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Impact of damming on the Chironomidae of the upper zone of a tropical run-of-the-river reservoir/Impacto de um represamento sobre Chironomidae do remanso de um reservatorio fio d'agua tropical.

1. Introduction

Chironomidae larvae are among the major components of benthic communities in most freshwater ecosystems, where they can reach high densities and richness (Oliver, 1971; Pinder, 1986; Cranston, 1995). Impacts on aquatic ecosystems can be followed by shifts in the Chironomidae that have been used in biomonitoring and environmental impact assessments, from organisms to the community level (Rosenberg et al., 1986). In general, the effects of dam construction on Chironomidae are evaluated by comparing sites located upstream and downstream the reservoir and the taxonomic identification varies from family (Nichols et al., 2006) to species (Penczak et al., 2006; Glowacki et al., 2010; Grzybkowska et al., 2012) and morphospecies (Rosin et al., 2009). In some cases, authors also analyse data using tribe and subfamily level (e.g. Grzybkowska et al., 2012).

For decades, knowledge of the conditions prior to damming has been considered fundamental to the assessment of dam impacts, as many rivers have been fragmented without prior knowledge of the of the lost species' ecological role (Petr, 1978; Petts, 1984; Power et al., 1988). However, comparing fauna of the same site in pre- and post-reservoir construction seems to have been the exception in the reservoir impact evaluation in recent years. Penczak et al. (2006) analyzed Chironomidae assemblages before and after a hydroelectric plant began operating, but sampling began two years after reservoir construction.

Differences in reservoir operation, drowned areas, substrates, and trophic states make the responses of Chironomidae composition and metrics vary from one reservoir to another. Therefore, the statement of expected responses is not easy. It is particularly true to backwater sites because the bulk of the papers in reservoir impact focused on changes in the fauna of downstream sites by the comparison with sites located upstream the reservoir.

Previous studies carried out in the pre-filling and in the first-year post-filling of the Mogi-Guacu reservoir damming revealed Chironomidae as the major component of the benthic fauna nearly all the sampling time. This result justifies a more detailed study about this family. These studies also showed low impact over the composition the communities of the main river channel upstream the reservoir and in the central zone of it. Moreover, similar temporal tendencies occurred for variation of richness of major taxonomic groups and Chironomidae genera (Brandimarte et al., 1997, 1999). This work aimed to use Chironomidae of the upper zone of the reservoir identified to levels behind family as a tool for evaluating the impact of the river damming. Based in the results quoted formerly, we hypothesized that the damming would not severely impact the larvae identified in levels behind family.

2. Material and Methods

2.1. The study area

The Mogi-Guacu river has its origin in the Mantiqueira mountain range, Minas Gerais State, southeast Brazil (26[degrees] 16' S, 46[degrees] 42' W; 1,650 m a.s.l.). It reaches Pardo River at Sao Paulo State after 473 km (377.5 km of which are in Sao Paulo State) and at about 490 m a.s.l. (Maier et al., 1978). The area is under the influence of the Koppen Cwa climate type-mesothermal with a dry winter, from June to September (CESP, 1993). The catchment has 17,560 [km.sup.2] and embodies 44 cities (37 in the Sao Paulo State); many of them unload raw sewage and wastewaters into the river. Significant industrial load is mostly released as effluents in the Mogi-Guacu tributaries (CESP, 1993). The original vegetation was mainly semi-deciduos latifoliate tropical forest as well some "Cerrado" (Brazilian savannah) remainders. Nowadays, small and sparse fragments remain (CESP, 1993), and sugar cane culture and pasture dominate the landscape of the study area.

A multipurpose run-of-the-river reservoir, with four gated spillways and power generation of 7.2 kW, was created on the Mogi-Guacu river (Sao Paulo State, Brazil), at 598.5 meters a.s.l. (Figure 1). Initially, in November 1995, the lake was filled to the volume required for water supply. Filling for the generation of electric power occurred in December 1995. Morphometric characteristics of the reservoir include length of 8 km, surface area of 5.73 [km.sup.2], volume of 12.56 million [m.sup.3], dam height of 13.5 m, dam length of 170 m, spillway level at 594.3 m a.s.l. (CESP, 1993), and calculated mean retention time of 74 hours.

2.2. Surface flow and depth analysis

The surface flow was estimated using a float (an orange) and measuring the time of its passage across a measured distance (Wetzel and Likens, 1991).

The test U of Mann-Whitney (Zar, 1999) was applied to compare values of depth and flow between pre- and post-filling phases.

2.3. Substrate characterization

The composition of the substrate was visually characterized for each sampling unit during the sampling period. The following fractions were recognized: stones, sand, sludge, and organic matter. Gravel and larger components were grouped as stones. Fractions finer than sand, but not necessarily muddy, were grouped as sludge. The frequency of occurrence of each fraction in the sampling units was calculated. The effect of the damming on the different fractions was evaluated deducting the frequency in the pre-filling phase from the frequency in the post-filling phase. The positive variation of a fraction shows that a higher number of sampling units contained the fraction in the post-filling phase. Negative variation indicates that a smaller number of sampling units contained the fraction in the post-filling phase.

2.4. Sampling and fauna analyses

The choice of reference sampling sites was difficult due to the hard access and navigability and the heavy influence of human activities in the study area. We applied an "impact inferred from temporal change alone" design sensu Green (1979) in order to compare the conditions before and after impoundment. One sampling site was established in the upper zone (backwater) of the reservoir (Figure 1) in a straight stretch of the river. Substrate sampling was conducted from February 94 to August 94 before the river damming (Pre-Filling Phase), in November 95 during the initial filling (Filling), and trimestrially from February 96 to August 96 (Post-Filling Phase).


Using a simple random scheme, three sampling units of substrate were taken in the main channel (MC) and in the right (RM) and left (LM) margins with a modified Petersen grab (325 [cm.sup.2]) in each sampling date. Stones and small boulders were individually washed for attached individual removal. Organisms in coarse substrates were floated out with saturated NaCl solution (Brandimarte and Anaya, 1998). They were selected by a 250 [mu]m mesh, preserved in 4% neutral formalin, and stained with phloxine-B.

Chironomidae larvae were identified to the genus level using the keys of Epler (1992), Oliver et al. (1978), Wiederholm (1983), Coffman and Ferrington Junior (1996), and Trivinho-Strixino and Strixino (1995).

The density per square meter and the percent abundance were calculated for the total of Chironomidae, subfamilies, tribes, and genera. The calculation of density involves a rule of three on the basis of the number of individuals collected in the sampler area. In spite of the density not being a reliable representation of numbers of individuals in a square meter due to that extrapolation, it is a good tool for comparing among data from different papers. For that, the authors chose to use it instead of raw data.

Genera richness was considered the simple sum of genera in the sampling units. The use of measures of richness assumes the richness decreases with impact occurrence. Dominance was measured by the higher value of percent abundance, and its use is based on the assumption that the number of individuals of tolerant taxa increases if an impact is negative.

The test U of Mann-Whitney (Zar, 1999) was applied to compare the density, richness, and dominance values between the pre- and post-filling phases. The Spearman rank correlation coefficient [(.sub.S]) (Zar, 1999) was applied to search for correlation between Chironomidae densities (using subfamilies, tribes, and more abundant genera data) and surface flow. Statistic analysis was performed using the free data analysis package Past (PAlaentological STastistics) (Hammer et al., 2001).

The Rosso's ecological value index (EVI) (Equation 1 that results from the Equations 2 to 4) for quantitative analyses was applied to determine the ecological importance of each genus in the pre- and post-filling phases. This index was first developed to qualitative analyses by Pinder and Rosso (1998). The quantitative form (Rosso, personal communication) ranked the genera based on a geometric average of three components: genus's presence in the totality of observations, equitability in the samples in which the genus was registered, and the genus's overall relative abundance:

[EVI.sub.j] = [cube root of [P.sub.j][J.sub.j][A.sub.J]]


[P.sub.j] = [n.sub.j]/N (2)

[n.sub.j] = samples with "j" genera and N = total number of sampling units or occurrence;

[E.sub.j] = [Levins.sub.j]/ln(nj), [Para Levins.sub.ij] = -[N.summation over (i=1)][P.sub.ij].ln([P.sub.ij]) (3)

[E.sub.j] = the Levins measure of the niche breadth calculated with [p.sub.ij] (the relative abundance of genus "j" in the sample "i"); and


[a.sub.ij] = absolute abundance from genus "j " in the sample "i" (measuring the overall relative abundance).

The three components reach values between 0 and 1, so the geometric average is also in this interval. Ecological values near 1 are related to genera with high frequency in the samples, high relative abundance, and high equitability. The difference between the EVI calculated for each sampling period was used as an impact measurement: a positive difference meant an increased ecological value for that genus in the post-filling phase; inversely, a negative difference meant a decreased ecological value in the same phase. The samples collected in November of 1995, during the filling phase, were removed from the calculation because they do not represent a well-defined (before or after) sample period.

3. Results

After the filling, the depth increased significantly in the margins and the main channel of the sampling site, and the surface flow decreased significantly, except for the left margin (Figure 2). The substrate also changed, mainly in the margins where it became finer (Figure 3).


The total density of Chironomidae tended to decrease after damming, and this reduction was significant in both of the margins (Figure 4). The density of Chironomidae was significantly correlated with surface flow: positive correlation for Orthocladiinae (n = 27; [r.sub.S] = 0.4166; p = 0.0306) and Lopescladius (n = 27; [r.sub.S] = -0.3901; p = 0.015) and negative for Chironomini (n = 27; [r.sub.S] = -0.4893; p = 0.0096).

The percent abundance tended to increase for Tanypodinae and Chironomini and decrease for Orthocladiinae and Tanytarsini (Figure 5). In relation to significant changes of densities, Tanypodinae increased significantly in the left margin, Orthocladiinae decreased in the main channel and margins, and Tanytarsini decreased in the right margin (Figura 4).

Lopescladius, Polypedilum, Parachironomus, and Rheotanytarsus had the highest densities and, with few exceptions, occurred during all the sampling period (Figure 6). Decreases of Orthocladiinae and Tanytarsini reflected respectively mainly the declines of Lopescladius that was significant in the right margin (U = 17.5; p = 0.0057) and main channel (U = 33;p = 0.0139) and Rheotanytarsus that was significant in the right margin (U = 15.5; p = 0.0056).

The Rosso's EVI decreased for Lopescladius and Polypedilum and increased for Parachironomus and Rheotanytarsus. The major differences in EVI between pre- and post-filling phases occurred for Lopescladius and Parachironomus (Table 1).


In the post-filling phase, the month values of dominance remained in the same range as the pre-filling phase, whereas richness was lower in the margins (Figure 7).

4. Discussion

Contrary to expectations, relevant changes occurred in the Chironomidae structure of the upper zone of the Mogi-Guacu reservoir. The occurrence of impact was indicated by richness decrease in the margins and by a reduction in the relative abundance of taxa representative of faster waters. The fauna in the margins, mainly in the left one, was more sensitive to the damming than the fauna in the main channel was. This fact is related to changes in the substrate and probable higher availability of organic matter as food.





Decreases of Orthocladiinae and Tanytarsini in the post-filling phase were associated with the decline of current velocity because their principal components, Lopescladius and Rheotanytarsus, prefer primarily lotic conditions (Coffman and Ferrington Junior, 1996; Trivinho-Strixino, 2011).

The preference of Orthocladiinae and particularly Lopescladius for faster water was indirectly supported by the positive correlation between larvae density and surface flow. In Brazil, this genus was found in high densities in benthic communities at regulated sandy rivers (Rosin et al., 2009) and well-preserved lotic environments (e.g. Henriques-Oliveira et al., 2003a). The absence of records of this genus in a review about Chironomidae at lentic systems of Sao Paulo State (Roque et al., 2004) is evidence of its association with faster water. Moreover, the relationship between Lopescladius and sand substrate (e.g. Henriques-Oliveira et al., 2003a; Trivinho-Strixino, 2011) can explain its decrease in the post-filling phase as this fraction became less important.

The decrease of total Orthocladiinae and Tanytarsini in one or both of the margins can be also related to the change of substrate, which became finer. Substrate dominated by fine fractions, as seen in the margins after filling, are inappropriate for the settlement of many Chironomidae taxa (Hogg and Norris, 1991; Shimizu et al., 1995).

The dominance of Chironominae genera, mainly Polypedilum and Rheotanytarsus, in the post-filling phase could be due to a high availability of detritus. The relationship between these genera and detritus is well-established and observed by several authors such as Henriques-Oliveira et al. (2003b), Anjos and Takeda (2010), Trivinho-Strixino (2011), and Galizzi et al. (2012).

The densities of Polypedilum tended to be higher in margins and months with reduced surface current velocity in the pre-filling and post-filling phases. This genus occurs preferentially in lentic habitats, and, in general, larvae are shredders-herbivores and collectors-gatherers (Coffman and Ferrington Junior, 1996). Galizzi et al. (2012) and Henriques-Oliveira et al. (2003b) found a high percentage of amorphous detritus in the gut content of this genus. Therefore, in the upper zone of the Mogi-Guacu reservoir, it was favored by the decline of current velocity and the expected higher sedimentation of organic matter in drier months.

The remaining terrestrial vegetation in the reservoir bottom could explain the increase of Parachironomus if we assume that vegetation has the same effect on sustaining habitat that submerged macrophytes, in which this genus is usually found, according Anjos and Takeda (2010). Changes in resources and conditions were certainly related to flow reduction and the flooding of riparian vegetation due to the river impoundment. Moreover, the increase in Chironomidae associated with the flooding and posterior degradation of terrestrial vegetation is a common event. It was observed, for example, in the Brazilian Paraibuna reservoir in the beginning of the rainy season, when larvae density increased substantially (Brandimarte and Shimizu, 1996).

The impact on the zoobenthic community in the first year after filling also occurred in a site downstream the Mogi-Guacu dam, where total density and taxa richness decreased. Nevertheless, this tendency did not continue in the following two years, and the variation of both metrics remained in the same range as the pre-filling phase (Brandimarte et al., 2005). So, the impact on Chironomidae might not last in the upper zone of the reservoir. Moreover, as the impact varied according to the habitat analyzed, these results highlighted the need for a multi-habitat approach in environmental impact studies concerning the creation of new reservoirs. Therefore, it would be possible to make a more robust assessment of the damming impact on the aquatic biota.

Finally, our results sustain the use of Chironomidae as bioindicators because the damming impact was indicated by changes in the structure of this taxocenose. Genera with similar ecological traits (such as a preference for slower waters and detritivore habit) were less affected by the damming. On the other hand, there was a negative impact on the rheophilic genera. Although the analysis of traits did not become an objective of this paper, those results also could sustain the use of functional traits in the assessment of benthic communitie's responses to anthropogenic stressors as proposed by Poff et al. (2006).


The authors are grateful to the technicians of the Sao Paulo State Energy Company (CESP) for logistic support and to the Brazilian National Research Council (CNPq) for the Mauricio Anaya MS grant.


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A. L. Brandimarte (a) *, M. Anaya (b) and G. Y Shimizu (a)

(a) Departamento de Ecologia, Instituto de Biociencias, Universidade de Sao Paulo-USP, Rua do Matao, Travessa 14, CP 321, CEP 05508-900, Cidade Universitaria, Sao Paulo, SP, Brazil

(b) Universidade Cidade de Sao Paulo-UNICID, Rua Cesario Galeno, 448/475, CEP 03071-000, Tatuape, Sao Paulo, SP, Brazil

* e-mail:

Received: August 15, 2014--Accepted: February 9, 2015--Distributed: May 31, 2016

(With 7 figures)
Table 1. Ecological value index for Chironomidae genera
with Rosso's EVI > 0.20 in pre and post-filling phases in
the upper zone of Mogi-Guacu reservoir (Sao Paulo State,


Genus              Total     Pre-     Post-    Difference
                  Period   Filling   Filling

Lopescladius       0.50      0.46      0.24       -0.22
Polypedilum        0.46      0.49      0.38       -0.11
Parachironomus     0.35      0.24      0.44        0.20
Rheotanytarsus     0.33      0.41      0.49        0.08
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Title Annotation:Original Article
Author:Brandimarte, A.L.; Anaya, M.; Shimizu, G.Y.
Publication:Brazilian Journal of Biology
Date:Apr 1, 2016
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