The fish fauna from the Lower Iguaçu River and tributaries upstream of the Iguaçu Falls, the last free-flowing river stretch, were investigated. Twenty five sites in tributaries and the main channel were sampled between 2010 and 2016 using several kinds of fishing gear. The species were categorized according to their size, origin, and conservation status. Species richness and abundance in the main channel and tributaries were compared. In total, 87,702 specimens were recorded, comprising 76 species, 25 families, 53 genera, and eight orders. Characiformes and Siluriformes were the richest orders, representing 92% of the total specimens; Characidae, Cichlidae, Pimelodidae, and Loricariidae were the richest families. The fish fauna was composed of small and medium-sized species and included endemic (42%), autochthonous (24%), allochthonous (21%), and exotic (9%) species, as well as hybrids (4%). Significant differences in the relative numerical abundance of species were found among sites. Ancistrus mullerae and Rhamdia branneri (endemic) were indicator species for tributaries inside of Iguaçu National Park (INP), while Phalloceros harpagos (autochthonous) and Ictalurus punctatus (exotic) for tributaries outside of INP and Odontesthes bonariensis (allochthonous) for the main channel. The last dam-free stretch of the Lower Iguaçu River and tributaries upstream the Iguaçu Falls exhibits a rich endemic fish fauna, including some rare, endangered species (Steindachneridion melanodermatum, Gymnogeophagus taroba, and Psalidodon gymnogenys). These findings are essential to predict and understand the effects caused by the new Baixo Iguaçu Hydroelectric Power Plant and highlight the importance of tributaries and Iguaçu National Park for conservation of endemic species.

Abundance, fish, origin, richness, size, threats, updated list

The high diversity of species in the Neotropical region is recognized worldwide. This region currently has more than 5,160 species of freshwater fish and may have as many as 9,000 species (Reis et al. 2016). Three large freshwater basins dominate the South American continent: Amazon, Orinoco, and Paraná-Paraguay (Reis et al. 2016). The Paraná-Paraguay basin represents the third most diverse freshwater basin in South America (Reis et al. 2016), and within it, the Iguaçu River is renowned for its peculiar geomorphological and ichthyofaunal characteristics (Baumgartner et al. 2012).

Endemism is a well-recognized feature of the Iguaçu river basin (Baumgartner et al. 2012), which has led to its classification as a distinct ecoregion for freshwater fish conservation (Abell et al. 2008). This unique fauna arose from the isolation of this basin caused by the formation of the Iguaçu Falls some 22 million years ago (Oligo-Miocene period) (Severi and Cordeiro 1994). Currently, approximately 127 species of fish are known from the Iguaçu river basin (Reis et al. 2020). Many of these species have been described in the last decade, although taxonomic problems remain (Baumgartner et al. 2012), indicating that the diversity may be underestimated.

The main anthropogenic threats to fish fauna are habitat loss and environmental degradation. Specifically, damming rivers for hydroelectric power generation and water diversion for irrigation, as well as extensive changes in land use for agriculture and urbanization, are the main drivers of habitat loss (Reis et al. 2016) and the leading causes of the loss of biodiversity (Carvalho et al. 2019; Teresa and Casatti 2017). Therefore, it is essential to identify species, understand their distribution, and mitigate threats.

The topographic relief of the Iguaçu river basin has been a major attraction for hydroelectric projects. There are now five large reservoirs and several small ones, which have changed the natural landscape and stream habitats in the basin (Baumgartner et al. 2012). The last dam-free stretch of the Iguaçu River is 190 km in length and extends downstream from Salto Caxias dam to the Iguaçu Falls and encompasses Iguaçu National Park (INP), a world heritage site. However, in 2013, construction began on the sixth hydroelectric power plant, the Baixo Iguaçu Hydroelectric Power Plant (HPP) about 30 km downstream of the Salto Caxias dam and 500 m upstream from the mouth of the Gonçalves Dias River, which forms the boundary of INP. INP is one of the few remaining areas of Atlantic Forest protected by law. Although this hydroelectric plant project is very controversial due to its possible impacts on the region and particularly on INP, its operation started in 2019. Worryingly, the Baixo Iguaçu HPP potentially could be source of threats to the fish fauna, especially endemic species both inside and outside the INP (UNESCO 2012; Assumpção et al. 2017; Delariva et al. 2018).

The demand for electricity has grown in recent decades. To supply this demand in Brazil, most of needed electricity comes from hydroelectric plants (Kliemann and Delariva 2015; Makrakis et al. 2019). The extensive water network favors the implementation of hydroelectric projects, from small and medium-sized plants to large ones, but these projects directly change the physical and abiotic characteristics of aquatic ecosystems (Barbosa et al. 1999; Pelicice et al. 2018) and their fauna. Among the adverse effects is the profound change in river hydrology, which alters the structure of the fish fauna by fragmenting habitat, restricting dispersal of fish, decreasing the diversity of microhabitats and the supply of resources, and preventing movements of migratory species (e.g., Agostinho et al. 2007). Effects on the trophic structure of fish are already known on the Iguaçu River at the Salto Caxias HPP (Delariva et al. 2013) and Salto Segredo HPP (Mise et al. 2013). Although these effects are recognized, cascade hydroelectric projects have become increasingly common in Brazilian rivers (Santos et al. 2018).

Changes in land use have also negatively affected the biodiversity of fish in the Lower Iguaçu river basin (Larentis et al. 2016; Delariva et al. 2018), and the Iguaçu River is also recognized as the second most polluted river in Brazil (Bueno-Krawczyk et al. 2015; IBGE 2015). This pollution originates mainly from industrial and domestic sewage of urban areas in the Higher Iguaçu region (Bueno-Krawczyk et al. 2015) and from contamination by pesticides using in agriculture in the middle and lower portions of the basin (Nimet et al. 2017; Neves et al. 2018). These threats can lead to species extinctions and changes in the distinct structure of the fish fauna, whose evolutionary and biogeographic history is still not well understood. Therefore, it is essential to study the fish fauna prior to additional anthropogenic threats to assess the state of this ecosystem’s conservation.

This study provides an ichthyofaunistic inventory of the last free-flowing river stretch of the Lower Iguaçu River. This area is poorly studied and may be affected by the construction of a new hydroelectric power plant near Iguaçu National Park. While a previous inventory has been carried out in the river mostly upstream of the Salto Caxias Dam (Baumgartner et al. 2012), our study was based on a wider spatial-temporal scale, and intense sampling efforts include areas not yet sampled downstream of this dam. The 190 km stretch of the Iguaçu River and its tributaries exhibits a diverse landscape, and includes the area protected within INP, including a pristine river, areas at the INP border, and anthropogenic areas. We compare the composition, richness, frequency, and numerical abundance of species in tributaries and the main river channel. We describe the relative numerical abundance of species according to their biogeographic origins among the sites. We determine fish species indicative for the main channel, as well as tributaries inside and outside of INP. The results contribute to the knowledge of the basin’s fish fauna, including important information on the biogeographic origins and conservation status of the species. Our new data are an important contribution to the conservation and sustainable management of the last free-flowing stretch of the Lower Iguaçu River and mitigate future anthropogenic threats to this river’s fish fauna.

A total of 87,702 specimens were recorded, comprising 76 species, 25 families, 53 genera, and eight orders (Fig. 2; Table 2). The richest orders were Siluriformes and Characiformes, with 28 and 27 species, respectively (Table 2). Together these two orders represent approximately 92% of all species collected (Fig. 2a). Characidae (13 species), Cichlidae (11 species), and Loricariidae (nine species) were the families with the greatest richness (Table 2). However, Characidae, Cichlidae, and Pimelodidae are the most abundant families and comprising approximately 80% (Fig. 2b). Seven species were identified to only the genus level: Apteronotus sp., Characidium sp., Crenicichla sp., Heptapterus sp., Hoplias sp. 1, Hoplias sp. 2, and Pariolius sp.

Figure 2. 

Relative numerical abundance of fish orders (A) and fish families (B) recorded between 2010 and 2016 in the Lower Iguaçu river basin, Brazil.

Species richness was greater (76 species) at sites in the tributaries than in the main channel (58 species). The tributaries with the highest species richness were T9 (62 species) and T4 (58 species). Species richness was less in T7 (39 species). Eighteen species were caught only in tributaries. The following species had a restricted occurrence: Heptapterus sp. in T2, Leiarius marmoratus in T4, Poecilia reticulata in T5, Pareiorhaphis cf. parmula and Crenicichla tapii in T6, Crenicichla tuca in T7, and Hypophthalmichthys nobilis in T9. In the main channel, the greatest species richness was at C2 (46 species) and the lowest at C4 and C5 (40 species each). The hybrid Piaractus mesopotamicus × P. brachypomus had restricted capture in the main channel (C3). The most frequent species at all sampling sites (main channel and tributaries) were Psalidodon bifasciatus (21%), Bryconamericus ikaa (11%), and Pimelodus britskii (10%).

The fish fauna was characterized chiefly by small and medium-sized species (74% of total numerical abundance; Table 2), represented mainly by Psalidodon bifasciatus (24%), P. gymnodontus (13%), and B. ikaa (9%). Nineteen large species were shared between the main channel and tributaries, with P. britskii (71%) being the most frequent and Steindachneridion melanodermatum the rarest (Table 2). Some large species were recorded only in the tributaries: Ctenopharyngodon idella, Megaleporinus piavussu, and Pseudoplatystoma corruscans.

On the biogeographic origin of the species in terms of richness, 42% are endemics, 24% autochthonous, 21% allochthonous, 9% exotic, and 4% hybrids. In terms of abundance, endemic and autochthonous species represented 92% of the total abundance (54% and 38%, respectively). In general, the most frequent endemic species were B. ikaa (10.83%), P. britskii (10.12%), and P. gymnodontus (7.68%). Psalidodon bifasciatus (20.71%) was most frequent autochthonous species, Astyanax lacustris (6.69%) the most frequent allochthonous species, Oreochromis niloticus (0.09%) and Coptodon rendalli (0.07%) the most frequent exotic species, and Pseudoplatystoma corruscans × P. fasciatum (<0.001%) was the most frequent hybrid (Table 2).

The results of the GLMMs indicated that the relative numerical abundance of allochthonous (F = 2.54; p = 0.007), autochthonous (F = 3.80; p = 0.0001), and endemic (F = 4.30; p < 0.0001) species differed among sites (Table 3; Fig. 3). For exotic species and hybrids, there were no significant relationships with sites (F = 1.32; p = 0.23; F = 0.97; p = 0.49, respectively). The main channel (C1 and C4) and tributaries (T2, T3, T4, T6, and T9) were the sites related with higher abundance of endemic species. In addition, C1, C4 and tributaries (T3, T6, and T9) also related to a great abundance of autochthonous species, and the main channel (C1 and C4) and tributaries outside of INP (T4 and T5) were most abundant in allochthonous species. Despite non-significant results, exotic and hybrid species were also richer and highly abundant in the tributaries, especially in those areas outside of INP, and in areas with intense urban and agricultural activities (Fig. 3; Table 2). The indicator species analysis (Table 4) showed that, among the 76 species considered, only a few species were significantly related with biogeographic origin: O. bonariensis (allochthonous) was an indicator species of the main channel, P. harpagos (autochthonous) and I. punctatus (exotic) were indicator species of tributaries located outside of INP, and A. mullerae (endemic) and R. branneri (endemic) were indicator species of tributaries inside INP.

Figure 3. 

Richness (%, A–C) and relative numerical abundance (B–D) of fish species according to the origin (AL: allochthonous; AU: autochthonous; END: endemic; EX: exotic; HY: hybrid) recorded between 2010 and 2016 in the tributaries (C, D) and main channel (A, B) Lower Iguaçu river basin, Brazil.

Three Endangered (EN) species were sampled in low abundance (<1%) (Table 2): Psalidodon gymnogenys, captured at most sites in the tributaries and the main channel but especially at C1 (0.38%); Steindachneridion melanodermatum, captured at T4, T6, and T9 in the tributaries but principally in the main channel at C1 (0.07%), and Gymnogeophagus taroba, captured widely in the study but especially at T9.

This study is the first ichthyofaunistic survey carried out on a dam-free stretch of the Iguaçu River and its tributaries between the Salto Caxias Dam and the Iguaçu Falls. The number of identified species accounted for 72% of the number of species observed in a previous study for the Lower Iguaçu basin (Baumgartner et al. 2012), of which seven species had not been recorded (Schizodon borellii, Charax stenopterus, Leiarius marmoratus, Poecilia reticulata, Crenicichla lepidota, C. tapii, and C. tuca). Other species identified only to genus level still have unresolved taxonomy (Apteronotus sp., Characidium sp., Heptapterus sp., Hoplias sp. 1, Hoplias sp. 2, and Pariolius sp.). These results are important, as the stretch of river studied by Baumgartner et al. (2012) was over 250 km long and included five reservoirs upstream of our study area. The high species richness we found may be due, in part, to the unprecedent collections within a conservation area, the INP.

The richness and abundance of Siluriformes and Characiformes species were higher than those of other orders, both in the Iguaçu River and in its tributaries. Similarly, the same pattern was pointed out by previous studies along the Lower Iguaçu river basin: in reservoirs (Baumgartner et al. 2006), in rivers (Bifi et al. 2006), and in streams (Sereia et al. 2017; Delariva et al. 2018). This pattern in the Iguaçu river basin demonstrates a trend in many Neotropical watersheds, as observed by Lowe-McConnell (1999).

Small water bodies are as refuges for small species and provide a greater diversity of food resources from riparian vegetation and a larger diversity of microhabitats (Castro and Polaz 2020). Our study finds a more remarkable small-bodied species richness in tributaries than in the main channel. Additionally, the results of GLMM also showed the tributaries importance for conserving endemic species, both outside of (T2, T3, T4, T9) and inside INP (T6). The autochthonous Pareiorhaphis cf. parmula and C. tapii were recorded only in tributaries within INP (T6), which suggests the park’s role in the conservation of the fish fauna. Other species also had restricted capture in tributaries, but outside INP: the autochthonous Heptapterus sp. (T2), the allochthonous P. reticulata (T5), and L. marmoratus (T4), and the exotic Hypophthalmichthys nobilis (T9), indicating that tributaries without the protection afforded by being outside of the INP are more susceptible to anthropic threats.

Other small species, mainly belonging to the genera Astyanax, Psalidodon, and Crenicichla, occurred at all sampling sites. These species are generalists with high trophic plasticity, favoring their wide distribution within the basin and in varied habitats (Pini et al. 2019; Delariva and Neves 2020; Kuhn et al. 2020). Some Astyanax species were described in the last decades (Alcaraz et al. 2009; Garavello and Sampaio 2010), but taxonomic relationships and the identity of some of these remains uncertain (Rossini et al. 2016), caused by phenotypic plasticity (Pavanelli and Oliveira 2009), which will require full taxonomic review.

The introduction of species is among the leading causes of species extinction in worldwide (Matthews 1998), and this problem has already been highlighted in the Lower Iguaçu river basin. The transfer of these species to the Iguaçu basin has multiple reasons but may be a result of commercial and sport fishing (using live bait), aquaculture, fish stocking, and aquarium fish release (Garavello et al. 1997; Daga et al. 2016; Larentis et al. 2019). The exotic P. reticulata was recorded only in the Monteiro River (T5), whose basin is highly impacted by the urbanization of the city Capitão Leonidas Marques near the sampling site. Allochthonous species were also recorded elsewhere in the Iguaçu river basin, such as in the Segredo reservoir (Garavello et al. 1997) and the Salto Osório reservoir (Baumgartner et al. 2006), where the migratory P. lineatus was introduced. The allochthonous Astyanax lacustris is commonly reported for the Upper Paraná river basin, and its introduction is uncertain.

Fish farms are potential sources of invasive species (Orsi and Agostinho 1999; Daga et al. 2016) and impact the basin (Agostinho et al. 1999). The capture of the allochthonous Salminus brasiliensis is due to escapes and releases, possibly originating from fish farms to increase sport fishing potential, as reported by residents in the region. Salminus brasiliensis is considered potentially invasive and can cause serious harmful effects to the ecosystem where it is introduced (Vitule et al. 2014). The exotic Tilapia species, Oreochromis niloticus and Coptodon rendalli, were probably escapes from fish farms. Tilapia culture already has an alarmingly poor record of high-risk invasions into natural environments (Frota et al. 2019). Records of introduced species were also found in Iguaçu reservoirs (Foz do Areia, Segredo, Salto Santiago, Salto Osório and Salto Caxias) where 20 species are known, with Tilapia being among the most common (Daga and Gubiani 2012). The presence of hybrids is associated with fish farming (Piaractus mesopotamicus × Colossoma macropomum, Piaractus mesopotamicus × Piaractus brachypomus, Pseudoplatystoma corruscans × Pseudoplatystoma fasciatum) (Valladão et al. 2018).

Due to their multiple uses of water, the implementation of hydroelectric projects has also been associated with facilitating the introduction and dissemination of exotic species (Agostinho et al. 1999). In addition, changes in the river’s physical and chemical characteristics promote non-measurable pressure on fish fauna, especially for species with greater sensitivity and specific ecological requirements. Psalidodon gymnogenys, Steindachneridion melanodermatum, and Gymnogeophagus taroba, could be most severely affected as they are already Endangered (ICMBio 2018). Steindachneridion melanodermatum is the largest fish in the Iguaçu River. It is an endemic and possibly migratory (Agostinho and Gomes 1997; Ludwig et al. 2005; Brehm et al. 2016), living in fast-flowing, deep waters in stretches of the Iguaçu River and tributaries where the natural flow of water is still preserved (Garavello 2005). In addition to the losses of their habitat and connectivity caused by the successive hydroelectric dams, fishing also contributes to declines in this species population (Assumpção et al. 2017). Stocks of this species have been under pressure from prohibited fishing (Assumpção et al. 2021) and are a challenge to monitor because the species occurs in two countries (Brazil and Argentina), and the fishing is most intense on weekends and holidays (UNIOESTE 2017). The extinction of S. melanodermatum could harm other trophic levels as it is a top-of-the-chain species. Gymnogeophagus taroba, a species of fast waters (Paiz et al. 2017), is widely distributed in the studied area. However, with the construction of the new hydroelectric reservoir, the species can disappear in the flooded area, and its distribution can be fragmented, which will lead to loss of genetic diversity and a population decline (Souza-Shibatta et al. 2018).

The last dam-free stretch of the Lower Iguaçu River upstream of the Iguaçu Falls exhibits a rich endemic fish fauna, rare endangered species restricted to this region, and new species for science. This diversity is threatened with extinction by biotic and abiotic factors. Exotic species have occurred in low abundance, but their presence in most sampling sites and the Iguaçu National Park is worrisome, requiring actions to mitigate its harmful effects and to avoid new introductions. The presence of hybrids of allochthonous species escaped from fish farms requires strict supervision of these commercial operations. Another source of threats is the construction of the Baixo Iguaçu HPP, which will promote hydrological changes in the main channel and severe damage to many fish species. Thus, tributaries will play an essential role in maintaining the diversity of fish in the Iguaçu river basin since many species of the Iguaçu River also frequent in the tributaries, besides the species that occur only in these environments. The protection of free-flowing tributaries has been an appeal worldwide (Grill et al. 2019; Makrakis et al. 2019), as they support endangered species populations, provide various environmental conditions, access to spawning habitat, and refugia for early life stages (Silva et al. 2019). The correct identification of species and taxonomic research are also essential, as they will help the development of strategies for the management and conservation of environments (Assumpção et al. 2021). Thus, preserving the free stretch below the Baixo Iguaçu HPP to the Iguaçu Falls is crucially necessary and the last resource to conserve endemic and endangered species. In addition, to enable the management of ichthyofauna, efforts should be concentrated on monitoring populations.

We thank Consórcio Empreendedor Baixo Iguaçu for the financial support to the research. Suelen F.R. Pini was supported by a doctoral scholarship from CAPES (Coordination for the Improvement of Higher Education Personnel). Sergio Makrakis received a Productivity Scholarship in Technological Development and Innovative Extension from CNPq. All authors are grateful to the students of Grupo de Pesquisa em Tecnologia em Ecohidráulica e Conservação de Recursos Pesqueiros e Hídricos from the Unioeste and technicians from the Instituto Água Viva for the fieldwork and laboratory assistance.