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Brazilian Journal of Microbiology

Print version ISSN 1517-8382

Braz. J. Microbiol. vol.45 no.4 São Paulo Oct./Dec. 2014

http://dx.doi.org/10.1590/S1517-83822014000400019 

RESEARCH PAPER

 

Gram-negative intestinal indigenous microbiota from two Siluriform fishes in a tropical reservoir

 

 

Silvana DuarteI; Flávia Cristina de Paula e SilvaII; Danielle Alves Gomes ZauliII; Jacques Robert NicoliII; Francisco Gerson AraújoI

ILaboratório de Ecologia de Peixes, Universidade Federal Rural do Rio de Janeiro, Seropédica, RJ, Brazil
IIDepartamento de Microbiologia, Instituto de Ciências Biológicas, Universidade Federal de Minas Gerais, Belo Horizonte, MG, Brazil

Correspondence

 

 


ABSTRACT

The Gram-negative intestinal microbiota of Hypostomus auroguttatus and Pimelodus maculatus, a detritivorous and an omnivorous fish species, respectively, were compared between fishes from the reservoir and the stretch of the river below the dam of the Funil hydroelectric plant, Rio de Janeiro, Brazil. Four selective culture media were used under aerobic and two under anaerobic conditions. The omnivorous species had microbiota with higher population levels compared to the detritivorous species. The number of morphotypes and population levels of total bacteria, vibrio and Bacteroides tended to be higher in summer and autumn in the reservoir, and not different in the river. The number of morphotypes of enterobacteria and total bacteria were higher in the lotic environment compared with the lentic one. The bacteria Aeromonas hydrophila and Plesiomonas shigelloides and the obligate anaerobic Fusobacterium mortiferum were the most frequently identified microorganisms in the intestine of both H. auroguttatus and P. maculatus. Both season and habitat influenced the Gram-negative intestinal microbiota of H. auroguttatus and P. maculatus. Environmental factors influenced the Gram-negative intestinal microbiota of both species with possible impact on the interrelationship between the fishes and their digestive ecosystem, although the gut microbiota composition of fishes may result from host-specific selective pressures within the gut.

Key words: alimentary regimen, environment, gut microbiology, Hypostomus auroguttatus, Pimelodus maculatus.


 

 

Introduction

The gastrointestinal microbiota of fish consists of similar population levels of strict and facultative anaerobes that, similarly to other animal species, have three main functions: resistance to colonization by pathogens, modulation of the immune system and nutritional contribution for the host (Búcio et. al., 2006). In this sense, an optimization of the relationship between the host with its associated microbiota is fundamental for the preservation and maximal exploitation of the microbiota and its mentioned functions. Therefore, a thorough knowledge of the identity of the components of this microbiota as well as the mechanisms they use to carry out their functions are required.

The composition of the microbiota and its functions may change or be influenced by factors such as diet and environmental conditions (Ringo et al., 2001). Currently, a high amount of information about environmental influences on gut microbiota associated with human and some domestic (pigs and poultry) and laboratory (rats and mice) terrestrial animals is available (Ley, 2008, Bevins and Salzman, 2011) but less is known for aquatic animal species. Concerning fishes, there is also little information on the factors (nutritional, environmental and stress) that may influence the equilibrium population of the normal microbiota and consequently their functions.

The degree of contribution of the indigenous microbiota to the digestive physiology of their host depends on the diet, and also on the complexity and difficulty to use the nutrient ingested by the host. In this way, herbivorous and detritivorous fishes depend much more on their microbiota than omnivorous and carnivorous fishes (Prejs and Blaszczyk, 2006; Shangong et al., 2010). The need for microbial contribution is accompanied by the existence of a longer, more complex and compartmented gastrointestinal tract (fermentation chamber), generally developed during the co-evolutionary development process between the host and its microbiota (Seeto et al., 1996).

Although there is a reasonable amount of information on the influence of feeding habits on the intestinal microbial populations, little is known on the habitat influences (e.g., lotic vs. lentic) and seasonal changes. Most ecological and physiological processes are supposed to change according to these constraints, including the intestinal microbiota (Podkowa and Goniakowska-Witalinska, 2003). In a lentic system (reservoir), the environmental variables tend to change in a wider scale when compared to the more stable environmental conditions of a lotic system (river) (Soares et al., 2008). Moreover, most of the lentic systems tend to eutrophication as they become old and receive and accumulate organic loads. In contrast, the continuous and unidirectional water movement of a lotic system enables more stable environmental conditions and generally leads to better water quality due to its constant renovation (Klapper, 1998). Similarly, seasonality should also influence microorganisms in the environment and in the indigenous microbiota of fish, in particular because the effect of rainwater as a nutrient carrier. Finally, physical, chemical, and nutritional changes found in different ecological environments are expected to affect the type and population levels of microorganisms.

The armored catfish (Hypostomus auroguttatus, Kner 1854) is a benthic iliophagous/herbivorous species with ventral lips (oral papillae) adhering to the river bottom and feeding by grasping the plant organic matter and "microalgae film" associated to rocky substrate (Fugi and Hahn, 1991). Such characteristics are probably functionally related to the fact that individuals in this species have one of the largest intestines among the teleosteans, with some individuals of this species having intestines reaching about fifteen times their individual length (Duarte et al., 2013). This suggests the occurrence of a prolonged digestive process (Nelson, 2002) that might depend on the presence of microbiota.

The long-whiskered catfish (Pimelodus maculatus, Lacepède 1803) is also a benthic species, capable to perform limited reproductive seasonal migration to spawn (Dei Tos et al., 2002). It is an omnivorous species with tendency to carnivorous regimen, having an intestinal size of almost 1.5 times its total length (Lobón-Cerviá and Bennemann, 2000). Vaz et al. (2000) reported that P. maculatus feeds on larvae of benthonic insects, algae, mollusks, fish, and plant fragments, accumulating reserves to be used in gonad development along the maturation process during the summer.

In the present study, the influence of feeding habits (iliophagous/detritivorous vs. omnivorous), habitat (lentic vs. lotic) and seasonality on the number of morphotypes and the population levels of the Gram-negative digestive microbiota of two siluriform fishes (H. auroguttatus and P. maculatus) was evaluated. By examining such differences in gut bacteria of fish from different trophic levels, seasons and habitats, we investigated some factors that shape these communities. We expected that fish with different diets, especially those that are difficult to digest (as the case of H. auroguttatus), have been selected to harbour more bacterial communities with more number of morphotypes and population levels. We also expected, a priori, that those indicators of microbes community would differ among seasons and between the more stable lotic habitat and the more changeable conditions of the lentic habitat.

 

Materials and Methods

Study area

Built in 1969, the reservoir of the Funil hydroelectric plant (22°30' S, 44°45' W, altitude 440 m) is located in the middle section of the basin of the Paraíba do Sul river, within the Atlantic Forest biome of Southeastern Brazil (Figure 1). This reservoir is the largest artificial impoundment in the river, with an area of 40 km2, maximum depth of 70 m, and water retention time of 10-50 days (Carvalho and Torres, 2002).

 

 

The Paraíba do Sul river (PSR) basin drains a major industrialized area in Brazil and suffers several impacts along its extension, with the heaviest alteration occurring in the middle reaches, where a generalized pollution from organic and industrial effluents is observed due to poorly planned sewage municipal systems. The climate is subtropical with monthly mean water temperatures of 18-24 °C. Rainfall volume is higher in the summer months (December-January, 200-250 mm per month) and lower in the winter months (June-August, < 50 mm per month).

Funil reservoir has poor water quality. It receives large amounts of phosphorus during the increases inflow of the Paraiba do Sul river. Dissolved oxygen, pH, and chlorophyll a levels peaked in the wet season; pH, chlorophyll a, and total phosphorus in several cases were recorded above the recommended Brazilian guidelines (Branco et al., 2002). Dissolved oxygen was lower than acceptable levels in the euphotic layer and reached very low levels in the hypolimnion, indicating thermal stratification (Araújo et al., 2011). Ferrão-Filho et al. (2009) showed that the high input of N and P favored the persistent dominance of cyanobacteria; cyanobacteria included potential hepatotoxins (microcystins) producers like Microcystis spp., and potential neurotoxins (saxitoxins) producers like Anabaena circinalis and Cylindrospermopsis raciborskii. Funil Reservoir is a turbid (median euphotic zone = 4.3 m), eutrophic reservoir (median total phosphorus = 3.1 µM), with a high phytoplankton biomass (median chlorophyll-a concentration = 10.0 g L-1) (Branco et al., 2008).

Fish collection and sample handling

The fishes were collected from two habitats: the Funil reservoir (lentic habitat) and the stretch of the Paraíba do Sul downriver of the Funil dam (lotic habitat). Thirty adult individuals of H. auroguttatus averaging 242 ± 4.5 mm total length (TL) and 152 ± 11.6 g total weight (TW), and 28 adults of P. maculatus averaging 252 ± 5.4 mm TL and 184 ± 13.1 g TW were collected. Fish collection occurred in July (winter) and October (spring) 2003, and in January (summer) and April (autumn) 2004. Four sets of three gill nets (30 m long x 2.5 m height) with different mesh sizes (2.5, 4.5 and 6.5 cm stretched knots) were used to sample an area of ca. 900 m2. The nets were deployed near to the shoreline during the afternoon and retrieved in the following morning, fishing for approximately 15 h. Voucher specimens were deposited in the Fish Collection of the Laboratory of Fish Ecology, University Federal Rural of Rio de Janeiro, under numbers LEP-UFRRJ 996 and 997, for H. auroguttatus, and 998 and 999, for P. maculatus.

The specimens were transported alive to the laboratory and sacrificed by immersion in water at 4 °C associated with an anterior incision to remove their intestines in a laminar flow hood (Vecco, Campinas, Brazil). The contents from the distal portion of the intestine were weighed and immediately introduced into an anaerobic chamber (Forma Scientific Company, Marietta, U.S.A.) containing an atmosphere of 85% N2, 10% H2 and 5% CO2. Then, the intestinal contents were submitted to serial decimal dilutions from 10-2 to 10-9 in sterile saline, and a volume of 0.1 mL of each dilution was plated onto Petri dishes containing the following selective and universal culture media: blood agar supplemented with 0.5% yeast extract, 0.1% hemin and 0.1% menadione, and Bacteroides Bile Esculin (BBE) agar. Sequentially, the same dilutions were removed from the anaerobic chamber and a volume of 0.1 mL of each of them used to inoculate under aerobic conditions Petri dishes containing: blood agar; MacConkey agar (Difco, Sparks, U.S.A.); thiosulfate citrate bile sucrose (TCBS) agar (Oxoid, Basingstoke, U.K.); and YM agar. After incubation at 25 °C for 24-48 h and 7 days under aerobic and anaerobic conditions, respectively, determination of colony counts and number of different morphotypes as well as isolation of dominant microorganisms of the intestinal contents were performed using the appropriate dilution. Population levels were expressed as decimal logarithm of colony forming units per gram of contents (log10 cfu g-1).

For isolation, a sample of each different colony morphotype was inoculated in the same original culture medium and an aliquot submitted to microscopic observations after Gram staining. Each isolate was also submitted to a determination of the growth atmosphere (facultative anaerobe, obligate anaerobe, or microaerophilic). The definitive identification was completed with the results obtained from the following API identification kits (BioMérieux SA, Marcy-l'Étoile, France): 20 A for obligate anaerobes, 20 E for enterobacteria and other Gram-negative bacteria, and 20 AUX for yeasts. When necessary, supplementary biochemical or physiological tests were performed (catalase, indol, H2S production, esculin hydrolysis and carbohydrate fermentation).

Statistical significance of the results was evaluated by non-parametric Kruskal-Wallis and Mann-Whitney tests for comparing multiple independent samples among groups. The level of significance was set at p < 0.05. Statistical analyses were performed using the Statistic software v.7.1 (StatSoft, Inc., USA).

 

Results

Feeding habits

The number of morphotypes did not differ between the two fish species, with exception for the vibrio group that was significantly higher (H = 9.2, p < 0.05) for P. maculatus when compared to H. auroguttatus (Table 1). The highest number of morphotypes was noted for the enterobacteria group with a number of about 4 (3.9 ± 2.0) and 5 (4.7 ± 2.9) per fish for P. maculatus and H. auroguttatus, respectively.

On the other hand, population levels differed significantly between the two species for all bacterial groups, with significantly higher values for P. maculatus when compared to H. auroguttatus (p < 0.05). As expected for aquatic species, Gram-negative facultative anaerobes (enterobacteria group) represented the dominant populations in the intestines of both fishes with 7.2 ± 1.7 and 5.7 ± 1.7 log10 cfu g-1 of contents for P. maculatus and H. auroguttatus, respectively.

Seasons

Seasonal differences were found only for the number of morphotypes for H. auroguttatus in the reservoir (Table 2), with a trend for higher values in summer for total aerobes, vibrio (H = 8.0, p = 0.04) and Bacteroides (H = 8.0, p = 0.04) and in spring and autumn for total anaerobes (H = 10, p = 0.01) when compared with the other seasons. Population levels also differed only for the reservoir (Table 3), with higher values in summer for vibrio and total aerobes (H = 7.6, p = 0.05), and in summer and autumn for Bacteroides (H = 9.6, p = 0.02) when compared to other seasons.

No seasonal difference (Table 4) was found for the number of morphotypes for P. maculatus, except for vibrio (H = 8.0, p = 0.04) obtained from individuals collected in the reservoir, with significant higher values in summer when compared to other seasons. Population levels changed seasonally (Table 5), with higher values for enterobacteria (H = 8.4, p = 0.03) of fishes collected in the reservoir in winter when compared to the spring. For the river, comparatively higher values were observed for winter and spring when compared to summer and autumn for total anaerobes (H = 10.9, p = 0.01) and Bacteroides (H = 10.5, p = 0.01).

Habitats (lotic vs. lentic)

The number of morphotypes was significantly higher for H. auroguttatus from the river when compared to the reservoir only for enterobacteria (Table 2). On the other hand, no significant difference was found between the two systems for population levels of any of the bacterial groups (Table 3).

For P. maculatus, no significant differences in the number of morphotypes was found between the bacterial groups (Table 4), while the population level was significantly higher for the river compared with the reservoir for the vibrio group (Table 5).

Growth atmosphere requirements

The mean number of morphotypes of total aerobes was similar for both fish species and both habitats, ranging from 0.0 ± 0.0 in the river during spring to 4.3 ± 0.5 in the reservoir during summer for H. auroguttatus, and from 1.2 ± 1.1 in the river during spring to 4.0 ± 1.1 in the reservoir during autumn for P. maculatus (Tables 1, 2 and 4). The mean population levels of total aerobes for H. auroguttatus (4.7 ± 2.9) was significantly lower than for P. maculatus (6.3 ± 3.2 log10 cfu g-1; Table 1). There is a slight trend for higher values in the reservoir compared with the river for H. auroguttatus, whereas no difference in habitats were found for P. maculatus (Tables 1, 3 and 5).

In relation to the mean number of morphotypes for total anaerobes, the values were similar for both fish species and habitats, ranging from 2.5 ± 1.0 in the reservoir during winter to 6.2 ± 1.3 in the river during spring for H. auroguttatus, and from 2.0 ± 0.0 in the reservoir during autumn to 4.6 ± 0.5 in the river during spring for P. maculatus (Tables 1, 2 and 4). The mean population levels of total anaerobes for H. auroguttatus was significantly lower compared with P. maculatus, with no differences between the habitats for H. auroguttatus, and a slight trend for higher values in the river for P. maculatus (Tables 1, 4 and 5). Mean values ranged from 5.7 ± 1.9 log10 cfu g-1 in the reservoir during winter to 6.6 ± 0.6 log10 cfu g-1 in the river during spring for H. auroguttatus, and from 7.2 ± 1.5 log10 cfu g-1 in the reservoir during spring to 8.5 ± 0.3 log10 cfu g-1 in the river during spring for P. maculatus (Tables 3 and 5).

Bacterial species

A list of identified bacteria for each species in both habitats is shown in Table 6. All the bacteria were Gram-negative bacteria rods, and most of them were facultative anaerobes. The most frequent bacteria were the facultative anaerobe Plesiomonas shigelloides and Aeromonas hydrophila and the obligate aerobe Fusobacterium mortiferum for both fish species, independently of the habitat. A higher biodiversity of bacterial species was observed for H. auroguttatus in the reservoir and for P. maculatus in the river.

 

 

Discussion

Feeding habits

The gastrointestinal microbiota in fishes is essentially constituted of Gram-negative facultative and obligate anaerobes, which may vary among fish species with different digestive apparatus (Sullan et al., 2012). Microorganisms are known to play crucial roles in maintaining gut integrity, in strengthening immunity and disease resistance, and in contributing to digestion in higher animals. One of the most important issues in microbial ecology of the gastrointestinal tract is the understanding of how microorganisms may provide exogenous enzymes and fermentation products to fish with various feeding habits, especially when their diet is rich in fibers (Zhao, 2012). Symbiotic bacteria often help their hosts acquire nutrients from their diet, showing trends of co-evolution and independent acquisition by hosts from the same trophic levels. Sullam et al. (2012) revealed that trophic level and possibly host phylogeny shape the composition of fish gut bacteria. Since microbes can play an important role in digestive processes, we expected that fish with similar diets, especially those that are nutrient poor or difficult to digest, have been selected to harbour similar bacterial communities with similar functional capacities.

In the present study, relative lower bacterial population levels (maximum of c. 7.9 log10 cfu g-1) were found in the intestines of both fishes when compared to mammal hosts (expected to be of c. 1010 to 1011 cfu g-1 in humans, and 109 to 1010 cfu g-1 in rodents) (Ley et al., 2008). Wu et al. (2010) found a number of average aerobic and facultative anaerobic bacteria of 3.4 x 108 colony-forming units (cfu)/g in the intestinal content of yellow catfish (Pelteobagrus fulvidraco Richardson, 1846). This might be explained by the faster intestinal transit in fishes than in mammals as a limiting growth factor for bacterial populations. The mean population levels of total aerobes and total anaerobes found in the gut of the iliophagous/detritivorous H. auroguttatus are similar to those found by Silva et al. (2005) for Prochilodus argenteus Spix and Agassiz 1829, a migratory species with seasonal reproduction. Such similarity could be due to their similar feeding habits, which are based mainly on detritus and algae. On the other hand, the omnivorous P. maculatus had comparatively higher population levels when compared to those species for both total anaerobes and total aerobes. These results are unexpected since it is well known that iliophagous/detritivorous animals ingest food with high amount of recalcitrant substrates, such as fibers, and require a complex and abundant microbiota to absorb these nutrients (Silva et al., 2005; Silva et al., 2010; Silva et al., 2011). Herbivorous and some omnivorous fishes utilize gut microbes to break down cellulose, the plant structural carbohydrate (Nelson, 2002). Bacteria having these cellulose activities are either maintained in the gut or regularly brought in with ingested detritus (Prejs and Blaszczyk, 2006). Therefore, it is reasonable to suppose that this latter mechanism may be used by H. auroguttatus to digest its food, predominantly algae and plant detritus. On the other hand, studies determining enzymatic activities in the guts of these two species showed high glucosidase activities in H. auroguttatus (Duarte el al., 2013). Because microorganisms (bacteria, fungi or protozoan) are the only group capable of degrading plant substrates, the relatively low bacterial population levels in the fish intestine might be compensated by a very high enzymatic activity of bacterial cells. Contrarily to the hypothesis of a nutritional contribution of the intestinal microbiota, Smith et al. (1996) found that amounts of intestinal volatile fatty acids (VFA), end products of anaerobic fermentation, did not appear to increase in species with diets containing recalcitrant substrates.

Seasons

Syvokiene and Mickenieno (1999) reported that the intestinal microbiota population level changes according to the seasons, being higher during the more intensive feeding season (e.g., summer). This can be explained by a higher availability of substrates for the multiplication of the intestinal microbiota components, leading simultaneously to an increased enzyme activity supplied by these bacteria. In the present study, a trend for higher number of morphotypes and population levels occurred for both total aerobes and anaerobes levels during the summer and autumn for H. auroguttatus in the reservoir only, but no seasonal difference was found for this fish species in the river. On the other hand, P. maculatus had a slight trend for higher population levels of total anaerobe populations during the winter and spring in the river only. As pointed above, higher population levels for intestinal microbiota during the summer and autumn for H. auroguttatus correspond to expectation of more nutrients and higher temperatures during these seasons, conditions which can benefit microbiota multiplication (Meeren et al., 2011) Such changes were observed only in the reservoir, which is probably more susceptible to such seasonal pulses than in the more resistant conditions of the lotic system. On the other hand, P. maculatus showed seasonal change restricted to population levels of total anaerobe that reached its highest value during the winter in the river. Zambonino Filho and Schulz (1999) reported that P. maculatus trigger its gonadal development between September and March, coinciding with increased temperature, with spawning peak occurring in winter, which was associated to hydrologic cycle. Thus, this increase in microbiota populations during the winter in the river for P. maculatus could be due to a more intense feeding, which occurs after spawning period in riverine systems. In the reservoir, such trend is less favored because of the lentic conditions.

Habitats (lotic vs. lentic)

Syvokiene and Mickenieno (1999) reported that fishes from polluted waters have an altered intestinal microbiota. In the present study, both H. aurogutatus and P. maculatus had comparatively higher microbial intestinal populations when collected in the river when compared to the reservoir. The continuous and unidirectional water movement of the lotic system enables more stable environmental conditions and generally lead to better water quality due to its constant renovation. This could favor a more favorable environment for intestinal microbiota. Organic matters dissolved or in suspension are substrate for microorganism growth, and this development can contribute to an increased microbial population in the fish intestines and in the surrounding water. On the other hand, pollution from metals and organic chlorate compounds can inhibit the growth of allochthonous and autochthonous microbes (Olafsen 2001; Shiro et al., 2006). The presence of heavy metals accumulated in the Paraiba do Sul watershed could be the cause of low levels of microbial populations found in the intestinal microbiota (Teixeira et al., 2005; Terra et al., 2010; Terra and Araújo, 2011).

Bacterial species

Sullam et al. (2012) also identified a significant association between intestinal microbiota composition and fish taxonomy. Roeselers et al. (2011) suggest that the host gut is a selective environment and observed high similarities among fish from the same order. This finding suggests specialized and potentially co-evolved associations between fish and their gut bacteria. Given the fish longer life history compared with other vertebrates, and the overlap of their gut communities with those from mammals reported by Sullan et al. (2012), those authors proposed that fish may have served as the first vertebrate hosts for many of the microbes that have come to proliferate in the guts of mammals. They also reported that this would imply that because fish were the first hosts with adaptive immune systems encountered by bacteria, and that the guts of several fish lineages served as training grounds for microbes that would eventually evolve relationships with mammals.

Bacterial composition in the intestines is generally believed to be dependent on the water in which the fish lives (Shewan, 1977), with fish from cold marine waters being dominated by Gram-negative species (Pseudomonas, Moraxella, Flavobacterium and Shewanella). While the above picture is well known fish from cold marine waters, much less is known about fishes in warm tropical waters. The first few data on tropical fish species were included in a review by Shewan (1977), which concluded that fish from warm waters carried a heavier bacterial load than fish from cold waters, and that the former had a higher count in Gram-positive species. Comparison of data sets from fish intestines and other environments revealed that fish gut microbiota compositions are often similar to those of other animals and contain relatively few free-living environmental bacteria (Wong and Rawls, 2012). Bevins and Salzman (2011) suggest that the gut microbiota composition of fishes is not a simple reflection of the micro-organisms in their local habitat but may result from host-specific selective pressures within the gut. Therefore, fish appear to have more complex relationships with their gut bacteria than previously described, and further studies are necessary to clarify this issue.

Bacterial species such A. hydrophila and P. shigelloides are frequently found in the indigenous intestinal microbiota of most fish species, but also in many other aquatic animals. Such Gram-negative facultative anaerobe species were found in P. argenteus (Silva et al., 2005). Although most of enterobacteria species and genera in fish are part of indigenous microbiota, some are considered pathogenic, such as P. shigelloides, Pantoea spp., Enterobacter sakazakii, Serratia odorifera and Edwardsiella tarda (Shangong, 2010; Silva et al., 2010). Plesiomonas shigelloides has frequently been considered a 'tropical' or 'subtropical' bacterium due to the number of isolations in the digestive tract of fishes in countries within these areas.

Overall, Gram-negative bacteria are associated to carbohydrases production (Ramirez and Dixon, 2003). A higher number of Gram-negative facultative anaerobe bacteria was found by Silva et al. (2005) for P. argenteus, which coincide with the present findings for the two Siluriformes species. Nelson et al. (1999) failed to isolate obligate anaerobe bacteria in the gut of the Loricariids Panagolus maccus Schaefer and Stewart 1993 and Liposarcus sp., and observed a high enzymatic activity due to aerobe and facultative anaerobe intestinal bacteria. Panagolus maccus is a detritivorous species that feeds on decomposed wood, requiring the contribution of an indigenous microbiota able to supply enzymes to break recalcitrant plant polymers.

This study found differences in gut microbiota among species, season and habitat type. It represents an important step in the process of looking for the finding patterns and it highlights that one cannot assume that intestinal microbiota of fish will not be sensitive to multiple environmental and evolutionary effects. Our results, therefore, not only provide some of the first insights into the intestinal microbiota of fish gut communities in the tropics, but they also illustrate their changes according these three factors. However, these results should be interpreted conservatively because we did not have replicates per species for our habitat or season comparisons and because our results on the effects of diet are based on a two-species comparison. Differences between species of different families (although in the same order) are highly expected because their distinct phylogenetic history. Moreover, differences in the intestinal microbiota between habitat and seasons contributed to add knowledge on this research field, but biological significance of these findings can only be evaluated after a more rigorous comparative analysis that takes into account phylogenetic relationships and/or includes multiple pairs of species with similar variation in diet and/or habitat type. Therefore, further studies are necessary to clarify these issues in more details.

 

Acknowledgments

The authors thank Alex Braz Iacone Santos for providing the map of the study area. We also thank Dr. Dirceu Marzulo Ribeiro, Paulo Sérgio Formagio, Marcos Antonio Evangelista and Maria das Neves for infrastructure support. Furnas Centrais Elétricas S/A financially supported this research by the Program of Research and Development (P & D), process no. 016206. The Carlos Chagas Filho Research Support Foundation of the Rio de Janeiro State, FAPERJ gave sponsorship to SD and FGA. FGA and JRN are recipients of CNPq fellowship.

 

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Correspondence:
F.G. Araújo
Laboratório de Ecologia de Peixes
Universidade Federal Rural do Rio de Janeiro
BR 465, km 7 23.890-000
Seropédica, RJ, Brazil
E-mail: gerson@ufrrj.br

Submitted: October 15, 2013
Approved: April 17, 2014

 

 

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