirical population size retained.
The scenarios used the following parameters: completely overlapping generations (100%); reproductive system (dioecious); expected longevity of the organism (11 years; Winemiller, Rose, 1992); age of reproductive maturation (two years; Barbieri et al., 2000); empirical population size (using a standardized sample size N = 30 by simulating new individuals for each population; Pop1 = 160, Pop2 = 108, Pop3 = 740, Pop4 = 260, Pop5 = 526; Tab. 1); time frame to simulate (100 years); and the number of iterations (1,000).
Population structure analysis. Spatial population genetic structure of S. brasiliensis was investigated using the Bayesian clustering STRUCTURE v.2.3.3 software (Pritchard et al., 2000; Falush et al., 2003). The admixture model with correlated allele frequencies was used without specifying sampling locations. The model was run with the likely number of clusters (K) ranging from 1 to 9, in a total of ten repetitions, using a burn-in period of 200,000 iterations followed by 600,000 Markov Chain Monte Carlo (MCMC) iterations. The optimal value of K was selected following Evanno et al. (2005), and the STRUCTURE bar plot was visualized by using the webapp (http://pophelper.com) POPHELPER.
Genetic differentiation was assessed by the FST index (Weir, Cockerham, 1984) between pairs of sampled populations using Arlequin v3.11 (Excoffier et al., 2005) and sequential Bonferroni corrections (Rice, 1989). We calculated the FST index between populations sampled upstream and downstream the Augusto César Gorge canyon, as well between upstream and downstream the Yucumã waterfall, for investigating the influence of these geographical barriers on the genetic structure. Analysis of Molecular Variance (AMOVA), also implemented in Arlequin v3.11, was conducted to check the existence of the partition of variance among groups and populations.
Population structuring between sampled populations was also assessed by Discriminant Analysis of Principal Components (DAPC), a multivariate method designed to identify and describe clusters of genetically related individuals. This tool allows the identification of genetic clusters and gives us a graphical representation of between-group structures to disentangle complex population structures, which may not be evident in other methods (Jombart et al., 2010). The DAPC analysis was performed using the adegenet package (Jombart et al., 2008), implemented in the R software (R Development Core Team, 2017).
Genetic diversity analysis. All 11 microsatellite loci were highly polymorphic with a mean number of alleles varying from 9.3 (Pop1) to 14.4 (Pop2 and Pop3) (Tab. 1). Mean Ho ranged from 0.754 (Pop1) to 0.896 (Pop3), while He ranged from 0.817 (Pop1) to 0.848 (Pop2), effective number of alleles from 6.1 (Pop1) to 9.5 (Pop2), and allele richness ranged from 8.1 (Pop 1 and Pop4) to 8.3 (Pop2, Pop3 and Pop5). No linkage disequilibrium among loci within populations was detected (data not shown). Pop1 and Pop2 showed positive values of inbreeding coefficient (FIS, 0.078 and 0.198, respectively), indicating a homozygous excess in these populations located upstream of the stretch studied; distinctly to the populations situated downstream (Pop3, Pop4, and Pop5), that exhibited negative FIS values (-0.075 to -0.030). Initially Pop1 showed negative Ne values due to the small sample size (data not shown); however, after standardizing all sample size (N = 30) using the Hybridlab software, the Ne ranged from 108.1 to 740.6 (Tab. 1). The infinite values were observed in the upper interval in Pop3, Pop4 and Pop 5, probably due to very large Ne (Waples, Do, 2010).
The simulated scenarios of population bottleneck (75 and 50% of the current population size; Fig. 2) showed loss of genetic diversity (Ae) in the population located in the uppermost portion of the dam cascade system (Pop1 and Pop2). Of note, the He retained did not reach values below 80% of the current genetic diversity (represented by 100%). The Ae reduction was faster than He and, in the worst scenario (Pop2 with 50% of Ne reduction), the Ae retained reached in 100 years values smaller than 60% of the current genetic diversity. We observed an intense decline of genetic diversity in the sampled populations located in the uppermost portion of the cascade systems (Pop1 and Pop2), and Pop4.
Population structure analysis. Bayesian clustering analysis without prior information separated the group of individuals in two genetic clusters (K = 2; S1); one formed by individuals from Pop1 and Pop2, and the other composed by Pop3, Pop4 and Pop5 (Fig. 3A). This same population structuring pattern with these two principal genetic clusters was also detected by the DAPC analysis (Figs. 3B,C). AMOVA analysis revealed that 97.2 % of the total genetic diversity occurred within individuals, while 1.90 % of the total variation occurred among sampled populations. We detected an identical divergence among sampled populations, with significance FST values between Pop1 vs. Pop3, Pop4 and Pop5, and Pop2 vs. Pop3, Pop4 and Pop5 (Tab. 2). The pairwise divergence between individuals from Pop1+Pop2 vs. Pop3+Pop4+Pop5 showed significant genetic differentiation (FST = 0.030, P < 0.05).
TABLE 1 | Summary of genetic diversity estimates in Salminus brasiliensis based on eleven microsatellite loci. N: samples size; A: mean number of alleles; Ae: No. of effective alleles; Ar: allelic richness; Ho: observed heterozygosity; He: expected heterozygosity; FIS: population inbreeding coefficient; Ne: effective population size (using a standardized sample size (N = 30) by simulating new individuals for each specific population); Inf: infinite.
Ne (range; 95% CIs)
FIGURE 2| Predicted genetic diversity in Salminus brasiliensis populations with distinct fragmentation levels over the next 100 years. Using BOTTLESIM 2.6, we estimated the retained percentage of effective number of alleles (Ae) and expected heterozygosity (He) under 100%, 75% and 50% of retain bottleneck scenarios. In all populations, the current population size is unable to maintain 80% of current genetic diveristy, which it is indicated by a red line.
TABLE 2 | Pairwise genetic distance, FST in populations of Salminus brasiliensis based on eleven microsatellites. Values in bold indicate significant differences.
(Pop1 + Pop2)
(Pop3 + Pop4 + Pop5)
FIGURE 3| A. Salminus brasiliensis population structure from the Bayesian cluster analysis for K = 2 (see also S1). Black lines separate the different sampled populations based on location (Pop1, Pop2, Pop3, Pop4 and Pop5; Fig. 1). B. DAPC scatterplots and membership probabilities show the first two principal components of the DAPC. Populations are represented in different colors: 1 – Lilac (Pop5); 2 – Green (Pop4), 3 – Orange (Pop3), 4 – Lilac (Pop2) and 5 – Brown (Pop1). C. Membership probabilities (in bar plots), represent individuals in different clusters.
Our results suggest that genetic diversity loss is quite inevitable in S. brasiliensis inhabiting the Uruguay River, and that it may compromise the viability of the fragmented populations isolated by dams in the uppermost portion of this hydrographic system in 100 years. It is believed that when conservation of endangered wild population is focused, the goal is retaining at least 80–90% of the initial genetic diversity over 100 years (Grueber, Jamieson, 2008; Corti et al., 2011; Shivaprakash et al., 2014). Our simulated scenarios of population bottleneck showed that lesser values of genetic diversity (Ae) will be reached in the populations located in the uppermost portion of the dam cascade system (Pop1 and Pop2). Although the He retained in 100 years was always above 80% of the current genetic diversity (represented by 100%), these results do not represent a signal of population persistence in future scenario, since after a population bottleneck He decays slower than Ae (Frankel, Soulé, 1981; Allendorf et al., 2013).
It is already recognized that anthropic fragmentation limits gene flow between populations and decreases population size. As a result of this population bottleneck, genetic diversity decreases, compromising the population viability (Frankham et al., 2010). While the river fragmentation by damming constitutes a major threat to global freshwater species diversity in the world (Dudgeon et al., 2006; Arthington et al., 2010; Vörösmarty et al., 2010), little is known on its long-term genetic consequences within and between populations of migratory fish (Baggio et al., 2018). The approach presented here allows us to infer on the genetic diversity changes over 100 years, corresponding to approximately 50 generations of S. brasiliensis.
This observed reduction on the genetic diversity seems to be directly connected with river fragmentation and its known consequences, e.g., reducing migration routes, habitat change, reduction of living area, and reduction of effective population size and gene flow (Esguícero, Arcifa, 2010). Our results suggested that S. brasiliensis populations possibly will experience different levels of impacts due to the river fragmentation. Both populations (Pop1, Pop2) sampled in the upper part of the Uruguay River will possibly suffer a higher impact over time, showing lower genetic diversity and high inbreeding than the populations located more downstream. This inference is especially valid for Pop1 and Pop2, and it can be directly associated to their living area. Inhabiting the uppermost river stretch, limited by two adjacent dams and lacking large tributaries (this stretch is enclosed in a valley, and the tributaries are short and have many waterfalls; Zaniboni-Filho, Schulz, 2003; Silva et al., 2012; Fig. 1), appears as the worst conditions for spawning and recruiting of new individuals. It is quite probable that our reduced sampling of Pop1 is already a consequence of this river fragmentation. This whole picture may explain the lower contemporary genetic diversity (A = 6.1) observed and the most unfavorable scenarios obtained in the future simulations for this population (Fig. 2).
On the other hand, the remaining populations (Pop3, Pop4, Pop5) located downstream Itá dam presented the best scenario for maintaining genetic viability in the long term, representing the healthiest populations in this study. However, the future scenario for Pop3 may be overestimated, since the presence of Foz do Chapecó dam, which started operation in 2010 (the same year of our Pop3 sampling), can restrict gene flow among downstream populations, and reduce genetic diversity of Pop3. Located in the most downstream river portion sampled, Pop5 inhabits a dam-free stretch of the Middle Uruguay River, within the Turvo State Park, and it is a stretch that still has the original characteristics of the river (Zaniboni-Filho, Schulz, 2003), with large spawning and recruiting areas for fish (Ziober et al., 2015; Reynalte-Tataje et al., 2020). It is the sampling area with the least anthropic impact (e.g., land use, such as cities, agriculture, and livestock) of all rivers stretches studied. Populations with a larger number of individuals have higher genetic diversity and, consequently, better chances of surviving anthropic actions and environmental changes (Vrijenhoek et al., 1985). The other sampled populations showed an intermediate reduction in genetic diversity in the long-term, particularly evaluated by the alleles number. Although long-term viability was simulated using the Ne with infinite values and in some populations that could indicate low precision and accuracy (e.g., sampling errors or a low number of markers; Waples, Do, 2010), these values can also be associated with large populations (Hare et al., 2011; Waples et al., 2018), and many of the theoretical models in population genetics assume an infinite population size (Allendorf, Luikart, 2009). Large populations are observed in freshwater fish (Garcez et al., 2011; Souza-Shibatta et al., 2018), as may be the case with these Salminus brasiliensis populations.
It appears that the long-term survival of S. brasiliensis populations in the Upper Uruguay River will largely depend on the effectiveness of protected areas in supporting viable populations, as represented by the downstream populations, which can serve as genetic stocks to help replenish upstream populations, that will have their genetic diversity reduced over the years. Previous ichthyoplankton studies within the site inhabited by Pop2 identified only three spawning events of S. brasiliensis, along nine years of monitoring, associated with a higher frequency of rain during spring and summer (Reynalte-Tataje et al., 2012). The presence of dam-free tributaries, as the Ligeiro River, offers lotic environments that allow the spawning of migratory fish, contributing to the viability of its population (Reynalte-Tataje et al., 2012).
The population genetic structure analyses revealed the occurrence of spatially structured genetic populations of S. brasiliensis in the upper portion of the Uruguay River basin. Individuals inhabiting upstream Itá dam (Pop1 and Pop2) were genetically differentiated (FST = 0.030, P < 0.05) from those sampled downstream (Pop3, Pop4 and Pop5). Higher levels of genetic differentiation are not expected among populations of migratory fish, often showing lower values (FST < 0.05; Wright, 1978) of genetic differentiation (Lopes et al., 2007; Braga-Silva, Galetti Jr., 2016; Ribolli et al., 2017). However, despite being the oldest hydroelectric plant along the Upper Uruguay River, Itá HPP had its gates closed in 1999, and our fish sampling occurred only seven to 12 years after the damming. It is not expected that a short period would be enough for promoting a fish population structuring due to the dam presence (Bessert, Orti, 2008). However, it is well known that the Itá dam replaced the Augusto César Gorge canyon (Fig. 1), completely flooded by the Itá reservoir. We suggest that this canyon could have represented a semi-permeable physical barrier, mainly during the dry seasons, facilitating the genetic differentiation between up and downstream populations related to the canyon. Nowadays, this semi-permeable canyon was replaced by the dam, an impassable barrier. In contrast, the Yucumã waterfall,believed to represent a temporary obstacle for fish migrating (Zaniboni-Filho, Schulz, 2003), seems not to lessen gene flow between downstream (Pop5) and upstream (Pop4) S. brasiliensis populations. Thus, the spatial population structuring of S. brasiliensis between the middle and upper portion of the Uruguay River appears to be only due to the ancient canyon’s presence. A fish community study conducted in this area, before the Itá dam construction, also revealed differences in the fish communities inhabiting up and downstream this canyon (Meurer, 2010). It reinforces the idea that the ancient canyon represented a last natural barrier for the free movement of fish. Therefore, this differentiation is relevant and could be amplified over the years due to presence of both Itá and Machadinho dams, which disrupted the connectivity between downstream (Pop3, Pop4, Pop5) and upstream (Pop1, Pop2) populations, and between Pop1 and Pop2. It reinforces the use of each sampled population in simulated future scenarios.
In summary, our results show that river fragmentation by damming can have a significant impact on the population viability of the migratory fish S. brasiliensis. The maintenance of viable populations of this large emblematic fish will at least partially depend on the populations living in non-anthropized areas, serving as stocks of genetic diversity that can be used for mitigation measures, such as restocking in fragmented and isolated populations. Considering the life history of S. brasiliensis and the fragmentation of habitat caused by the Upper Uruguay River’s cascade system, the future scenario is of collapse mainly for the uppermost populations. Additionally, we highlight the importance of maintaining river stretches without dams, as observed in the Middle Uruguay River, which allows the long-term maintenance of migratory fish populations. This approach, applied for the first time for Neotropical migratory fish, can be used for rheophilic species that inhabit the large and fragmented rivers of South America, and contribute for conservation of these fishes.
This work was due to SISBIOTA – Top predator network (Conselho Nacional de Desenvolvimento Científico e Tecnológico, CNPq 563299/2010–0, and Fundação de Amparo à Pesquisa do Estado de São Paulo, FAPESP 2010/52315-7). JR thanks Coordenação de Aperfeiçoamento de Pessoal de Nível Superior, CAPES (PDSE – 1592/81–2). JR and CBM thank PNPD/CAPES (Finance code 001). EZF, PDF and PMGJ thank CNPq (302860/2014–2, 304477/2018–4, 303524/2019–7, respectively). We are grateful to Pedro Iaczinski for help in collecting biological material. This study was carried out under permit and guidelines of the Animal Care Protocol PP00788 of Universidade Federal de Santa Catarina (UFSC).
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 Programa de Pós-Graduação em Ecologia e Recursos Naturais, Universidade Federal de São Carlos, Rodovia Washington Luís km 235, 13565-905 São Carlos, SP, Brazil. (JR) firstname.lastname@example.org (corresponding author).
 Laboratório de Biologia e Cultivo de Peixes de Água Doce, Departamento de Aquicultura, Universidade Federal de Santa Catarina, Rodovia SC 406 km 3, 3532, Lagoa do Peri, 88066-260 Florianópolis, SC, Brazil. (EZF) email@example.com.
 Laboratório de Biodiversidade Molecular e Conservação, Departamento de Genética e Evolução, Universidade Federal de São Carlos, Rodovia Washington Luís km 235, 13565-905 São Carlos, SP, Brazil. (CBM) firstname.lastname@example.org; (TCSG) email@example.com; (PDF) firstname.lastname@example.org; (PMGJ) email@example.com.
Josiane Ribolli: Conceptualization, Data curation, Formal analysis, Investigation, Methodology, Supervision, Validation, Writing-original draft, Writing-review and editing.
Evoy Zaniboni-Filho: Conceptualization, Funding acquisition, Investigation, Project administration, Supervision, Writing-review and editing.
Carolina Barros Machado: Conceptualization, Formal analysis, Methodology, Software, Validation, Writing-review and editing.
Tailise Carolina de Souza Guerreiro: Conceptualization, Formal analysis, Methodology, Software, Writing-review and editing.
Patrícia Domingues de Freitas: Investigation, Project administration, Supervision, Writing-review and editing.
Pedro Manoel Galetti Jr: Conceptualization, Funding acquisition, Project administration, Resources, Supervision, Writing-review and editing.
This study was carried out under permit and guidelines of the Animal Care Protocol PP00788 of Universidade Federal de Santa Catarina (UFSC).
The authors declare no competing interests.
How to cite this article
Ribolli J, Zaniboni-Filho E, Machado CB, Guerreiro TCS, Freitas PD, Galetti Jr PM. Anthropogenic river fragmentation reduces long-term viability of the migratory fish Salminus brasiliensis (Characiformes: Bryconidae) populations. Neotrop Ichthyol. 2021; 19(2):e200123. https://doi.org/10.1590/1982-0224-2020-0123
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Diversity and Distributions Published by SBI
Submitted October 30, 2020
Accepted April 22, 2021 by Elizete Rizzo
Epub July 05, 2021