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Journal of the Chilean Chemical Society

versión On-line ISSN 0717-9707

J. Chil. Chem. Soc. vol.55 no.4 Concepción dic. 2010

http://dx.doi.org/10.4067/S0717-97072010000400017 

J. Chil. Chem. Soc., 55, N0 4 (2010)

A PRELIMINARY STUDY OF THE DISTRIBUTION AND MOBILITY OF MERCURY IN WATER AND SEDIMENTS FROM THE SAN JUAN RIVER WATERSHED, NUEVO LEON MEXICO

 

ROBERTO MACÍAS MEDRANO1, JUAN MANUEL ALFARO BARBOSA1, LAURA HINOJOSA REYES1, ARACELY HERNÁNDEZ-RAMÍREZ1, KARIM ACUÑA-ASKAR2

1Facultad de Ciencias Químicas, Universidad Autónoma de Nuevo león. Pedro de Alba s/n, Cd. Universitaria. San Nicolás de los Garza, NL. 66400. México.
2facultad de Medicina, Universidad Autónoma de Nuevo León. Av. Madero y Dr. Aguirre s/n, Col. Mitras Centro, Monterrey, NL. 64460. México.


ABSTRACT

Monitoring of distribution and fractionation of mercury (Hg) from within the San Juan River Basin that provides water for the Metropolitan Area of Monterrey, Mexico (MAM), was performed. The purpose of this work was to characterize the risk of Hg exposure to human populations that reside in communities nearby the area. Total Hg was quantified from water and surface sediments (0-10 cm) collected from 11 locations during the summer season of 2006. The analysis of Hg was carried out by Cold Vapor Atomic Absorption Spectroscopy (CVAAS). Simultaneously, some relevant physical and chemical parameters were analyzed in water samples and correlated to Hg concentrations to trace the fate of Hg in the watershed. In the river water samples, Hg levels were in the range from 0.17 to 1.14 |ig/L. The mean concentration level of Hg in sediment samples was 0.405±0.074 mg/Kg and showed a uniform Hg distribution along the San Juan River Basin, conversely, the fractionation studies showed that chemical speciation plays an important role in stability and low mobility.

Keywords: mercury; fractionation; sediments; waterbodies; San Juan River watershed; Monterrey, Mexico.


INTRODUCTION

According to the United States Environmental Protection Agency (US EPA), mercury (Hg) is a priority contaminant of continuous concern on the global scale [1]. Numerous national and international agencies and organizations have targeted Hg for emission control due to its persistence, bioaccumulation and toxicity in the environment [2]. Although aquatic Hg contamination is a result of atmospheric deposition and terrestrial sources from natural and anthropogenic origin [3], regional emission sources could significantly contribute to Hg loadings through discharges from industrial processes, mining activities, and watershed runoff [4,5]. In the environment, elemental and inorganic Hg is deposited on aquatic sediments where a fraction reacts with sulfate to form mercury sulfide, which is not soluble, and therefore, its bioavailability becomes significantly reduced, whereas a small percentage is converted to methylmercury (MeHg) by bacteria. MeHg is an environmental neurotoxicant which is bioaccumulated and biomagnified in the food web [2]. Therefore, information regarding concentrations and transport of Hg in aquatic ecosystems is needed to predict potential impact on both human and aquatic life.

Worldwide contamination of Hg has been reported in aquatic systems [6-11], including contamination in Mexico [12-14]. However, no data has been published concerning the distribution of Hg contamination in the San Juan River watershed ecosystem. The San Juan River watershed is located in northeastern Mexico and belongs to the Bravo-Conchos River basin. The San Juan River basin has a total surface area of approximately 33 000 Km2 comprising the states of Coahuila (40 %), Nuevo Leon (57 %), and Tamaulipas (3 %). The watershed includes a number of smaller tributary basins such as Pesqueria River, Santa Catarina River, San Juan River, and Pilon River. Among the various rivers that make up this basin, the San Juan River is the largest and most important river in the Mexican state of Nuevo Leon and stands out as the major tributary of the lower Grande/Bravo River basin. This river originates in the mountain range of the Sierra Madre Oriental Mountain, approximately 30 Km southeast Monterrey and runs across the border between Mexico and USA from Ciudad Juarez (Chihuahua) and El Paso (Texas) to its outlet into the Gulf of Mexico near Matamoros (Tamaulipas) and Brownsville (Texas). The San Juan River supplies the Cuchillo reservoir, which provides water for the Metropolitan Area of Monterrey (MAM) [15-17]. The MAM is the third largest metropolitan area in Mexico and holds a population of approximately four million inhabitants [18]. Although a number of water quality studies have been conducted within the San Juan River watershed, serious problems associated to the persistence of heavy metal pollution have been reported [19,20]. A study conducted in the Santa Catarina River tributary of the San Juan River reported contamination by Fe, Cu, Zn, Cd, and Sr in sediments [17]. Subsequently, Flores-Laureano and Navar [20] assessed the pollution of the San Juan River and its tributary Santa Catarina River during the period 19951996. Metals including Al, As, Ba, Cd, Cu, Cr, Fe, Mn, Pb and Fe, exceeded the drinking water quality standards set by the Mexican environmental regulations. Furthermore, this study reported bacteriological and physical parameters that exceeded the drinking water quality standards. Thus, the need for monitoring other relevant priority pollutants such as Hg is mandatory for improving our understanding and assessment of this complex water ecosystem.

The aim of this work was to investigate Hg concentrations in surface water and sediments in the San Juan River watershed and evaluate changes in Hg distribution along different sampling sites followed by an assessment of the degree of environmental impact and human exposure to Hg. In addition, a three-step sequential extraction procedure (SEP) described in the United States Environmental Protection Agency (US EPA) method 3200 [21] was applied to evaluate Hg fractionation and mobility in the sediment samples.

EXPERIMENTAL

2.1 Study area and sampling

Water and sediment samples were collected in 11 locations from the San Juan River watershed situated in the state of Nuevo Leon in August 2006 (Fig. 1). Shallow water samples were taken nearby the river bank. Surface sediment samples in the depth range 0-10 cm were collected. Six sites were selected along the Santa Catarina River from the eastern suburbs of the city of Monterrey to its junction with the River San Juan; one sample was collected from the La Silla River, at the intersection of this river course and Santa Catarina tributary; three additional sites were located along the San Juan River, between the Boca and the Cuchillo reservoirs; and one sample was collected from the Cuchillo reservoir in the municipality of China, Nuevo Leon, located at 102 Km eastern Monterrey.



Fifty seven percent of the San Juan River watershed has a tropical weather, whereas thirty four percent ranges from semiarid to arid. Monthly rainfall has a bimodal type of distribution, with the first peak occurring in May-June and the second peak, the most important in terms of total depth, occurring during September-October. The annual average rainfall varies from 200 mm to 1500 mm [15]. Metropolitan Area of Monterrey soils are characterized by Feozem, Cambisol and Regosol soils with calcareous structures [22].

2.1.1 Water samples. Water samples were collected at the surface (0.5 m depth) in 500 mL cleaned polytetrafluoroethylene (PTFE) bottles. Characterizations and localization of observed water ecosystems are presented in Table 1.



2.1.2 Sediments. A 4.4 cm i.d. by 50 cm long custom-made sediment core sampler meeting the US EPA specifications [23] was used to collect sediment samples. All samples were placed in polyethylene bags and frozen before being subjected to analysis.

2.2 Laboratory analysis

2.2.1 Water samples

Water samples were filtered through Whatman No. 41 filter paper. Filtered samples were acidified at pH 2 with 0.5 mL of HNO3 (65% w/v) and stored at 4°C until analysis. Total Hg was quantified in water samples during the first week after field sampling.

2.2.2 Sediments

Sediment samples were thawed, brought to room temperature and homogenized. Percent moisture was determined on a separate representative portion of the sample by loss of mass upon heating below 40°C to minimize losses of Hg [2]. Results on a dry weight basis were used to remove some of the variability associated with wet samples. The average moisture content of samples was 27± 6% (n = 11). The dry samples were further grounded and homogenized in agate mortar, and sieved through 63 mu mesh, proceeding to store it in a propylene container.

For total Hg, sediment samples were digested using the EPA Method 3052 [24] microwave-assisted method in closed vessels (CEM MSP-1000 Microwave Sample Preparation System). Approximately, 1 g representative wet samples were weighed into microwave vessels followed by the addition of 9 mL concentrated HNO3 and 2 mL concentrated HCl. Vessels were then sealed and microwave irradiated at 180°C for 10 min. Following digestion, the Teflon® PFA (perfluoroalkoxy) microwave vessels were cooled down and the digests diluted to 25 mL in volumetric flasks with double-deionized (DDI) water (18 M£2-cm) obtained from a Barnstead NANOpure Water System (Dubuque, IA, USA).

2.2.3 Fractionation procedure

A three-step sequential extraction procedure was performed as described in US EPA 3200 method [21,25,26] . This procedure included a sequential extraction process for different operationally defined fractions (mobile Hg, semi-mobile Hg, and non-mobile Hg) and provided detailed information about the mobility of Hg in all samples. Sequential extraction procedures (SEPs) have been widely used to determine the partitioning of contaminants associated with different categories of soil constituents and to elucidate the transfer potential and thus the availability and mobility according to the extractability by various operationally defined solvents [27]. Extractions were carried out using moist samples weighing 1 g. After completion of the specific conditions of each stage, mixtures were centrifuged at 3300 rpm for 5 min. For each sample, the supernatant was transferred to a volumetric flask, and if necessary acidified with HNO3 at pH < 2 and then diluted to 25 mL before analysis. The residue was then treated following the conditions summarized in Table 2.



2.2.4 Analytical procedure for total Hg determination

The determination of the total Hg in water samples, and acid digests and extracts of sediment samples were performed by cold vapor atomic absorption spectrophotometry (CVAAS) in a Varian SpectrAA5 apparatus equipped with a continuous flow VGA-77 Vapor Generation Accessory. Total Hg concentrations were determined using the conventional CVAAS procedure following the reduction of inorganic Hg with SnCl2 in acidic medium [28]. Quantification of mercury was based on aqueous standard calibration curves (external calibration). The Hg concentration was within the range 1-10 (ig/L. The limit of detection (LOD) for water and sediment samples were 0.21 (ig/L and 0.021 mg/Kg, respectively. The LOD was defined as three times the standard deviation of three measurements of the blank, divided by the slope of the calibration curve. Water samples were analyzed in duplicate and sediment samples were analyzed in triplicate. Blank samples and certified reference material for marine sediment IAEA-433 acquired from the International Atomic Energy Agency (Geneva, Switzerland) with a total Hg concentration of 0.168 ± 0.017 mg/Kg were routinely analyzed with each batch of samples to evaluate the accuracy and precision of the analytical procedure. Certified and measured values were in agreement with a recovery efficiency of 98 ± 13%. For the analysis of water samples, the proposed method was validated by spiking the sample with known amount of inorganic mercury. The recoveries from spiked solutions were varied in the range 92-97%.

2.2.5 Other physical and chemical parameters

Water quality parameters, including pH, redox potential, temperature, conductivity, dissolved oxygen (DO), total dissolved solids (TDS), and salinity were simultaneously measured in the field. An Orion 290 A pH meter was used for pH and redox potential (Eh) measurements; DO was measured using an Orion 835 Dissolved Oxygen meter; and temperature, conductivity and TDS were measured with an Orion 135 probe.

2.2.6 Statistical methods

Pearson's correlation was used to evaluate the associations between parameters. All statistical analyses were performed with SPSS software version 17 (SPSS Inc., Chicago, IL, USA). A two-tailed p < 0.05 was considered statistically significant.

RESULTS AND DISCUSSION

Eleven representative sampling points of varying degree of pollution of the San Juan River Watershed were selected on the basis of previous reports in this area [19, 20] and unpublished work from our laboratory.

3.1 water quality

Sampling locations with coordinates and environmental conditions during sampling with total Hg concentration found in filtered river samples are shown in Table 1. Water samples from San Juan River watershed recorded temperatures ranging 24.0-34.5°C. Standards for temperature to sustain aquatic life establish a range between 20-30°C. The pH is the indicator of acidic or alkaline conditions of waterbodies. The standard for any purpose in-terms of pH is 6.5-8.5 [29]; in this regard, the pH of San Juan River ranged from 7.60 to 9.01 with a mean value of 8.3 indicating alkaline water streams. Total dissolved solids (TDS) ranged from 252 mg/L at sample site 2 to 452 mg/L at sample site 8. Although, TDS is a non-priority pollutant in surface waters, but the EPA suggests a maximum level of 250 mg/L to minimize harm to humans and aquatic life [30]. The average electrical conductivity was 720 (iS/cm. This high value observed at the San Juan River watershed could be related to the high level of TDS in this waterbody. The mean Eh was 134.5 mV, which ranged from 85.10 to 211.90 mV, while the average salinity was 1.2 mg/L.

Some of the physicochemical parameters such as pH, temperature and TDS exceed the water quality standards. These results could be indicative of contamination problems in the San Juan River watershed and were in agreement with a preliminary study carried out by Flores-Laureano and Navar [20].

Horvart et al. [7] pointed out that total Hg concentration in water streams could be affected by the hydrological conditions prevalent the sampling period. In this study, total Hg concentrations in water samples were variable across the region (Table 1) and ranged from 0.17 to 1.14 (ig/L with a mean value of 0.63 (ig/L. The tributary Santa Catarina River, sampling point 3 showed the highest concentration of total Hg, which was below the maximum concentration level of Hg (10 (g/L) set by the environmental regulations for wastewater effluents in Mexico [31]. The Santa Catarina River originates from the hills of Sierra La Huasteca and flows to the San Juan River in the State of Nuevo Leon, passing through the counties of Santa Catarina, San Pedro Garza Garcia, Guadalupe, Escobedo, Juarez and Cadereyta as well as the urban area of Monterrey. The high concentration observed in the river water could be related to anthropogenic wastewater releases by local residents and industry. The lowest Hg concentration in water samples was found in the Cuchillo reservoir (sampling point 11). This reservoir supplies domestic and industrial water to the MAM. In general terms, the average concentration of total Hg in the San Juan River watershed was not higher than the US EPA ambient surface water quality criteria (0.77-1.4 |ig/L) [30]. Furthermore, some of the sampling sites evaluated in this study, including sampling points 5, 6, 9, and 11, were below 0.5 |ig/L, which is the World Health Organization (WHO) guideline value for Hg in groundwater and surface waterbodies [32]. Sampling site 6 was located downstream La Silla River tributary and could contribute to dilute some of the contamination of the main stream of the San Juan River. Sampling site 6 was located downstream one of the three wastewater treatment plants established in 1994 by the government of the Estate of Nuevo Leon through the metropolitan area program "Monterrey Plan IV". The objective of this program was to eradicate pollution problems in the San Juan River watershed [20].

3.2 Sediment samples

Total Hg concentrations in sediment samples following acid digestion are shown in Table 3. Concentrations were expressed on a dry weight basis. The concentration of total Hg in sediments was fairly uniform across the study area. Total Hg concentrations ranged from 0.289 to 0.501 mg/Kg with a mean value of 0.405 ± 0.074 mg/Kg. As compared with other waterbodies, Hg concentrations in the San Juan River watershed sediment samples were higher than the concentrations of Hg reported in the Coatzacoalcos estuary (0.07-1.06 mg/Kg) [14]. However, a lower level of Hg in sediment samples was reported in the Papaloapan River Basin located in southern Veracruz, Mexico (0.027-0.090 mg/Kg) [12]. The lowest and highest content of total Hg in sediment samples were observed in the Santa Catarina River sampling site 1 and 2, respectively. However, the higher levels found at sampling site 2 were not surprising because this site was located in the immediate vicinity of the MAM. Hg accumulation in sediment from sampling site 2 could be attributed to industrial activities in this area. Despite of Hg accumulation nearby the MAM, Hg levels were within range for values reported for uncontaminated sediment samples (0.2-0.4 mg/Kg) [33]. In addition, the average concentration of Hg in sediment samples taken from this study area was below the maximum concentration criteria levels proposed by the US EPA for unpolluted sediments (<1 mg/Kg) [34]. These results suggest that local sediments have not yet been impacted severely by Hg contamination. By adopting the National Oceanic and Atmospheric Administration (NOAA's) screening reference guideline [35], the average Hg concentration in sediment samples from this study was in the category of moderately polluted sediments (0.15-1.30 mg/Kg). Although sediment quality criteria for Hg have been set in some countries [33, 35], it is necessary to evaluate the reactivity, solubility and potential bioavailability of Hg in sediments [36] (Table 2). The levels of Hg extracted from sediment samples can be seen in Fig. 2. The distribution of Hg in the fractions was similar across the sampling site locations. Results showed that Hg was mainly distributed in the non-mobile Hg fraction (0.29 ± 0.07 mg/Kg), which accounted for 71±10% of total Hg in sediments. The non-mobile fraction is related to elemental and strongly bound Hg compounds. The semi-mobile fraction of Hg represented nearly 9% of the total Hg (0.038 mg/Kg), whereas the mobile fraction represented 20±8% of total Hg. The mobile fraction contains most of the available fraction of Hg, including methylmercury (MeHg), thus making it the most toxic fraction. Total Hg content in this fraction corresponded to 0.079±0.028 mg/Kg of total Hg in sediments samples.





3.3 Association between hg and environmental parameters in the San Juan River watershed.

In this study, associations between Hg concentrations and several environmental factors were estimated using the Pearson's correlation coefficient (r). Correlation tests having P-values < 0.05 indicated strong association between tested variables. The statistical analysis revealed a highly significant positive correlation (p<0.01) between total Hg in sediments and the non- mobile Hg fraction (r=0.862).

There was a strong positive correlation (p<0.05) between total Hg levels in water samples and the semi-mobile Hg fraction in sediments (r=0.650). Pearson correlation analysis indicated that total Hg concentrations in water samples were negatively correlated with the redox potential measured in the samples (r=-0.660, p<0.05). However, Pearson's correlation analysis indicated that Hg levels in water samples were not associated with pH (r=0.195, p>0.05). The concentration of total Hg and MeHg in aquatic environment can be influenced by several physical and chemical parameters including temperature, pH, salinity, organic carbon, redox potential, bacterial activity, inorganic and organic complexing agents and organic matter content [37,38]. Alkaline pH waters and total Hg average concentrations below the US EPA ambient surface water quality criteria [30] were observed within the San Juan River Watershed. The weak correlation between Hg content and some physicochemical variables could indicate the influence of the local anthropogenic activities [39].

CONCLUSIONS

The San Juan River watershed was characterized by relatively low levels of Hg. The slightly higher Hg concentrations found at some monitoring points could be related to diffuse sources of Hg, such as anthropogenic and industrial activities. Concentrations of Hg in water samples varied from 0.17 to 1.14 |g/L and were below the maximum concentration for Hg established by the mexican environmental regulations. Additionally some of the physiochemical parameters such as pH, TDS and temperature exceeded the drinking water safety levels. On the other hand, Hg concentrations in surface sediments were very similar among all the sampling sites and ranged from 0.289 to 0.501 mg/ Kg. A significant amount of Hg in sediments was found to be associated with the non-mobile fraction that corresponds to a number of very stable chemical species with low mobility.

The study was conducted to help assess the need for a more comprehensive survey of Hg distribution in this ecosystem, which may eventually have an impact on the health of the nearly four-million inhabitant metropolitan area of Monterrey, known to harbor the largest metallurgical urban zone in northern Mexico.

ACKNOWLEDGEMENT

Financial support from Chemistry School of the Universidad Autonoma de Nuevo Leon is gratefully acknowledged. The authors thank IAEA for kindly providing the reference material. Also, thanks are given to Ing. Pedro Garza Treviño, Managing Director of CNA in Nuevo Leon, for his assistance in the field sampling. Laura H. Reyes acknowledges to Conacyt the financial support (grant 116627) through the Repatriation Program 2009.

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(Received: August 17, 2010 - Accepted: December 2, 2010)

Corresponding author: Juan Manuel Alfaro Barbosa. Tel: +52 (8220-4900), ext. 3461. Fax: +52 (8376-8553)