Journal of Water Resource and Protection
Vol.07 No.03(2015), Article ID:54205,8 pages
10.4236/jwarp.2015.73018

Trace Metal Concentration in Two Matrices in an Urban Subtropical River

Nyasha Mabika1, Trust Masiya2, Beaven Utete3*, Maxwell Barson4, Joshua Tsamba4

1Department of Anatomy, University of Zimbabwe, Harare, Zimbabwe

2Institute of Mining Research, University of Zimbabwe, Harare, Zimbabwe

3Department of Wildlife Ecology and Conservation, Chinhoyi University of Technology, Chinhoyi, Zimbabwe

4Department of Biological Sciences, University of Zimbabwe, Harare, Zimbabwe

Email: *beavenu@yahoo.co.uk, mkaiyo@gmail.com

Copyright © 2015 by authors and Scientific Research Publishing Inc.

This work is licensed under the Creative Commons Attribution International License (CC BY).

http://creativecommons.org/licenses/by/4.0/

Received 27 January 2015; accepted 22 February 2015; published 25 February 2015

ABSTRACT

This study investigates the concentration of metals namely aluminium, manganese and cobalt in two matrices: sediment and fish organs (whole muscle stomach tissue, gills, liver and kidney) in an urban river, Mukuvisi River, Zimbabwe. River bed sediments and fish samples were collected simultaneously at five sites over seven months (September 2008-April 2009). Concentrations of aluminium, manganese and cobalt in the selected fish organs and sediment were estimated using the Flame Atomic Absorption Spectrometry (FAAS). Water limnochemical aspects, dissolved oxygen, pH, temperature and conductivity were measured concomitantly at each site. Aluminium had significantly higher mean concentrations and bioconcentration factors in both sediments and fish tissues relative to cobalt and manganese. Cobalt and aluminium were detected in all fish tissues, whilst manganese was not detected in muscle and liver. Significant differences in bioconcentration factors for the metals in organs of the same fish species analysed in this study show differences in metal assimilation. Metal specific river rehabilitation methods need to be applied for the future restoration of the ecological integrity of Mukuvisi River.

Keywords:

Metal Assimilation, Bioconcentration Factors, Pollution, Ecosystem Integrity

1. Introduction

The chemistry of metals in sediments and water in rivers with respect to bio-availability to aquatic organisms and chemical reactivity is regulated by pH, texture, and organic matter contents, specific binding form and coupled reactivity of the metals [1] . Metals accumulate through the aquatic chain and their bioavailability is an indirect measure of potential toxicity [2] . Faced with rapid industrialization and an accelerating demotechnic growth, urban authorities deliberately discharge sewage and industrial effluent into urban streams [3] . This effluent contains metals which have potential deleterious impacts on the aquatic fauna [4] . In natural freshwater ecosystems most metals are typically present in low concentrations such that any increase in the levels of bio- available metals in the sediment and water phases may lead to an increase in the bioaccumulation of the metals in tissues of aquatic organisms [5] [6] .

Among the aquatic fauna, fish are most susceptible to heavy metal toxicants and are thus more vulnerable to heavy metal contamination than any other aquatic fauna [3] . When fish are exposed to elevated concentrations of metals in a polluted aquatic ecosystem, they tend to absorb these metals directly from their environments [7] [8] . After uptake, the metals are transported by the blood, where they are usually bound to proteins and brought into contact with the tissues and consequently accumulate in different tissues [9] [10] . The accumulated heavy metals may ultimately reach concentrations hundreds or thousands of times above those measured in the water, sediment and food [11] .

The Mukuvisi River, drain the greater part of the city of Harare, the most industrialized and urbanized city in Zimbabwe [12] . As a result, the river displays a gradient in pollution as most of the urban, agricultural and industrial run off uploads into it before it uploads into Lake Chivero Because of the threat of water pollution, several studies to monitor the water quality of Mukuvisi River have been done. However, most of these studies have focused on monitoring of the river integrity using resident aquatic organisms particularly macroinvertebrates [13] [14] , selected water quality parameters [15] - [18] , metazoan fish parasites [19] and selected heavy metals [20] , largely neglecting the essential and trace metal elements like manganese, aluminium and cobalt analysed in this study. The main objectives of this study were to investigate the concentration of aluminium, manganese and cobalt in the sediment phase and assess their potential bioavailability to the African catfish (Clarias gariepinus, Burchell 1822) in an urban river, Mukuvisi River, Zimbabwe.

2. Material and Methods

2.1. Sampling Sites

Five sampling sites were selected along the Mukuvisi River. The Seke Road Bridge was the first site. At this site, industrial effluent (from Graniteside and City Centre) and leachate from landfills are presumed to be discharged into the river. Site 2 was the Magaba bend industry. Effluent is expected to be discharged from the informal industry in the Magaba area into the river. Site 3 was Glen Norah where most of the effluent from the Southert on industry is discharged into the river. Site 4 was the Amalinda farm. Effluent from urban cultivation such as fertilizers and pesticides are leached into the river. Site 5 was pension farm where effluent from the Firle Sewage Treatment Plant is presumed to be discharged into the river. The sampled sites in the Mukuvisi River are shown in Figure 1.

2.2. Sample Collection

Sediment and fish were sampled at five selected sites in the Mukuvisi River once after every two months (from September 2008 to April 2009). Sampling occurred between 1000 and 1400 hours on all occasions to minimize variation due to climate factors. Sediment samples were collected using an acid-washed polyethene corer to a depth of 3 cm. At each sampling site three replicate samples were collected at an interval distance of 15 m. The sediments were stored in sterilized polyethene bags and returned to the laboratory in sealed containers containing ice packs for metal analysis. Live fish samples were collected at each site using 89 mm meshfyke nets and a DC electro fisher (Smith-Root Type IV-A). Electro fishing was done for 10 minutes at each sampling station.

2.3. Water Quality

Temperature, pH, conductivity and dissolved oxygen (DO) were measured in situ. Water temperature and DO were measured using a HACH oxygen 330i meter; pH and conductivity were measured using a HACH pH meter and WTW 330i conductivity meter, respectively. Water samples were analysed in the laboratory for total and reactive phosphorus (orthophosphate), total nitrogen, nitrate and ammonia. The nutrients were measured with a

Figure 1. Location of sampling sites in the Mukuvisi River.

HACH water analysis kit (HACH DR/2010 portable data logging spectrophotometer) using filtered water samples filtered through 0.45 μm Whatman GF 47 mm filters, except for total nitrogen and phosphorus analysis. The methods are described in detail in [21] .

2.4. Heavy Metals in Sediments

The two step acid digestion process used for the sediments is a strong digestion method and was chosen so that the total metal content could be estimated. Metals in the sediments were analysed using flame atomic absorption spectrophotometry (FAAS) [22] after acid digestion to extract the metals from the sediments. This procedure consisted of two parts:

1) Digestion: The sediments were oven-dried at 180˚C in a muffle furnace and large aggregates were broken up and then 20 ml nitric acid and 5 ml perchloric acid were added to 5 g of the oven-dried sample. The mixture was heated on a hot plate until fumes were produced and allowed to cool to room temperature.

2) Acidification: 20 ml of 50% hydrochloric acid was added to the mixture from the first digestion. The acidified mixture was heated until boiling and then was cooled to room temperature. The acidified mixture was filtered and distilled water was added to the filtrate in a volumetric flask up to the 100 ml mark. The digested sediments were then analysed for metal amounts in an atomic absorption spectrometer [22] .

2.5. Heavy Metals in Fish Tissues

In the laboratory, fish were dissected with clean autoclaved stain less teel instruments. One gram (wet weight) of gill, liver, kidney and muscle tissue of C. gariepinus was measured using an electronic balance. The tissues were placed into Petri dishes to dry at 120˚C until they reached a constant weight. Drygill, liver, kidney and muscle tissue were placed in digestion flasks to which 5 ml perchloric acid and 10 ml nitric acid were added. All acids used were of analytical grade quality. The digestion flasks were placed in an oven at 130˚C until all materials dissolved. The prepared tissue samples were analysed using flame atomic absorption spectrophotometry (FAAS).

2.6. Data Analysis

Spatial differences in limnochemical aspects of the water among sites sampled in the Mukuvisi River were investigated using Kruskall Wallis ANOVA at 5% level of significance respectively using Paleontological Statistics (PAST) software Version 190 [23] . The bioconcentration factor (BCF) was calculated after metal concentrations were determined for sediment and fish tissues. The BCF is defined in this study as the concentration of a metal in a fish tissue in relation to the concentration of that metal in the sediment surrounding that tissue, and was calculated using the formula [24] :

BCF values greater than 1000 are considered high and those under 250 low. Those between these extremes are classified as moderate. Differences in bioconcentration factors were assessed using the Kruskall Anova at 5% significance level.

Canonical correspondence of the metal concentration in the sediment and fish tissue to water limnochemistry was analysed using CANOCCO 5 [25] .

3. Results

3.1. Limnochemistry of the Mukuvisi River

The pH of the water at all sites sampled in the Mukuvisi River was slightly acidic to alkaline (6.1 - 7.3) during the period of study, only site 1 had a pH below the lower limit accepted for effluent and river water (Table 1). The mean temperature varied with the time of sampling ranging from 20.8˚C to 22.1°C. Conductivity readings were above 540 µS∙cm−1 at all sites. Dissolved oxygen was highest at site 2 (5.0 mg∙l−1) and lowest at site 5(1.1 mg∙l−1). Phosphate levels exceeded the WHO limits (0.5 mg∙l−1), whilst nitrate levels remained within the acceptable limits of 10.0 mg∙l−1. The highest levels of ammonia were recorded at site 3 (0.18 mg∙l−1) whilst the lowest levels were recorded at site 1 (0.03 mg∙l−1). There were significant differences (Kruskall ANOVA; p < 0.05) in the concentration of D.O, RP and TP among sites sampled in the Mukuvisi River.

3.2. Metal Concentration in Mukuvisi River Bed Sediment and Catfish Tissues

All the three metals (Al, Mn and Co) were recorded in sediments at all sites (Table 2). Aluminium had the highest concentrations in the sediments followed by manganese. The levels of aluminium ranged from 17.20 - 215.00 mg∙kg−1 in sediments. Manganese levels ranged from1.44 - 72.40 mg∙kg−1, whilst the levels of cobalt ranged from 0.20 - 2.85 mg∙kg−1. No fish were collected from sites 1 and 5 (Table 2). Aluminium was not detected in gills and kidney on site 3, whilst manganese was not detected in fish muscle and liver. Manganese was not detected in the kidney on sites 2 and 3. Cobalt was not detected in the liver on sites 2 and 3. Aluminium ranges in the fish tissues were; muscle (0.27 - 1.18 µg∙g−1), gill (ND-1.35 µg∙g−1), kidney (ND-2.7 µg∙g−1), liver (0.06 - 1.13 µg∙g−1). Manganese ranges in the fish tissues were; gill (0.15 - 0.85 µg∙g−1), kidney (0.10 - 0.30 µg∙g−1), whilst cobalt ranges were; muscle (0.01 - 0.1 µg∙g−1), gill (0.02 - 0.13 µg∙g−1), kidney (0.01 - 0.08 µg∙g−1) and liver (0.03 - 0.05 µg∙g−1). The prominence (hierarchical ranking) order of mean concentration of metals in the sediments was; Al > Mn > Co. Prominence order of metals in the muscles and liver of the catfish was; Al > Co >Mn, whilst in the gills and kidneys it was; Al >Mn> Co (Table 3).

Metal accumulation pattern (bioconcentration factors) differed for each organ analysed and comprised of the following pattern: Aluminium: Liver > Gill > Muscle > Kidney, Manganese: Kidney > Gill > Liver > Muscle and for Cobalt: Liver > Muscle = Kidney > Gill (Table 4). Aluminium had the highest bioconcentration factors

Table 1. Water quality parameters in sites sampled in the Mukuvisi River. DO = Dissolved oxygen, RP = Reactive phosphorous, TP = Total phosphorous, TN = Total nitrogen. EMA and WHO [35] threshold levels are highlighted.

Table 2. Ranges, mean ± SD of the concentrations of Al, Mn and Co in sediments (mg∙kg−1/ppm) and tissues (µg∙g−1/ppm) of C. gariepinus.

Note: ND: not detected, Rs: ranges, M: mean.

Table 3. Summary of mean ± SD concentrations of metals in sediments (ppm or mg∙kg-1) and fish tissues (ppm or µg∙g-1).

Note: ND: Not detected.

Table 4. Bioconcentration factors of Al, Mn and Co from sediments to selected catfish tissues in Mukuvisi River.

in all organs of the catfish analysed except in the kidney where Mn had a significantly higher bioconcentration (Table 4). There was a significant difference (ANOVA, p < 0.05) in the bioconcentration the three metals from the sediments into the catfish stomach muscles and liver.

Canonical correspondence analyses show that there was a strong association in aluminum concentration in the kidney, liver and gill of the catfish with the levels of DO and TN in water in Mukuvisi River particularly at site 2, whilst there is a strong association of Al concentration in the catfish muscles with nitrate levels in the water at Mukuvisi site 1. The first two axes explain 87.61% of the variation in Al concentration in the catfish tissues sampled (Figure 2). A narrow angle of attachment shows that temperature; conductivity and ammonia values were closely linked in the water phase in Mukuvisi River. The correspondence analysis for manganese was not valid as the number of ND non-detectable values in the catfish tissues which were treated as missing figures or zeros exceeded the possible explanatory variables (water limnochemical parameters). Figure 3 shows that the cobalt concentration in the muscle and gill of the catfish had a strong association with the nitrate, ammonia and DO values in the Mukuvisi River. Cobalt concentration in the kidney and liver of the catfish sampled in the Mukuvisi River had a strong association with the RP values in the water. The first two axes explain only 64.13% of the variation in the concentration of Co concentration in the catfish tissues analysed in this study. A narrow angle of attachment shows that temperature, conductivity and TN values are closely related in the water phase in Mukuvisi River (Figure 3).

4. Discussion

The objectives of this study were to investigate the concentration of Al, Co and Mn in two matrices: sediments and selected fish tissues of the African catfish Clarias gariepinus, Burchell 1822, in a subtropical urban river, Mukuvisi River, and assess potential bioavailability of metals to the fish. Results show Al, Co and Mn contamination in sediments and fish tissues. This contamination is attributed to localized pollution sources along the Mukuvisi River mainly automobile and detergent manufacturing industries which directly discharge metal laden effluent into the river [13] [20] . Al, Co and Mn concentrations in sediments were significantly higher relative to fish tissues. This is expected as sediments act both as a source and a sink for metals [26] . However, an elevated concentration of metals in sediments translates to increased potential bioavailability to resident aquatic fauna [27] . For instance, aluminium which has highest concentration in sediments among the three metals we analysed

Figure 2. Correspondence analyses of the Al concentration in catfish tissues and selected water limnochemical parameters in sites sampled in the Mukuvisi River.

Figure 3. Correspondence analyses of the Co concentration in catfish tissues and selected water limnochemical parameters in sites sampled in the Mukuvisi River.

has a higher bioconcentration factor in all the fish tissues except in the kidneys where Mn had the highest bioconcentration factors. An increased bioavailability of a metal is not problematic as long as the lethal dose limit is not exceeded [28] .

Significant differences in bioconcentration factors for the metals in organs of the same fish species analysed in this study show differences in metal assimilation. Metal assimilation in an aquatic organism corroborates closely with its specific binding form (species/fraction), chemical reactivity, and depuration [29] . Aluminium has a range of species but the most assimilated fractions by freshwater aquatic organisms are the Al2+ and Al3+ ions [30] . Speciation modelling of the assimilation and toxicity of Al to freshwater fish has been correlated to the water limnochemistry particularly the concentration of dissolved organic carbon, dissolved oxygen levels and pH [30] [31] . In this study correspondence analysis shows that Al levels in the sediment and fish tissue matrices is strongly associated with the concentrations of dissolved oxygen (DO), total nitrogen (TN) and nitratesin the water phase in the Mukuvisi River.

Manganese is a toxic element frequently overlooked when assessing the toxicity of sewage and industrial effluents, sediments and pore waters [32] [33] . Manganese exists in different fractions but the most assimilated form is the Mn2+ ion in freshwater [32] . Several authors have correlated the rapid assimilation and acute toxicity of Mn2+ ion in freshwater organisms to stochastic shifts in pH, as well as DO concentration. In well aerated waters with slightly alkaline pH (pH > 7), Mn2+ concentration is low in lotic systems due to redox equilibrium reactions that favour its conversion to the less toxic Mn (IV) fraction which is easily sequestered into insoluble Mn oxides [32] [33] . Manganese analyses show non-detectable (ND) incidences at most sites in both the sediment and fish matrices in the Mukuvisi River. This could be due to the rapid conversion of the highly reactive and radical Mn2+ ion into the insoluble Mn (IV) fraction which is assimilated by aquatic organisms as it is an essential element. Hence we could not investigate the possible relation between Mn concentration in the sediments and fish tissues to the levels of water limnochemistry parameters.

Elevated concentrations of Co were observed in the sediments mainly at Mukuvisi site 1 and in the liver of the catfish. The elevated concentrations of cobalt at site 1 can be attributed to the industrial effluent discharge from Graniteside Industrial Area and City Centre and leachate from adjacent landfills [20] . Cobalt is an essential metal vital for flora and fauna as it forms the backbone of the cofactors in most vitamins. However, elevated concentrations in aquatic systems can be detrimental to the fauna as elevated cobalt (particularly Co2+ ion) toxicity has been demonstrated to lungs, heart and skin of amphibians and fish [34] . Toxicity and assimilation of cobalt have been correlated to water pH and water hardness [34] . For our study the cobalt concentration in the sediment and the fish tissues (kidney and liver) of the catfish sampled in the Mukuvisi River had a strong association with the RP values in the water.

Results from this study demonstrate metal (Al, Co and Mn) contamination in the sediment and fish tissue matrices in the Mukuvisi River. Furthermore there is accumulation/bioconcentration of Al, Co and Mn in catfish tissues thus indicating their potential toxicity. In addition our analyses show that there is possible association and relation of Al and Co concentration in sediments and catfish tissues to the stochastic levels of water limnochemical parameters in the Mukuvisi River. Although the lack of metal fraction analyses and the specific sediment toxicity tests underestimate the risks associated with each metal, use of total components in the analysis of metal contamination in sediment and fish tissues provides a useful river integrity assessment option for management. In future studies there is need for both single and multispecies sediment toxicity tests for any specified metal, and metal specific river rehabilitation methods need to be applied for the rehabilitation and restoration of the Mukuvisi River.

Acknowledgements

The laboratory and field assistance of Elizabeth Munyoro is greatly appreciated.

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NOTES

*Corresponding author.

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