Journal of Fish Biology (2015) doi:10.1111/jfb.12734, available online at wileyonlinelibrary.com

Isotopic variation in five species of stream fishes under the influence of different land uses D. R. Carvalho*†, D. Castro‡, M. Callisto‡, M. Z. Moreira§ and P. S. Pompeu* *Laboratório de Ecologia de Peixes, Setor de Ecologia, Departamento de Biologia, Universidade Federal de Lavras, Campus Universitário, Caixa Postal 3037, CEP 37200-000, Lavras, MG, Brazil , ‡Laboratório de Ecologia de Bentos, Departamento de Biologia Geral, Instituto de Ciências Biológicas, Universidade Federal de Minas Gerais, Av. Antônio Carlos, 6627, Caixa Postal 486, Pampulha, CEP 30161-970, Belo Horizonte, MG, Brazil and §Laboratório de Ecologia Isotópica, Centro de Energia Nuclear na Agricultura - CENA, Universidade de São Paulo, Av. Centenário, 303, Caixa Postal 96, CEP 13400-970, Piracicaba, SP, Brazil (Received 2 December 2014, Accepted 19 May 2015) The aim of this study was to test if changes in land use alter the isotopic signature of fish species, promoting changes in the trophic position and food resource partitioning between these consumers. Three different systems were investigated: pasture streams (n = 3), streams in sugar cane plantations (n = 3) and reference streams (n = 3). Fish species Aspidoras fuscoguttatus, Astyanax altiparanae, Characidium zebra, Hisonotus piracanjuba and Knodus moenkhausii were selected, and their nitrogen and carbon isotopic compositions were estimated to assess changes in the trophic level and partitioning of food items consumed. The composition of 𝛿 13 C (‰) only differed among the land use categories for A. altiparanae, H. piracanjuba and K. moenkhausii. Resource partitioning was different for all species, with changes in the sources or proportions they consumed in each land use category, but only A. altiparanae introduced new food sources in large quantity in altered land uses. It is important to note, however, that the results from the resource partitioning analysis are limited due to large overlapping of isotopic signatures between the analysed food resources. All fish species exhibited variation in 𝛿 15 N (‰), with the highest values found in streams under sugar cane or pasture influence. Despite the variation in nitrogen isotopic values, only C. zebra and H. piracanjuba displayed changes in trophic level. Therefore, it is believed that the increase in the 𝛿 15 N (‰) value of the individuals collected in streams under the influence of sugar cane or pasture was due to the greater influence of livestock dung and chemical and organic fertilizers. The results also highlight the importance of studying consumer species along with all forms of resources available at each location separately, because the signatures of these resources also vary within different land uses. © 2015 The Fisheries Society of the British Isles

Key words: carbon; food resources; nitrogen; stable isotopes; trophic position; trophic webs.

INTRODUCTION Aquatic environments are altered by a variety of external factors, including those of natural origin, such as floods and droughts, and also by anthropogenic ones, such as †Author to whom correspondence should be addressed. Tel.: +55 35 3829 1201; email: deboracarvalhobio@ yahoo.com.br

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the construction of dams, urbanization, monoculture and pasture systems (Malmqvist & Rundle, 2002; Pompeu et al., 2005; Cunico et al., 2006; Barletta et al., 2010). In the Cerrado, which is the second major Brazilian biome, the main threats to biodiversity are related to two economic activities: intensive grain monoculture and extensive cattle ranching (Diniz-Filho et al., 2009). These two activities have great potential for altering aquatic communities because they may trigger a series of effects that adversely affect aquatic ecosystems. The replacement of native vegetation by pastures and monoculture systems has resulted in the reduction or even removal of riparian vegetation, which can directly affect the flow of carbon in aquatic environments (Silva et al., 2007). This substitution can also significantly alter the incidence of solar energy and the exchange of organic and inorganic material between aquatic and terrestrial ecosystems (Pusey & Arthington, 2003). Changes in riparian vegetation cover interfere with nutrient supply, allochthonous material, autochthonous production and the quality and quantity of available food resources, which may alter the trophic webs of affected environments and have an effect on aquatic biodiversity (Pusey & Arthington, 2003; Thomas et al., 2004; Meynendonckx et al., 2006; Ferreira et al., 2012). Thus, one way to observe the effects of anthropogenic changes on aquatic communities is to assess how fish respond to changes in the sources of available resources. Tropical freshwater fishes exploit food resources in a variety of ways, and many species can change their diet opportunistically in response to the relative abundance of food (Peterson & Winemiller, 1997; Abelha et al., 2001). This ability to take advantage of the food resources that are more abundant at any given time is characterized as trophic adaptability, and these changes in resource use can be temporary or permanent depending on the circumstances (Gerking, 1994). The capacity to exploit available resources will also vary according to the strategies adopted by each species, including generalist species (with no strong preference for a food resource, using a variety of resources), specialists (with a diet restricted to a relatively small number of items and usually presenting remarkable morphological adaptations) and opportunists (that feed on a resource that is not common to their diet or make use of an abundant and unusual food source) (Gerking, 1994). Another important factor is that the ability to change the sources consumed can result in changes in the trophic positions occupied by fishes. Most tropical species of fish alter their trophic position during ontogeny, and in the same populations, individuals may have food preferences or make use of different dietary tactics (Abelha et al., 2001). Thus, one way to observe the dynamics of aquatic communities is to estimate the positions occupied by stream fishes in trophic webs with different anthropogenic influences. Studies investigating the diet and feeding ecology of fishes are conducted primarily through stomach contents analysis (Pompeu & Godinho, 2003; Maroneze et al., 2011; Gandini et al., 2012). New approaches, however, such as the use of stable isotopes, allow for the quantification of the carbon sources effectively entering into a system (Forsberg et al., 1993; Benedito-Cecílio et al., 2000; Ferreira et al., 2012), in addition to determining the relative assimilation of some resources that are poorly quantified in the analysis of stomach contents, as is the case for detritus (Keough et al., 1998). The use of this tool has yielded progress in studies of aquatic environments, especially in trophic ecology studies, and carbon (13 C) and nitrogen (15 N) isotopes are the most commonly used isotopes (Jepsen & Winemiller, 2002; Hoeinghaus et al., 2007; Jardine,

© 2015 The Fisheries Society of the British Isles, Journal of Fish Biology 2015, doi:10.1111/jfb.12734

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2014). The transfer of the carbon isotope signature along the trophic web is conservative and can be used to trace the flow of energy in systems where there are several types of foods with different 13 C values (Jardine et al., 2003; Manetta & Benedito-Cecílio, 2003). The 15 N isotope, in turn, is consistently fractionated throughout the trophic web, allowing inferences about the trophic relationships of consumers with their diet (Vander Zanden et al., 1997; Post, 2002; Vanderklift & Ponsard, 2003). Therefore, these two isotopes are useful to trace the transfer of carbon and nitrogen from plants and detritus to primary and secondary consumers (Peterson & Fry, 1987; Ferreira et al., 2012; Jardine, 2014). Assuming that anthropogenic actions promote significant changes in the dynamics of energy flow in aquatic communities, the hypotheses that fishes exhibit different isotopic signatures of carbon and nitrogen in streams under influence of different land use were tested. Confirming this hypothesis, the aim becomes to assess whether some or all fish species display a similar trend and whether this could be accounted for by: (1) shift in the isotope ratios of resource or (2) utilization of a novel resource. The possible variation in the trophic level of each species between streams under the influence of different land uses was assessed. The isotopic composition of carbon and nitrogen of five fish species and the available food sources present in streams with different degrees of anthropogenic influence (streams with natural cover, streams under the influence of sugar cane cultivation and streams located in pastures) were used to detect possible changes in the consumption of food sources and to determine the trophic position of the consumers studied.

MATERIALS AND METHODS S T U DY A R E A A N D L A N D C O V E R C L A S S I F I C AT I O N This study was carried out in tributary streams of the São Simão reservoir, located in the sub-basin of the Paranaíba River, south-eastern Brazil. The Paranaíba River basin is the second largest hydrographic unit of the Paraná Basin, encompassing 25⋅4% of its area, which corresponds to a drainage area of 222⋅8 km2 , covering parts of the states of Goiás (65%), Minas Gerais (30%), Federal District (3%) and Mato Grosso do Sul (2%). Most parts of the Paranaíba River basin are located in Cerrado, the second largest Brazilian biome, but much of this area has been deforested as a result of anthropogenic activities. The hydrological regime of the rivers in this basin is governed by two seasons: rainy from October to March and with episodic rainfall in the remaining months of the year (CBH-Paranaíba, 2012). Nine second and third-order streams (located in the states of Goiás and Minas Gerais) were selected from 110 previously visited tributary streams of the São Simão reservoir (Fig. 1). The 110 sampling points were chosen according to the methodology proposed by Olsen & Peck (2008), in which points are defined by a spatially balanced and ranked selection algorithm. The nine streams were selected according to the different types of land use in which they were located, with three located in pastures and three in sugar cane cultivation areas. Three streams defined as reference streams were selected as controls for having representative riparian vegetation and good water quality (Brazilian Water Quality Resolution, CONAMA 357/2005, Brazilian National Environmental Council). The anthropogenic stream characteristics included the total absence (streams located in pastures) or low presence (streams with influence from sugar cane cultivations) of riparian vegetation. The land use surrounding the sampled streams was evaluated according the oriented mapping method described in Lima et al. (2010), in eight multi-spectral RapidEye images (https://apollomapping.com) between September and October 2011, with five spectral bands. The percentage of natural vegetation, pastures and plantations of sugar cane was determined for

© 2015 The Fisheries Society of the British Isles, Journal of Fish Biology 2015, doi:10.1111/jfb.12734

50° 15′

Quirinópolis

São Simão

Paranaiguara

50° 30′

Santa Vitória

Gouvelândia Ipiaçu

Inaciolândia

Gurinhatã

49° 45′

Bom Jesus de Goiás

Castelândia

50° 0′

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15

Ituiutaba

Capinópolis

0

Panamá

N

49° 15′

30 km

Cachoeira Dourada

49° 30′

Fig. 1. Locations of the nine tributary streams of the São Simão reservoir in the Paranaíba River basin where sampling was performed in September 2012 ( , study area ; , reservoir; , drainage; , cities; , pasture; , sugar cane; , natural cover. Geographic Projection Datum WGS-84. Cartographic Data: IBGE, 1979, 2000 Geominas, 2004; ANA, 2008.).

Paraná River basin

Minas Gerais State

São Simão Reservoir basin

São Simão Reservoir basin

Paraná River basin

Brazil

50° 45′ 18° 0′ 18° 15′ 18° 30′ 18° 45′ 19° 0′ 19° 15′

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the nine streams accordingly, in a 150 m radius buffer, around the upstream limit of the sampled stretch (Table I). Ortho-rectified and atmospherically corrected images were obtained through a partnership between the Federal University of Lavras (UFLA) and the Ministry of Environment (MMA). Acquisition errors, clouds and shadows were removed in the pre-processing phase (Coppin et al., 2004), which also included visual evaluation of image registration. To validate the results of the classification, an array of errors was generated, measuring the global and kappa accuracy (Shanmugam et al., 2006). Real field data collected in September 2012 were used to verify the accuracy of mapping. The mapping results in a high kappa and global accuracy with values of 96 and 98%. The length of the section sampled in each stream was proportional to its width, being defined as 40 times the mean width of the stream and encompassing a minimum of 150 m of sampling. Each stream was sampled (fishes and resources) and evaluated only once in the dry season, in September 2012. To illustrate the variation in the physical habitat of streams with different anthropogenic influences, environmental variables were quantified according to the protocols proposed by Lazorchak et al. (1998), and the metrics were calculated according to Kaufmann et al. (1999). In this study, the percentages of fine substrata, vegetation cover, rapid flow, algae, aquatic plants (macrophytes) and leaf banks were evaluated. These variables were assessed because they consistently reflected the effects of different land uses on the physical habitat of streams, especially with regard to the availability of resources (Table I).

C O L L E C T I O N A N D P RO C E S S I N G O F F I S H E S Fish collection was performed in the downstream–upstream direction with nets made with insect screen (80 cm in diameter, 1 mm mesh) and trawls (3 m long, 5 mm mesh). Each stream was subdivided into 10 sections for the collection of ichthyofauna, with a sampling time of 12 min per section, totalling 2 h of collection per stream. The collected samples were immediately killed and stored on ice for further processing in the laboratory and subsequent analysis of the isotopic composition. In the laboratory, the collected organisms were taxonomically identified with the aid of identification keys of Paraná Basin fishes. Adults individuals of the species Aspidoras fuscoguttatus Nijssen & Isbrücker 1976, Astyanax altiparanae Garutti & Britski 2000, Characidium zebra Eigenmann 1909, Hisonotus piracanjuba Martins & Langeani 2012 and Knodus moenkhausii (Eigenmann & Kennedy 1903) were selected. The factors that determined the choice of these five species are: (1) presence and abundance in all of the streams under the influence of the different land uses, (2) similar ontogenetic stage, (3) absence of migratory behaviour, (4) representation in different trophic guilds and (4) feeding in different positions in the water column (Table II). For larger specimens (>5 cm total length, LT ), such as A. altiparanae and C. zebra, a part of the muscle was removed for isotopic analysis. Smaller fishes (