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Niveis de metais pesados em aguas superficiais de um rio tropical, Estado de Pernambuco, Brasil.

Heavy metal levels in surface waters from a tropical river basin, Pernambuco State, northeastern Brazil

Introduction

The gathering of data related to the levels of toxic metals in the environment is not satisfying, especially in view of the setting of future permissible concentrations. However, research on heavy metals has met with strong growing interest in recent years. This is partly a consequence from the concern for environmental protection, and is due to increasing knowledge about the role and effect of metallic elements on living organisms. In Brazilian rivers are decrypted studies on concentration, distribution and transport of heavy metals in Paraiba do Sul, Mogi-Guacu, Pardo, Ribeira de Iguape and das Pedras rivers in Sao Paulo State (CETESB, 1978a, b, c; BOLDRINI et al., 1983; EYSINK et al., 1985, 1988; 2000; PFEIFFER et al., 1986; SALOMAO et al., 2001), in Iraja and Sao Joao do Meriti rivers, in Rio de Janeiro State (PFEIFFER et al., 1982; REGO et al., 1993) and in Amazonian rivers (HACON et al., 1995; LECHLER et al., 2000; PEREIRA FILHO, 1995). Specifically in Tapacura and Capibaribe river basins, Aprile et al. (2003, 2004) and Aprile and Bouvy (2008) conducted preliminary studies on content and distribution of trace metals in water and sediments.

The necessary presence of metals in trace amounts, in all living organisms seems to obey to equilibrium laws among the different metals. In order to understand the behavior of heavy metals in an aquatic ecosystem, we need to identify the major reservoirs of these elements, as well determine the rates of elemental turnover, among reservoirs. The purpose of this research was: (1) to establish the dissolved heavy metal (Fe, Mn, Cu, Pb and Zn) concentrations in natural waters, to evaluate managing strategies of the Tapacura river basin, used to supply urban and rural areas; (2) to estimate significant relationships between trace metals; and (3) to provide a database necessary for developing strategies for pollution control of the basin. These reports on the distribution of heavy metals at the Tapacura river can provide valuable contribution to the program of sanitation from the Company of Environment.

Material and methods

Study area

Tapacura river basin is located in Zona da Mata at Pernambuco State, Northeast of Brazil (Figure 1). This basin is responsible for 9.5% from the water supply to Recife Metropolitan Region. The rainfall is about 2,000 mm year-1, in the Zona da Mata Region, with maximum concentration between April and July (see Figure 1B), and 700 mm [year.sup.-1], at the Agreste. Nevertheless, many people in Agreste and Zona da Mata have no access to potable water. In general, the water depths are less than eight meters, with lower spring tides (exception of the reservoir), resulting in environments not well-mixed vertically and with lowly dynamic. There is not efficient sewage treatment system in the municipalities until today, and over 80% from domestic wastewaters are directly released into the tributaries without treatment. Furthermore, there are agricultural and industrial areas located within or around the basin, which contribute with significant amount of untreated effluents for the tributaries, in the Pombos and Vitoria de Santo Antao cities. Agriculture is the most important economic sector in semi-arid and Zona da Mata from the Pernambuco State. In Pombos city, we observed the improvement of cassava starch, whose result is the production of manipueira, a solid/liquid waste that creates a huge impact on the biota, due to high toxicity caused by heavy metals and cyanide acid (APRILE et al., 2004).

[FIGURE 1 OMITTED]

Proceedings

Eight sampling sites were established along the river, considering the area influenced by municipal sewage (zone I), agricultural runoff (zone II) and industrial plant (zone III, Figure 1). Coordinates for sampling sites were determined with Garmin brand GPS-12XL and the locations were: T1 (08[degrees]07'53"S-35[degrees]24'58"W) at Itapecirica river, upstream from Pombos city, receiving solid/liquid wastes from the improvement of cassava starch; T2 (08[degrees]07'26''S-35[degrees]22'29''W) in Tapacura river, downstream from the confluence between Agua Azul and Itapecirica rivulets, and upstream from Vitoria de Santo Antao city; T3 (08[degrees]07'11''S-35[degrees]19'15''W) at Tapacura river, downstream from the wastewater at the spirit company Pitu; T4 (08[degrees]10'56''S-35[degrees]20'22''W) in Natuba river, affluent of Tapacura river, in an agricultural area near at the Mocoto Sugar Mill, where the uncontrolled use of fertilizers and herbicides was observed; T5 (08[degrees]05'55"S-35[degrees]15'37"W) in Tapacura river, downstream from Vitoria city, and receiving part of the municipal sewage; T6 (08[degrees]05'57"S-35[degrees]14'39"W) at Tapacura river, in an agricultural area near to Manain farm, with uncontrolled use of fertilizers and herbicides; T7 (08[degrees]02'12"S-35[degrees]09'44"W) in Tapacura reservoir, and T8 (08[degrees]02'06''S-35[degrees]09'39''W) in Tapacura river, located 300 m downstream from the dam, before the supply line.

Temperature ([+ or -] 0.1[degrees]C) and pH ([+ or -] 0.1) of the surface waters were measured with a termistor and ohmmeter WTW, respectively. At each site, surface water samples (0 - 20 cm) were taken monthly, from March 1997 to December 1998, and from June 2005 to March 2006, using a Van-Dorn bottle and stored in one liter polystyrene bottles, refrigerated at 4[degrees]C. Water samples for chemical analysis were acidified to pH 2, using HCl (0.1 N), and filtered through a GF/C filter to remove the suspended material. All the manipulations were conducted inside a clean room. Heavy metals (Fe, Mn, Cu, Pb and Zn) in the 1 liter filtered samples were digested with 5 mL each of aqua-regia (HN[O.sub.3] + HCl) + HCl[O.sub.4] (Merck) at 200[degrees]C, made up to 50 mL in a volumetric tube, and measured using a Perkin-Elmer AAS Model 3300 equipped with an air-acetylene flame. All the samplings and analytical determinations followed the suggestions from Loring and Rantala (1992) and APHA (1998). Quantification of metals was based on calibration curves of standard solutions of respective metals, prepared from a commercial stock solution (trace metals 1 ICM-411 H in 5% HN[O.sub.3],

Radian International LLC) and standard seawater reference materials (CASS 1-4) from the National Research Council of Canada. Blanks and standard reference materials (SRMs) were included in the analysis, and the calibration curves were determined several times during the analysis, to check the efficiency of the extraction technique. The detection limits (DL) obtained in the analysis for the metallic ions were 0.05 Fe, 0.02 Mn, 0.001 Cu, 0.006 Pb and 0.003 mg [L.sup.-1] Zn. Values were always within the certified range. The heavy metal contamination levels were compared to the background level in a close area (see Bl in Figure 1), using the enrichment factor (EF), (ALOUPI; ANGELIDIS, 2001; SELVARAJ et al., 2004; WOITKE et al., 2003), and the potential contamination index ([C.sub.p]) (DAVAULTER; ROGNERUD, 2001). The metal levels were normalized to the surface water characteristics, with respect to iron. Therefore, EF and [C.sub.p] were defined as:

EF = [[Metal].sub.surface water] /[[Fe].sub.surface water]/[[Metal].sub.background]/[[Fe].sub.background] (eq. 1)

Cp = [[Metal].sub.maximum]/[[Metal].sub.background] (eq. 2)

Where [[Metal].sub.surface water] and [[Metal].sub.background] are the levels of targeted metals (Mn, Cu, Pb and Zn) in the water samples, and uncontaminated local, respectively. Baseline values for [[Metal].sub.background] were as follows: 0.65 for Fe, 0.12 for Mn, 0.002 for Cu, 0.006 for Pb, and 0.004 for Zn, all these values in mg L-1. Martin and Meybeck (1979) recommend 3.6% for Fe, 32.0 mg [L.sup.-1] for Cu, 16.0 mg [L.sup.-1] for Pb, and 127.0 mg [L.sup.-1] for Zn, as baseline values for [[Metal].sub.background]. Ratios between dissolved metals were determined for the waters of Tapacura river. For the chemical interpretation, the dates were analyzed using simple statistical tests and multivariate statistical analyses. Linear regressions with respective standardized residual plot were performed to estimate significant relationships between dissolved metals.

Results and discussion

Dissolved trace metals concentrations at surface waters are summarized in Table 1 (levels per sites) and Figure 2 (total averages). The concentrations of dissolved trace metals in Tapacura river basin indicate contamination with regard to anthropogenic metals. The lower distribution of dissolved metals in surface water can indicate that sedimentation process affects the suspended particle composition. The total level of dissolved Fe was high; the results were characterized by Fe concentrations ranging from 0.30 to 4.22 mg [L.sup.-1], and with average 1.35 mg [L.sup.-1], exceeding those elements in the respective river by an order of magnitude. A strong link between high soil surface and water iron levels is consistent with major erosion observed along the riverbanks. However, in the Tapacura river basin we did not verify indications of this process. Dissolved manganese presented concentrations ranging from 0.02 to 1.09 mg [L.sup.-1] (average 0.27 mg [L.sup.-1]). The highest levels of Fe and Mn were found at sites T4, T5 and T6. Copper values ranged from 0.001 to 0.014 mg [L.sup.-1], with average concentration of 0.0058 + 0.03 mg [L.sup.-1], and lowest concentration at site T1 (average 0.002 mg [L.sup.-1]). Lead concentrations were low, and varied between [less than or equal to] 0.006 (detection limit) and 0.029 mg [L.sup.-1] in site T4. This metal was below the detection limit at sites T1, T5, T6, and T8. The highest concentrations were found at sites T2, downstream from Pombos city; T3, downstream from the spirit company Pitu Ltd, and T4, in an agricultural region. Dissolved zinc ranged from [less than or equal to] 0.003 to 0.020 mg [L.sup.-1] (average 0.009 [+ or -] 0.003 mg [L.sup.-1], see Table 1 and Figure 2).

The heavy metals are environmental contaminants, very common from metal mining and processing, as well as from many other industrial, municipal and agricultural activities. According to IPCS (2001), local geological and anthropogenic influences determine the concentrations of heavy metals in aquatic systems. In general, the concentration of dissolved metals increased between the sampling sites T2 and T5. The absence of efficient sewage treatment in Pombos and Vitoria cities may be contributing to increase the levels of trace metals in part of the basin. According to National Recommended Water Quality Criteria Correction by U.S. Office of Water Drinking Water and Health (EPA, 1999); the safe limits established by Cetesb (2001), and Brazilian Health Ministry (BRASIL, 2004) to drinking water directive, in Tapacura river basin was not observed high levels of contamination by heavy metals in the water. However, in some sampling sites, the levels of Fe, Mn and Pb exceeded the recommended limits, suggesting more caution in the monitoring process of these sites.

The degree of anthropogenic impact, estimated through enrichment factor (EF) and potential contamination indices (Cp), is listed in the Table 2. Based on the classification from Taylor (1964), Mn and Pb presented the lower enrichments with EF ranging from 0 to 4 (average 1.3) for Mn, and 0 to 1.8 (average 0.5) for Pb. Enrichment factor is a good tool to distinguish the natural and anthropogenic sources (SELVARAJ et al., 2004). Five sampling sites with EF < 1 for Mn, and six sites with EF < 1 for Pb, indicated that there is no enrichment by these metals in the water column. In other words, these metals are close to background levels. On the other hand, copper and zinc presented, according to the same Taylor's classification, enrichment from moderate to severe at sampling sites T2, T7, and T8. Probably, this result means a heavy metal release, from moderate to high amount from urban area/municipal sewage (zone I) and agricultural runoff (zone II). According to the classification from Davaulter and Rognerud (2001), 30% of the samples present potential contamination indices ranging from severe to very severe contamination by heavy metals in the water column. The heavy metals showing the most extensive contamination were Mn that ranged from 0.2 to 9.1 and Cu, ranging from 1.7 to 4.6. The metal that presented the narrowest contamination was Pb, with Cp varying between 0 and 4.8 (average 1.6).

In water systems, estimates point that amorphous forms of Fe (FeOOH) and Mn (MnOOH) are predominant (LAKIND; STONE, 1989). The ratio between FeOOH and MnOOH (Fe/Mn) indicate the relative abundance of each sorbent phase. In natural conditions, there is a direct relationship between the Fe and Mn concentrations, within a confident interval. When any change in the water quality occurs (e.g. by industrial discharge), the equilibrium Fe/Mn is lost. A summary of the ratios between trace elements at each sampling site is given in Table 3. The average ratios of Fe/Mn for the Tapacura river varied from 1:1 (T6) to over 145:1 (T4). Duff (1992) reported that exist ratios of 20:1, which represents the ratio in which Fe: Mn is found in aqueous solution due to the anthropogenic activities, such as mining. Inter-riverine variations in Fe and Mn at Tapacura river may be associated to municipal sewage. Fe and Mn are diagenetically mobile in aqueous ecosystems. Reduced Fe and Mn can migrate to the marsh surface, via the pore fluids, to be re-oxidized and precipitated as (oxy) hydroxides. This process produces higher concentrations of Fe and Mn at sediments' surface (TURNER; MILLWARD, 2000), consequently reducing the levels at the water column. Other significant ratios obtained were: Fe:Cu, ranging from 60:1 (T7) to 1039:1 (T1); Fe:Zn, from 38:1 (T7 and T8) to 354:1 (T4); Mn:Cu, from 4:1 (T4) to 189:1 (T6). We also observed relationships quite close between Cu: Pb, ranging from 0.4:1 (T4) to 1.4:1 (T2), and Cu:Zn, from 0.1:1 (T1) to 2:1 (T2). Copper and zinc levels are strongly influenced by anthropogenic sources (IPCS, 1998) that may affect the two metals simultaneously.

Linear regression analysis was applied between dissolved trace metals at the sampling sites, and the significant results (at the 95% confidence interval) are reported in the Figure 3, including the residual plots. The residual analysis showed a heterogeneous trend of the 'y' axis (Mn, Cu, and Pb). The results evidenced that Fe and Mn are independent variables, that is, the presence of dissolved iron does not affect the concentrations of Mn, and vice versa (Figure 3A). We determined a factor F of 0.044, with p = 0.836, for Fe versus Mn. The results of the analysis for Zn versus Cu (F = 0.368; p = 0.550, see Figure 3B), and Zn versus Pb (F = 0.461; p = 0.505, see Figure 3C) indicated that the variables are also independent. Correlations were significant at the sites T3, T4 and T7, due to industrial and agricultural effluents. The results reflected a well-defined source of contamination, common for some trace metals. A plot composed by all samples indicates a general relationship between concentrations of Pb and Cu (F = 7.762; p = 0.010, see Figure 3D), which is not driven by the abundance, and availability of oxide material, such as iron and manganese. The lead distribution at surface waters of the Tapacura river is characterized by relative anthropogenic mobilization rates.

A PCA was applied to discover and interpret relationships between trace metals at surface waters of the basin, and the results obtained through chemical analyses are supplied in Table 4 and Figure 4. All elements were well represented by three components. Based on initial component of matrix indicators, Mn and Zn with high value (> 0.89) were found within the first component. The first factor explained 37.34% of the total variability, with an eigenvalue of 1.867. This factor can be termed as anthropogenic factor from both urban/municipal sewage (zone I) and agricultural runoff (zone II). The second factor explained 25.94% of the total variability, with an eigenvalue of 1.297, and medium to high values of Fe and Pb. This factor can be termed as 'transition factor', with characteristics from zones I and II for Fe, and with characteristics from zones II and III (industrial plant) for Pb. Although erosion processes along the riverbanks had not been observed, the contribution of iron from geogenic origin is not refused. The third factor explained 19.13% of the total variability, with an eigenvalue of 0.956, and high Cu value (> 0.97). Copper may have arisen from an anthropogenic source from agricultural runoff, although the highest levels of this element had been verified at site T2, downstream from Vitoria city. As observed in linear regression analysis, Fe and Mn were independent variables;in fact, the PCA presented two distinct factor explanations for each one.

[FIGURE 3 OMITTED]

[FIGURE 4 OMITTED]

The precision and accuracy were quite good, with most relative standard deviations and relative errors below 10% over the data tested through AAS method. In general, the industrial release of heavy metal was low, in comparison to those from municipal and agricultural areas. The metals presented a horizontal distribution very heterogeneous. In the Tapacura river basin, there is no program to remediate the contaminated water by heavy metals. As a result, we believe that the first step to apply a remedial measure and management strategies is the inspection of the agricultural areas surrounding the basin, with appropriate control in the use of fertilizers and herbicides, as well as a significant financial support to develop an efficient sewage treatment in Pombos and Vitoria cities.

Conclusion

Heavy metals presented a horizontal distribution quite heterogeneous with hotspots in the municipal and agricultural areas. Data analyses through EF and [C.sub.p] indicated moderate to severe contamination by Cu and Zn, at surface waters of the basin. The results indicated the potential pathways of trace metals, via soil from the agricultural areas and from inefficient sewage treatment, at the cities of the river basin. According to recommended safe limits, in the Tapacura river basin we did not observe high contamination levels by heavy metals, at surface waters, during this study. Nevertheless, the sampling sites from T2 to T4, and T7, require more attention in future researches. The results may assist the development of management strategies for pollution control, mainly in the agricultural areas surrounding the basin, with severe contamination.

DOI: 10.4025/actascibiolsci.v32i4.5231

Acknowledgements

The authors acknowledge the colleagues at the CPRH and ITEP for valuable help with the sampling and chemical analyses; to CNPq for the important financial support Project no. 301746/96.6; and constructive comments from anonymous reviewer that significantly improved the manuscript.

Received on September 25, 2008.

Accepted on July 16, 2009.

References

ALOUPI, M.; ANGELIDIS, M. O. Geochemistry of natural and anthropogenic metals in the coastal sediments of the island of Lesvos, Aegean Sea. Environmental Pollution, v. 113, n. 2, p. 211-219, 2001.

APHA-American Public Health Association. American Water Works Association and Water Environment Federation. Standard methods for the examination of water and wastewater. 20th ed. Washington, D.C., 1998.

APRILE, F. M.; BOUVY, M. Distribution and enrichment of heavy metals in sediments at the Tapacura river basin, Northeastern Brazil. Brazilian Journal of Aquatic Science and Technology, v. 12, n. 1, p. 1-8, 2008.

APRILE, F. M.; PARENTE, A. H.; BOUVY, M. A dinamica dos metais pesados nas aguas e sedimentos superficiais do rio Tapacura, Pernambuco, Brasil. Quimica e Tecnologia, v. 2, p. 7-14, 2003.

APRILE, F. M.; PARENTE, A. H.; BOUBY, M. Industrial residues analysis of the processing of cassava flour in the rio Tapacura basin (Pernambuco State/ Brazil). Bioikos, v. 18, n. 1, p. 63-69, 2004.

BOLDRINI, C. V.; PADUA, H. B.; NAVAS-PEREIRA, D.; RESENDE, E. K.; JURAS, A. A. Contaminacao por mercurio nos rios Mogi-Guacu e Pardo, Sao Paulo. Revista DAE, v. 44, n. 135, p. 106-117, 1983.

BRASIL. Ministerio da Saude. Portaria no. 518, de 25 de marco de 2004. Legislacao em vigilancia sanitaria. Estabelece os procedimentos e responsabilidades relativos ao controle e vigilancia da qualidade da agua. Disponivel em: <http://dtr2004.saude.gov.br/dab/saudebucal/legislacao/portar ia518_25_03_04.pdf>. Acesso em: 17 jan. 2007.

CETESB-Companhia Ambiental do Estado de Sao Paulo. Campanha especial de metais pesados e pesticidas realizada no Rio Paraiba do Sul. Sao Paulo, 1978a.

CETESB-Companhia Ambiental do Estado de Sao Paulo. Metais pesados e pesticidas na agua, sedimento de peixes: rio Mogi-Guacu. Sao Paulo, 1978b. CETESB-Companhia Ambiental do Estado de Sao Paulo. Consideracoes sobre metais pesados no rio MogiGuacu. Sao Paulo, 1978c.

CETESB-Companhia Ambiental do Estado de Sao Paulo. Relatorio de estabelecimento de valores para solo e agua subterranea do Estado de Sao Paulo. Sao Paulo, 2001. (Relatorios ambientais).

DAVAULTER, V.; ROGNERUD, S. Heavy metal pollution in sediments of the Pasvik River drainage. Chemosphere, v. 42, n. 1, p. 9-18, 2001.

DUFF, P. M. D. Economic geology. In: DUFF, P. M. D.; SMITH, A. J. (Ed.). Geology ofEngland and Wales. London: The Geology Society, 1992. p. 589-637.

EPA-United States Environmental Protection Agency. Contaminant specific fact sheets for consumers. Washington, D.C.: U.S. Office of Water Drinking Water and Health, 1999.

EYSINK, G. G. J.; DE PADUA, H. B.; PIVA BERTOLETTI, S. A. E. P. Estudo emergencial dos niveis de contaminacao por metais pesados na agua, sedimento e peixes do reservatorio rio das Pedras. Sao Paulo: Cetesb, 1985.

EYSINK, G. G. J.; DE PADUA, H. B.; PIVABERTOLETTI, S. A. E.; MARTINS, M. C.; PEREIRA, D. N. Metais pesados no Vale do Ribeira e em Iguape-Cananeia. Revista Cetesb de Tecnologia, v. 2, n. 1, p. 6-13, 1988.

EYSINK, G. G. J.; TOLEDO JUNIOR, A. P.; COSTA, M. P. Qualidade ambiental do rio Ribeira de Iguape com relacao a presenca de metais pesados e arsenio. Sao Paulo: Cetesb, 2000.

HACON, S. S.; ARTAXO, P.; GERAB, F.; YAMASOE, M. A.; CAMPOS, R. C.; CONTI, L. F.; LACERDA, L. D. Atmospheric elements and trace elements in the region of Alta Floresta in the Amazon Basin. Water Air and Soil Pollution, v. 80, n. 1-4, p. 273-283, 1995.

IPCS-International Programme on Chemical Safety. Environmental heath criteria 200: copper. Geneva: World Health Organization, 1998.

IPCS-International Programme on Chemical Safety. Environmental heath criteria 221: zinc. Geneva: World Health Organization, 2001.

LAKIND, J. S.; STONE, A. T. Reductive dissolution of goethite by phenolic reductants. Geochimica et Cosmochimica Acta, v. 53, n. 5, p. 961-971, 1989.

LECHLER, P. J.; MILLER, J. R.; LACERDA, L. D.; VINSON, D.; BONZONGO, J. C.; LYONS, W. B.;

WARWICK, J. J. Elevated mercury concentrations in soils, sediments, water, and fish of the Madeira River basin, Brazilian Amazon: a function of natural enrichments? Science of the Total Environment, v. 260, n. 1/3, p. 87-96, 2000.

LORING, D. H.; RANTALA, R. T. T. Manual for the geochemical analyses of marine sediments and suspended particulate matter. Earth Science Reviews, v. 32, n. 4, p. 235-283, 1992.

MARTIN, J. M.; MEYBECK, M. Elemental mass-balance of material carried by major world rivers. Marine Chemical, v. 7, p. 173-206, 1979.

PEREIRA FILHO, S. R. Metais pesados nas sub-bacias hidrograficas de Pocone e Alta Floresta. Rio de Janeiro: Cetem/CNPq, 1995. (Serie Tecnologia Ambiental).

PFEIFFER, W. C.; FISZMAN, M.; LACERDA, L. D.; WEERELT, M. V. Chromium in water, suspended particles, sediments and biota in the Iraja river estuary. Environmental Pollution, v. 4, n. 2, p. 193-205, 1982.

PFEIFFER, W. C.; FISZMAN, M.; MALM, O.; AZCUE, J. M. P. Monitoring heavy metals pollution by the critical pathway analyses in the Paraiba do Sul river. Science of the Total Environment, v. 58, n. 1/2, p. 73-79, 1986.

REGO, V.; PFEIFFER, W. C.; BARCELLOS, C.; REZENDE, C. E.; MALM, O.; SOUZA, C. M. M. Heavy metal transport in the Acari - Sao Joao de Meriti river system, Brazil. Environmental Technology, v. 14, p. 167-174, 1993.

SALOMAO, M. S. M. B.; MOLISANI, M. M.; CARVALHO, C. E.; LACERDA, L. D.; OVALLE, A. R. C.; REZENDE, C. E. Particulate heavy metal transport in the lower Paraiba do Sul river basin, southeastern Brazil. Hydrological Processes, v. 15, n. 4, p. 587-593, 2001.

SELVARAJ, K.; RAM MOHAN, V.; SZEFER, P. Evaluation of metal contamination in coastal sediments of the Bay of Bengal, India: geochemical and statistical approaches. Marine Pollution Bulletin, v. 49, n. 3, p. 174-185, 2004.

TAYLOR, S. R. Abundance of chemical elements in the continental crust: a new table. Geochimica et Cosmochimica Acta, v. 28, p. 1273-1285, 1964.

TURNER, A.; MILLWARD, G. E. Particle dynamics and trace metal reactivity in estuarine plumes. Estuarine, Coastal and Shelf Science, v. 50, n. 6, p. 761-774, 2000.

WOITKE, P.; WELLMITZ, J.; HELM, D.; KUBE, P.; LEPOM, P.; LITHERATY, P. Analysis and assessment of heavy metal pollution in suspended solids and sediments of the river Danube. Chemosphere, v. 51, n. 8, p. 633-642, 2003.

Fabio Marques Aprile (1) * and Marc Bouvy (2)

(1) Instituto de Ciencia e Tecnologia das Aguas, Universidade Federal do Oeste do Para, Av. Marechal Rondon, s/n, 68040-070, Caranazal, Santarem, Para, Brazil. 2Institut de Recherche pourle Developpement, Universite du Montpellier II, Montpellier, France.

* Author for correspondence. E-mail: aprilefm@hotmail.com
Table 1. Concentrations (average [+ or -] SD) and range of
dissolved trace metals (mg [L.sup.-1]).

Site           Fe                   Mn                    Cu

T1     1.30 [+ or -] 0.143  0.21 [+ or -] 0.052  0.002 [+ or -] 0.003
           1.16 - 1.44          0.14 - 0.27         0.001 - 0.005
T2     0.77 [+ or -] 0.066  0.34 [+ or -] 0.061  0.011 [+ or -] 0.002
           0.71 - 0.84          0.26 - 0.41         0.009 - 0.014
T3     1.22 [+ or -] 0.202  0.24 [+ or -] 0.072  0.004 [+ or -] 0.003
           1.02 - 1.42          0.15 - 0.33         0.001 - 0.007
T4     3.66 [+ or -] 0.553  0.03 [+ or -] 0.001  0.007 [+ or -] 0.001
           3.11 - 4.22          0.02 - 0.03         0.006 - 0.008
T5     2.09 [+ or -] 0.336  0.30 [+ or -] 0.090  0.006 [+ or -] 0.004
           1.75 - 2.42          0.19 - 0.41         0.001 - 0.011
T6     1.35 [+ or -] 0.232  1.00 [+ or -] 0.091  0.005 [+ or -] 0.004
           1.10 - 1.56          0.87 - 1.09         0.001 - 0.008
T7     0.50 [+ or -] 0.016  0.06 [+ or -] 0.017  0.008 [+ or -] 0.001
           0.49 - 0.52          0.04 - 0.08         0.007 - 0.009
T8     0.33 [+ or -] 0.033  0.05 [+ or -] 0.021  0.004 [+ or -] 0.003
           0.30 - 0.36          0.03 - 0.08         0.001 - 0.008
N =            132                  176                  176

Site            Pb                     Zn

T1              --            0.010 [+ or -] 0.001
             < 0.006             0.009 - 0.011
T2     0.008 [+ or -] 0.006   0.004 [+ or -] 0.003
         < 0.006 - 0.014         0.003 - 0.008
T3     0.011 [+ or -] 0.008   0.009 [+ or -] 0.008
         < 0.006 - 0.018         0.003 - 0.019
T4     0.019 [+ or -] 0.013   0.010 [+ or -] 0.001
         < 0.006 - 0.029         0.010 - 0.011
T5              --            0.008 [+ or -] 0.000
             < 0.006             0.008 - 0.008
T6              --                     --
             < 0.006                < 0.003
T7     0.008 [+ or -] 0.007   0.013 [+ or -] 0.006
         < 0.006 - 0.016         0.010 - 0.020
T8              --            0.009 [+ or -] 0.004
             < 0.006             0.006 - 0.013
N =            154                    132

Table 2. Degree of anthropogenic impact estimated based on the
enrichment factor (EF) * and potential contamination index
([C.sub.p]) ** for the waters of the basin.

Site      Temp.      pH        Fe          Mn          Cu
       ([grados]C)
                            EF    Cp    EF    Cp    EF    Cp

T1        25.5       7.70   1.0   2.2   0.9   2.3   0.3   1.7
T2        29.6       8.04   1.0   1.3   2.4   3.4   4.8   4.6
T3        31.7       7.95   1.0   2.2   1.1   2.8   1.2   2.3
T4        29.0       7.26   1.0   6.5   0.0   0.2   0.6   2.6
T5        27.4       7.02   1.0   3.7   0.8   3.4   0.9   3.5
T6        27.4       7.33   1.0   2.4   4.0   9.1   1.3   2.8
T7        29.2       7.78   1.0   0.8   0.6   0.6   5.4   3.1
T8        28.5       7.32   1.0   0.6   0.8   0.6   4.4   2.5

Site      Pb          Zn

       EF    Cp    EF    Cp

T1     0.0   0.0   1.3   2.8
T2     1.1   2.3   1.2   2.1
T3     0.9   3.0   1.7   4.7
T4     0.6   4.8   0.5   2.8
T5     0.0   0.0   0.6   2.0
T6     0.0   0.0   0.0   0.0
T7     1.8   2.7   4.3   5.0
T8     0.0   0.0   4.3   3.2

* EF < 1 no enrichment; EF [mayor que o igual a] 1 - < 3 minor
enrichment; EF [mayor que o igual a] 3 - < 5 moderate enrichment;
EF = [mayor que o igual a] 5 - < 10 moderate -severe enrichment;
EF [mayor que o igual a] 10 - < 25 severe enrichment; EF > 25
[mayor que o igual a] < 50 very severe enrichment and EF [mayor
que o igual a] 50 extremely severe enrichment (Taylor, 1964). **
[C.sub.p] > 3 (bold) [??] severe contamination.

Table 3. Ratios between trace metals in the fluvial waters.

Ratio       T1       T2      T3      T4        T5

Fe:Mn      6:1       2:1     5:1    145:1     7:1
Fe:Cu     1039:1    67:1    278:1   524:1    362:1
Fe:Pb       --      97:1    116:1   192:1      --
Fe:Zn     129:1     137:1   96:1    354:1    269:1
Mn:Cu     166:1     29:1    55:1     4:1      52:1
Mn:Pb       --      42:1    23:1     1:1       --
Mn:Zn      21:1     59:1    19:1     2:1      38:1
Cu:Pb       --      1.4:1   0.4:1   0.4:1      --
Cu:Zn     0.1:1      2:1    0.3:1   0.7:1    0.7:1
Pb:Zn    < 0.01:1   1.4:1   0.8:1   1.8:1   < 0.01:1

Ratio     T6      T7        T8

Fe:Mn     1:1     9:1      6:1
Fe:Cu    257:1   60:1      74:1
Fe:Pb     --     61:1       --
Fe:Zn     --     38:1      38:1
Mn:Cu    189:1    7:1      12:1
Mn:Pb     --      7:1       --
Mn:Zn     --      4:1      6:1
Cu:Pb     --      1:1       --
Cu:Zn     --     0.6:1    0.5:1
Pb:Zn     --     0.6:1   < 0.01:1

Table 4. Explanation of total variability from the water samples
with rotated component matrix (for three factors) and initial
eigenvalues.

                    Component matrix

                    Factor 1   Factor 2   Factor 3

Fe                  -0.0599    -0.8827     0.1119
Mn                  -0.9096     0.1525    -0.0125
Cu                  -0.0566    -0.0497    -0.9759
Pb                   0.2628    -0.7619    -0.2653
Zn                   0.8914     0.0020     0.0415

                    Initial Eigenvalues

Eigenvalue           1.8669     1.2970     0.9564
Cumul. Eigenval      1.8669     3.1639     4.1203
% total Variance      37.34      25.94      19.13
Cumulative %          37.34      63.28      82.41

* Bold values are similar sources in factors > 0.7000.

Figure 2. Total average [+ or -] SD of trace metals in surface
waters from the Tapacura river basin

Fe   1.35 [+ or -] 0.20
Mn   0.27 [+ or -] 0.05
Cu   0.0006 [+ or -] 0.0003
Pb   0.0006 [+ or -] 0.0004
Zn   0.009 [+ or -]  0.0003

Note: Table made from bar graph.
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Title Annotation:texto en ingles
Author:Marques Aprile, Fabio; Bouvy, Marc
Publication:Acta Scientiarum Biological Sciences (UEM)
Date:Oct 1, 2010
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