# Assessment of Levels, Speciation, and Toxicity of Trace Metal Contaminants in Selected Shallow Groundwater Sources, Surface Runoff, Wastewater, and Surface Water from Designated Streams in Lake Victoria Basin, Uganda

Authors: G. K. Bakyayita; A. C. Norrström; R. N. Kulabako
Journal: Journal of Environmental and Public Health
 (2019)

---

## Abstract

The levels, speciation of elements, and toxicity of selected trace metals as well as other parameters in selected surface water, shallow groundwater sources, landfill leachate, and associated surface runoff in the Lake Victoria basin, Uganda, were studied. The WHO guidelines, Ugandan standards, Canadian guidelines and Swedish EPA were used for assessment. The shallow groundwater was acidic with pH values below 6.5. The pH, dissolved organic carbon, flouride, and sulphate levels for all springs were below the guideline values although 52.8% was contaminated with nitrates while 39% was contaminated with chloride ions. Some surface water samples had levels of major elements, such as iron, chromium, aluminium, and manganese, above the guideline values. Speciation studies showed that 74% of the metal ions was bound to dissolved organic matter in surface water, whereas in landfill leachates, the dominant ionic species was metal hydroxides or fulvic acid bound. Risk analysis based on the Swedish EPA showed varied risks of negative effects in 30%–76% of the sample sites ranging from high to increased risk in surface water, whereas the results from modelling sorption data using the Bio-met tool showed potential risk to toxicity effects of Cu2+, Ni2+, Zn2+, and Pb2+ in 15.3%–30.8% surface water samples and 8.3%–62.5% groundwater samples.


---

## Body

## 1. Introduction

The presence of heavy metals and other pollutants in the aquatic systems has become a serious problem for environmental scientists in many developing countries and also for agencies engaged in environmental production [1]. Freshwater resources constitute only about 2.5% of the total volume of water on Earth (∼1.4 million·km3), and only about 0.01% (200,000 km3) of all the water on Earth is usable freshwater for ecosystems and humans [2]. While the freshwater volume remains generally constant, the population using the water continues to rise, stressing this supply more critically each year [3]. Freshwater is therefore a meagre resource whose quality is very difficult and costly to reverse to pristine and usable condition when it deteriorates [4]. Uganda is a developing country that is home to the source of the River Nile which is the longest river in the world that moves 6,850 km to the Mediterranean Sea from Lake Victoria. Lake Victoria is the second largest freshwater lake in the world with a surface area of 68,800 km2 and a volume of 2,760 km3 [5]. The Nile river basin covers almost 10% of the total area of the African continent with an area of 3,100 km2 [6]. There are eleven countries that make up the Nile River drainage basin, namely, Rwanda, Burundi, Democratic Republic of Congo, Uganda, South Sudan, Sudan, Kenya, Tanzania, Ethiopia, Eritrea, and Egypt. Some of those riparian countries only have a small part of their area within the basin while others are located virtually entirely within the basin [5]. Nile River drainage basin serves the domestic, industrial, and agricultural needs over 150 million people. The Lake Victoria basin, Uganda, forms a bigger part of the upper Nile basin that covers much of Uganda where it serves over 36 million people. There are socioeconomic as well as industrial activities of the urbanizing region with consequential unprecedented anthropogenic contamination of the basin’s surface water system which may eventually irreversibly impact the shallow aquifers. The extent of anthropogenic environmental pollution in the developing world is well documented [7]. Geologically, Uganda is dominated by crystalline rocks which are covered by regolith, a layer of the weathered material that varies from rock fragments to well-weathered soil and hardened laterite at the ground surface [8]. The British Geological Survey [8] reported that groundwater is abstracted from both the fractured bedrocks and the weathered regolith. According to Taylor and Howard [9], the regolith aquifer is a reusable resource due to its promising yields and lower cost of development than the deeper groundwater from the basement. However, the commonest groundwater sources in Kampala abstract water from shallow aquifers through protected and unprotected springs. Spring waters are the least mineralised with compositions approaching those of the surface waters [10] which indicate that groundwater in shallow aquifers discharges fast with minimum chemical interactions with aquifer minerals. The shallow aquifers are prone to contamination from anthropogenic sources due to unorthodox handling and management practices for domestic, municipal, and industrial wastes and wastewater. For instance, the unlined landfills for the urban wastes are located in wetlands and pollute the aqueous environment with noxious gases and leachate. Muwanga and Balifaijo [11] revealed that industrial effluents were one of the main sources of pollution in the Lake Victoria basin, Uganda. Kulabako et al. [12] indicated that the quality of the shallow groundwater in periurban areas is a potentially major environmental health problem, and Howard et al. [13] observed that the consumption of contaminated drinking water in the densely populated periurban areas is one of the most significant causes of ill-health. Relatively little data are available on the extent of environmental pollution because there are no agencies charged with the routine monitoring and protection of the environment [14]. Therefore, the assessment of levels and speciation of toxic trace metal contaminants in shallow groundwater, surface runoff, and surface water from selected waterways would reveal the state of environmental health of the shallow aquifers associated with them.Trace metals are always present in trace amounts in fresh waters from terrigenous sources such as weathering of rocks resulting in geochemical recycling of heavy metal elements in these ecosystems [15, 16], but Sekabira et al. [17] observed that heavy metal pollution of aquatic ecosystems is becoming a potential global problem. Inadequate waste handling and management systems as well as the release of untreated dumpsite leachate and industrial effluent to the environment have significantly contaminated wetlands, surface water, and groundwater which affect the proper functioning of the aquatic ecosystems and endanger aquatic life especially when the pH is low. Studies on an urban open drain Nakivubo Channel have indicated high concentration of toxic trace metals in water and the soils in the near-stream zone that are flooded with contaminated water [18, 19]. Moulodi and Thorsell [20] observed that infiltration is however taking place by localized recharge of different types of wastewater in the periurban areas, which has a clear negative impact on the quality of water resources. The contamination of land and surface water ecosystems with trace metals will continuously threaten the aquifers and shallow groundwater resources for a long time. The environmental health effects of trace metal contaminants are manifested after chronic exposure to low levels or acute exposure to high doses of trace metals. Trace metals are grouped into essential and nonessential trace metals depending on their biological importance. The essential trace metals are those that have known biological roles in living organisms, whereas the nonessential trace metals interfere with the uptake of the essential ones and have known toxicity to life processes. Trace metals such as cadmium, mercury, lead, copper, and zinc are regarded as serious pollutants of aquatic ecosystems due to their environmental persistence, toxicity, and ability to be incorporated into food chains [21]. Essential trace metals such as zinc show toxicity effects when ingested in excess of the optimal levels or in insufficient amounts to bodily needs, whereas nonessential trace metals such as lead and cadmium express toxicity effects when taken in above the tolerable levels.The major anthropogenic sources of trace metals are combustion of fossil fuels, sewage sludge, and waste dumpsite leachates as well as the wearing of car tyres, brake pads, bearings, radiators [22], mining, smelting, and processing industries. The high concentrations of trace metals are attributed to wastes and industrial effluent deposited in the environment which may result from wearing of machines, smith workshop waste, motor service centres, surface runoff, and industrial chemicals. The main recipient of these metals is the soil, and their fate depends on the chemical and physical properties of the metal or its compounds, soil type, and its organic matter content. Adsorption onto soil particles and soil organic matter causes retention of trace metals and reduces their transmission to the soil water, but when the soil is overladen or when the soil pH is lowered, trace metals’ vertical mobility increases and contamination of groundwater occurs through the soil solution. Consequently, the trace metal contaminants may show toxicity effects on fauna since the flora are more tolerant to high levels of trace metals.The aim of this study was to assess the levels of major and trace elements and establish the speciation of selected trace elements in the aqueous environment of selected shallow groundwater, surface runoff, surface water, landfill leachate, and wastewater in several subcatchment areas in Lake Victoria basin, Uganda. The other objective of the study was to risk assessment for selected trace elements in designated surface water and shallow groundwater sources to inform policy and action on remediation and protection of environmental health. The speciation of trace elements in the aqueous environment will show the distribution of the different metal species amongst metal ions bound to organic species, free metal ions, and inorganic metal ions which would have different effects on environmental mobility, distribution, and life support systems.


## 2. Materials and Methods

### 2.1. Study Area and Sampling Sites

The study area is the Lake Victoria basin, Uganda, with sampling points on streams (Figure1) and protected springs (Figure 2). Some of the coordinates of the sampling points mapped in Figures 1 and 2 are shown in Table 1. The streams, protected springs, and landfill leachate that were sampled and studied are within in the catchment areas associated with Lake Victoria basin and are located in Kampala Capital City (Figure 2) which is the country’s most industrialized business district. The choice of the sampling points in the study area was based on the resident population density and anthropogenic activities in the area, dependence of the population on the shallow groundwater, and surface water sources as well as logistics and time limitations.Figure 1
Map of Uganda showing the sampling sites for surface water from urban and rural waterways.Figure 2
Map of Kampala city showing shallow groundwater and surface runoff sampling sites.Table 1
Coordinates of some of the sampling points that were plotted on the maps in Figures1 and 2 using ArcGIS.
Sample site
Latitude (N)
Longitude (E)
Units
° (degrees)
′ (minutes)
″ (seconds)
° (degrees)
′ (minutes)
″ (seconds)
Katarina
00
20
58
32
37
48
Nabuze
00
20
38
32
38
28
Buwooya
00
21
30
32
38
0
Bukoto 1
00
21
29
32
36
0
Bukoto 2
00
21
10
32
35
3
Nabukalu
00
21
30
32
33
4
Abdu
00
21
0
32
33
0
SP4306K
00
20
5
32
33
0
Kikoni
00
19
53
32
33
4
SP1414R
00
20
44
32
32
0
Sentamu
00
20
40
32
32
0
Kunnya
00
20
10
32
32
0
SP5003C
00
19
26
32
34
0
SP1212R
00
20
0
32
32
0
Kibumbiro
00
19
10
32
31
2
Kabaale
00
18
40
32
31
0
Nababirye
00
19
36
32
32
10
SP1010R
00
20
37
32
33
24
Kapeke
00
17
47
32
34
5
Yusuf
00
18
10
32
34
5
Kasanvu
00
18
25
32
36
45
Nsambya
00
18
29
32
36
45
Nabagereka
00
18
40
32
34
9
Barracks
00
19
11
32
34
10
Lubigi
00
21
01
32
33
56
Mulago
00
20
44
32
34
11
Nakivubo
00
18
56
32
35
43
Lugogo
00
19
19
32
36
34
Bugoloobi
00
19
07
32
37
0
Kiteezi
00
24
49
32
34
37


### 2.2. Water Sampling

The shallow groundwater from protected springs was drawn as it discharged from shallow aquifers. The sampling of shallow groundwater was done four times, once each year from March 2012 to February 2015. Surface runoff that flowed and settled in the catchment areas associated with the protected springs was trapped in shallow patches from which grab samples were picked thirty minutes after the onset of heavy downpours of the wet season, from September to October 2013. Three grab samples were picked and homogenised before a representative sample was taken for analysis. The surface runoff was sampled because there is a risk of intrusion to the shallow aquifers since during wet seasons the water table rises and increases probabilities of surface water and shallow groundwater mixing. The surface runoff assessment is therefore a basic and meaningful part of hydrological studies. The surface water samples from urban and rural waterways as well as leachate samples from unlined landfills were picked at points 1 m from the peripheral at depths within 0.5 m of the surface. The water samples were collected from the sample sites in 500 mL plastic bottles that had been prewashed thrice using sample water prior to collection. Water samples were filtered through 0.45µm nonpyrogenic syringe filters and stored in 30 mL polypropylene vials. The pH, temperature, and electrical conductivity were measured at the point of collection of samples. The samples were placed in cooler boxes and transferred to the analytical laboratory.For streams, the sampling was done twice in June 2014 and February 2015. The plastic bottles used for collection of water samples were cleaned and rinsed twice with the water to be sampled before use. Field measurements of pH, temperature, and electrical conductivity (EC) were measured using a pH Ion meter. The water samples for determination of DOC were filtered into sample bottles using 0.45µm filters and cooled before being transferred to the laboratory. The water samples were subsampled twice; one sample was filtered and cooled, while the sample for trace metals analysis was filtered and acidified with concentrated nitric acid before being transferred to the analytical laboratory at room temperature (25°C).


### 2.3. Metals, Anions, and DOC Analyses

The acidified water samples were subsequently analysed for trace and major elements using an inductively coupled plasma-mass spectrometer (ICP-MS) (2007, Model: PerkinElmer Elan 9000) with an instrument limit of detection of 0.002 ppm for cadmium and 0.009 ppm for lead, whereas the samples for DOC and anions analysis were evaluated using the Shimadzu TOC-5000 without acidification. The leachate samples were digested using the wet acid digestion procedure. Pretreatment of 50 ml of leachate was done with 2 ml nitric acid, and 5 drops of 30% hydrogen peroxide were added in a closed bottle and placed in a constant temperature water bath at 60°C for 1 hour. The clear supernatant was filtered through 0.45µm filters into plastic sample bottles and analysed for cations, whereas the samples for DOC and anions analysis were only filtered before analysis. The analyses were done over a period of three years, and mean values of the measurements have been reported. The major anions Cl−, NO3−, and SO42− were analysed at KTH, Stockholm, using a Dionex DX-120 ion chromatograph.


### 2.4. Speciation and Toxicity Studies

The chemical species distribution in organic and inorganic phases would impact on the sorption process since the metal ions in the free ionic state and inorganic state would be available for sorption onto biosorbents and would also be important for toxicity studies. The speciation of selected trace metals was performed with Visual MINTEQ 3.1, and risk assessment of trace metals to aquatic fauna was done by comparison with the Swedish environmental guidelines for selected shallow groundwater and surface water samples. Pb2+ and Cd2+ ions speciation in selected contaminated surface water and leachate at various conditions of DOC and pH was performed with Visual MINTEQ 3.1 which was originally coded by the U.S. Environmental Protection Agency (EPA) and has been further developed by Gustafsson [23, 24]. For the speciation studies of the metal ions in selected surface water, the Stockholm Humic Model (SHM) was used. The assumption used by the US EPA in setting the Water Quality Criteria in which all DOC in natural waters was considered to be active and organic matter consisted of 90% fulvic acid and 10% humic acid was adopted in these studies. Toxicity studies were done by assessing the environmental risks due to trace elements through modelling using the Bio-met software tool. The Bio-met software tool version 4 is based on calculations from Biotic Ligand Models (BLM) to estimate the potential risk to the aquatic environment posed by copper, nickel, zinc, and lead after considering bioavailability. The basis of biotic ligand modelling is that metal accumulation at the “biotic ligand” is proportional to toxicity and that this accumulation can be predicted by solving the appropriate simultaneous equilibria among the biotic ligand(s) and the dissolved components (aqueous ligands and competing cations) in the exposure water [25]. Data analysis for environmental risks due to trace metals was done using the Swedish environmental protection agency criteria and the bioavailability-based approach through simulations using the biotic ligand model and the Bio-met software tool.In Figure3, a remodified schematic diagram of the biotic ligand model (BLM) has been presented that explains the assumptions and interactions between the inorganic, organic, and biotic ligands in the aqueous media. These interactions are shown in Figure 3 with the free metal ion, M2+, and naturally occurring competitive cations, Na+, H+, Mg2+, and Ca2+, and abiotic ligands by DOC, CO32−, HCO3−, OH−, and Cl−, whereas the site toxic action is represented by the biotic ligand or test organism under study. According to the conceptual framework of the BLM, the accumulation of the metal ions at the biotic ligand or greater than a critical threshold concentration of metal ions onto the biotic ligand leads to toxicity effects. BLMs allow chemical and biological interactions to be taken into account and relate, through water chemistry, metal toxicity to a dissolved concentration which can be used in the compliance assessment [27].Figure 3
Remodified schematic diagram of the biotic ligand model. M2+ is the free metal ion (after [26]).


## 2.1. Study Area and Sampling Sites

The study area is the Lake Victoria basin, Uganda, with sampling points on streams (Figure1) and protected springs (Figure 2). Some of the coordinates of the sampling points mapped in Figures 1 and 2 are shown in Table 1. The streams, protected springs, and landfill leachate that were sampled and studied are within in the catchment areas associated with Lake Victoria basin and are located in Kampala Capital City (Figure 2) which is the country’s most industrialized business district. The choice of the sampling points in the study area was based on the resident population density and anthropogenic activities in the area, dependence of the population on the shallow groundwater, and surface water sources as well as logistics and time limitations.Figure 1
Map of Uganda showing the sampling sites for surface water from urban and rural waterways.Figure 2
Map of Kampala city showing shallow groundwater and surface runoff sampling sites.Table 1
Coordinates of some of the sampling points that were plotted on the maps in Figures1 and 2 using ArcGIS.
Sample site
Latitude (N)
Longitude (E)
Units
° (degrees)
′ (minutes)
″ (seconds)
° (degrees)
′ (minutes)
″ (seconds)
Katarina
00
20
58
32
37
48
Nabuze
00
20
38
32
38
28
Buwooya
00
21
30
32
38
0
Bukoto 1
00
21
29
32
36
0
Bukoto 2
00
21
10
32
35
3
Nabukalu
00
21
30
32
33
4
Abdu
00
21
0
32
33
0
SP4306K
00
20
5
32
33
0
Kikoni
00
19
53
32
33
4
SP1414R
00
20
44
32
32
0
Sentamu
00
20
40
32
32
0
Kunnya
00
20
10
32
32
0
SP5003C
00
19
26
32
34
0
SP1212R
00
20
0
32
32
0
Kibumbiro
00
19
10
32
31
2
Kabaale
00
18
40
32
31
0
Nababirye
00
19
36
32
32
10
SP1010R
00
20
37
32
33
24
Kapeke
00
17
47
32
34
5
Yusuf
00
18
10
32
34
5
Kasanvu
00
18
25
32
36
45
Nsambya
00
18
29
32
36
45
Nabagereka
00
18
40
32
34
9
Barracks
00
19
11
32
34
10
Lubigi
00
21
01
32
33
56
Mulago
00
20
44
32
34
11
Nakivubo
00
18
56
32
35
43
Lugogo
00
19
19
32
36
34
Bugoloobi
00
19
07
32
37
0
Kiteezi
00
24
49
32
34
37


## 2.2. Water Sampling

The shallow groundwater from protected springs was drawn as it discharged from shallow aquifers. The sampling of shallow groundwater was done four times, once each year from March 2012 to February 2015. Surface runoff that flowed and settled in the catchment areas associated with the protected springs was trapped in shallow patches from which grab samples were picked thirty minutes after the onset of heavy downpours of the wet season, from September to October 2013. Three grab samples were picked and homogenised before a representative sample was taken for analysis. The surface runoff was sampled because there is a risk of intrusion to the shallow aquifers since during wet seasons the water table rises and increases probabilities of surface water and shallow groundwater mixing. The surface runoff assessment is therefore a basic and meaningful part of hydrological studies. The surface water samples from urban and rural waterways as well as leachate samples from unlined landfills were picked at points 1 m from the peripheral at depths within 0.5 m of the surface. The water samples were collected from the sample sites in 500 mL plastic bottles that had been prewashed thrice using sample water prior to collection. Water samples were filtered through 0.45µm nonpyrogenic syringe filters and stored in 30 mL polypropylene vials. The pH, temperature, and electrical conductivity were measured at the point of collection of samples. The samples were placed in cooler boxes and transferred to the analytical laboratory.For streams, the sampling was done twice in June 2014 and February 2015. The plastic bottles used for collection of water samples were cleaned and rinsed twice with the water to be sampled before use. Field measurements of pH, temperature, and electrical conductivity (EC) were measured using a pH Ion meter. The water samples for determination of DOC were filtered into sample bottles using 0.45µm filters and cooled before being transferred to the laboratory. The water samples were subsampled twice; one sample was filtered and cooled, while the sample for trace metals analysis was filtered and acidified with concentrated nitric acid before being transferred to the analytical laboratory at room temperature (25°C).


## 2.3. Metals, Anions, and DOC Analyses

The acidified water samples were subsequently analysed for trace and major elements using an inductively coupled plasma-mass spectrometer (ICP-MS) (2007, Model: PerkinElmer Elan 9000) with an instrument limit of detection of 0.002 ppm for cadmium and 0.009 ppm for lead, whereas the samples for DOC and anions analysis were evaluated using the Shimadzu TOC-5000 without acidification. The leachate samples were digested using the wet acid digestion procedure. Pretreatment of 50 ml of leachate was done with 2 ml nitric acid, and 5 drops of 30% hydrogen peroxide were added in a closed bottle and placed in a constant temperature water bath at 60°C for 1 hour. The clear supernatant was filtered through 0.45µm filters into plastic sample bottles and analysed for cations, whereas the samples for DOC and anions analysis were only filtered before analysis. The analyses were done over a period of three years, and mean values of the measurements have been reported. The major anions Cl−, NO3−, and SO42− were analysed at KTH, Stockholm, using a Dionex DX-120 ion chromatograph.


## 2.4. Speciation and Toxicity Studies

The chemical species distribution in organic and inorganic phases would impact on the sorption process since the metal ions in the free ionic state and inorganic state would be available for sorption onto biosorbents and would also be important for toxicity studies. The speciation of selected trace metals was performed with Visual MINTEQ 3.1, and risk assessment of trace metals to aquatic fauna was done by comparison with the Swedish environmental guidelines for selected shallow groundwater and surface water samples. Pb2+ and Cd2+ ions speciation in selected contaminated surface water and leachate at various conditions of DOC and pH was performed with Visual MINTEQ 3.1 which was originally coded by the U.S. Environmental Protection Agency (EPA) and has been further developed by Gustafsson [23, 24]. For the speciation studies of the metal ions in selected surface water, the Stockholm Humic Model (SHM) was used. The assumption used by the US EPA in setting the Water Quality Criteria in which all DOC in natural waters was considered to be active and organic matter consisted of 90% fulvic acid and 10% humic acid was adopted in these studies. Toxicity studies were done by assessing the environmental risks due to trace elements through modelling using the Bio-met software tool. The Bio-met software tool version 4 is based on calculations from Biotic Ligand Models (BLM) to estimate the potential risk to the aquatic environment posed by copper, nickel, zinc, and lead after considering bioavailability. The basis of biotic ligand modelling is that metal accumulation at the “biotic ligand” is proportional to toxicity and that this accumulation can be predicted by solving the appropriate simultaneous equilibria among the biotic ligand(s) and the dissolved components (aqueous ligands and competing cations) in the exposure water [25]. Data analysis for environmental risks due to trace metals was done using the Swedish environmental protection agency criteria and the bioavailability-based approach through simulations using the biotic ligand model and the Bio-met software tool.In Figure3, a remodified schematic diagram of the biotic ligand model (BLM) has been presented that explains the assumptions and interactions between the inorganic, organic, and biotic ligands in the aqueous media. These interactions are shown in Figure 3 with the free metal ion, M2+, and naturally occurring competitive cations, Na+, H+, Mg2+, and Ca2+, and abiotic ligands by DOC, CO32−, HCO3−, OH−, and Cl−, whereas the site toxic action is represented by the biotic ligand or test organism under study. According to the conceptual framework of the BLM, the accumulation of the metal ions at the biotic ligand or greater than a critical threshold concentration of metal ions onto the biotic ligand leads to toxicity effects. BLMs allow chemical and biological interactions to be taken into account and relate, through water chemistry, metal toxicity to a dissolved concentration which can be used in the compliance assessment [27].Figure 3
Remodified schematic diagram of the biotic ligand model. M2+ is the free metal ion (after [26]).


## 3. Results and Discussion

The levels of major elements in shallow groundwater, surface runoff, landfill leachate, wastewater, and surface water were analysed and studied with the guidance of WHO guideline values, Ugandan standards, and the Swedish Environmental Protection Agency guideline values [28–30]. According to the WHO guidelines, the results for selected protected springs in Kampala which are shown in Tables 2 and 3 indicate that 58% of the sampled protected springs are contaminated with Fe which exceeds 0.3 mg/l in the range 0.34–1.86 mg/l. This exceedance of the guideline value can be attributed to weathering, and a clear testimony is observed with surface water in the corresponding wetlands having a rusty flimsy layer in slow and stagnant waters. The results for Fe are in agreement with the report by BGS [8] where it was stated that iron was one of the main inorganic groundwater quality problems. Iron is mainly transported in groundwater in the reduced form as Fe2+. Therefore, the main source of Fe contamination appears to be background levels in the soils where acidic and redox conditions enhance release of Fe and Mn into soil water. There were only 4% of the springs that had Cr levels above the 0.05 mg/l level.Table 2
Major elements (mg/L) in water from selected protected springs in Kampala city (n=3, ±standard deviation) compared with WHO guideline values and the Ugandan standards [28, 30].
WHO guideline values
Na
Mg
Al
K
Ca
Cr
Mn
Fe
200
100
0.2
10
200
0.05
0.4
0.3
Ugandan standards
200
50
0.1
—
75
0.05
0.1
0.3
Sample site
Nakawa division
Nabuze
23 ± 0.3
4.7 ± 1.2
0.002
3.6 ± 0.4
11.6 ± 1.3
0.051 ± 0.004
0.14 ± 0.01
0.3 ± 0.01
Katarina
14 ± 0.6
2.2 ± 0.7
0.002
4.4 ± 0.5
6.7 ± 0.8
0.020 ± 0.006
0.02 ± 0.01
0.2 ± 0.01
Buwooya
10 ± 1.5
1.8 ± 0.2
0.191
3.6 ± 0.3
5.7 ± 1.5
0.021 ± 0.003
0.02 ± 0.01
0.7 ± 0.03
Bukoto 1
10 ± 1.2
1.3 ± 0.3
0.098
2.6 ± 0.2
4.9 ± 1.0
0.012 ± 0.007
0.06 ± 0.02
0.5 ± 0.02
Bukoto 2
23 ± 1.2
2.0 ± 0.4
0.360
5.7 ± 0.5
9.2 ± 1.3
0.011 ± 0.004
0.24 ± 0.01
0.7 ± 0.02
Kawempe division
Nabukalu
37 ± 1.9
4.1 ± 0.4
0.012
8.3 ± 0.5
13.5 ± 1.0
0.007 ± 0.006
0.33 ± 0.01
0.3 ± 0.02
Abdu
61 ± 2.3
6.5 ± 0.6
0.167
17.2 ± 1.0
21.4 ± 2.1
0.007 ± 0.005
1.14 ± 0.02
0.4 ± 0.01
SP4306K
40 ± 3.0
4.4 ± 0.8
0.001
15.1 ± 1.3
17.1 ± 1.2
0.007 ± 0.007
0.84 ± 0.02
0.3 ± 0.02
Kikoni
20 ± 2.9
3.1 ± 0.7
0.001
4.9 ± 0.6
11.1 ± 0.6
0.006 ± 0.001
0.62 ± 0.03
0.2 ± 0.01
Rubaga division
SP1414R
31 ± 2.5
4.1 ± 0.2
0.001
6.5 ± 0.5
12.0 ± 1.3
0.008 ± 0.002
0.24 ± 0.02
0.2 ± 0.01
Sentamu
27 ± 2.6
3.8 ± 0.1
0.001
7.9 ± 0.6
13.0 ± 1.1
0.007 ± 0.001
0.24 ± 0.01
0.2 ± 0.01
Kunnya
23 ± 2.2
1.9 ± 0.1
0.107
8.6 ± 0.3
8.3 ± 0.4
0.006 ± 0.002
0.28 ± 0.04
0.4 ± 0.02
SP1212R
22 ± 1.7
3.7 ± 0.2
0.001
8.3 ± 0.5
11.0 ± 0.5
0.005 ± 0.002
0.14 ± 0.02
0.1 ± 0.03
Kibumbiro
23 ± 1.8
2.7 ± 0.3
0.299
5.7 ± 0.4
11.2 ± 0.3
0.006 ± 0.001
0.78 ± 0.02
0.7 ± 0.02
Kabaale
19 ± 1.3
3.2 ± 0.4
0.169
7.6 ± 0.2
14.3 ± 0.3
0.007 ± 0.003
0.09 ± 0.01
0.5 ± 0.03
Nababirye
8.0 ± 0.2
2.4 ± 0.2
0.002
4.2 ± 0.1
7.1 ± 0.1
0.010 ± 0.002
0.02 ± 0.01
1.9 ± 0.05
SP1010R
35 ± 1.9
4.2 ± 0.3
0.002
9.7 ± 0.4
12.7 ± 0.4
0.005 ± 0.001
0.53 ± 0.02
0.2 ± 0.03
Makindye division
Nsambya
45.8 ± 2.3
4.4 ± 0.2
0.002
11.1 ± 0.6
14.7 ± 0.3
0.005 ± 0.003
0.58 ± 0.01
0.2 ± 0.02
Kapeke
66.4 ± 3.3
4.9 ± 0.1
0.015
12.2 ± 0.2
17.2 ± 0.2
0.005 ± 0.002
1.20 ± 0.02
0.2 ± 0.05
Yusuf
23.2 ± 1.1
2.8 ± 0.1
0.001
7.4 ± 0.5
11.7 ± 0.1
0.005 ± 0.001
0.09 ± 0.01
0.4 ± 0.06
Kasanvu
21.0 ± 1.3
4.0 ± 0.2
0.001
5.2 ± 0.1
18.7 ± 0.3
0.005 ± 0.002
0.02 ± 0.00
0.2 ± 0.02
Central division
Nabagereka
43.7 ± 2.3
5.3 ± 0.2
0.150
15.1 ± 0.4
23.5 ± 0.1
0.006 ± 0.002
0.74 ± 0.01
0.5 ± 0.02
Barracks
25.1 ± 1.2
4.6 ± 0.3
0.001
5.9 ± 0.1
20.2 ± 0.1
0.006 ± 0.001
0.04 ± 0.00
0.2 ± 0.01
SP5003C
37.5 ± 2.4
5.1 ± 0.1
0.101
14.9 ± 0.3
17.3 ± 0.2
0.007 ± 0.001
0.27 ± 0.01
0.4 ± 0.03Table 3
A summary of the percentage of selected protected springs in Kampala city with levels of major elements in water above and below the WHO guideline values and the Ugandan standards.
Element
Na
Mg
Al
K
Ca
Cr
Mn
Fe
Springs above Ugandan guidelines
0
0
20
—
0
4
66.7
58.3
Springs below Ugandan guidelines
100
100
80
—
100
96
33.3
41.7
Springs above WHO guidelines
0
0
8
33.3
0
4
29
58.3
Springs below WHO guidelines
100
100
92
67.7
100
96
71
41.7The protected springs with the elevated Cr levels are located in Nakawa division, and their contamination may be attributed to the existence of paint manufacturing industries in the spring catchment zone. However, 8% of the samples had high levels of Al (0.299–0.360 mg/l) exceeding the 0.2 mg/l level. The contamination of the environment with aluminium may be due to anthropogenic activities besides wear and tear of motor parts since the contaminated sampling points were located in a built environment with paved roads but near a car parking lot. On the contrary, the soils in Kampala were reported to be acidic by Moulodi and Thorsell [20], whereas under acidic conditions, the natural sources of metals may contribute to high levels of aluminium since it is mobilised and solubilized from bedrock and soil into soil water at pH < 5.5. The springs that had levels of K above the guideline value, 10 mg/l, were 33% and had values between 15 and 17 mg/l, whereas 29% had Mn levels above the 0.4 mg/l mark with values ranging between 0.58 and 1.20 mg/l. The BGS [8] report indicates that high concentrations of manganese are a common problem in Ugandan groundwater. The high iron and manganese occurrences have been attributed to the shallow clayey regolith that restrict aeration of underlying aquifers leading to anaerobic conditions to which the high iron and manganese are related [8]. These results for iron and manganese concur with other studies in Uganda by GIBB [31] where iron levels were reported as 0.3–4.9 mg/l; moreover, Taylor and Howard [32] reported iron concentrations up to 45 mg/l and the Mn levels up to 2 mg/l. The water samples that had Ca levels below the required levels for drinking water (20 mg/l) were 95.5%, and with the low pH, it may be a health risk. According to the Ugandan standards, the levels of contamination of the groundwater samples were 20% for Al, 4.2% for Cr, 66.7% for Mn, and 58.3% for Fe, whereas the other major elements were within the Ugandan urban drinking water standards.Tables4 and 5 show levels of trace elements in protected springs and percentage springs with levels above and below the guideline values, respectively. For the case of Ugandan standards, all the elements were below the guidelines, whereas for the WHO guideline values, 8.3% of the protected springs had barium levels above the guideline value, and all the other elements were below the guideline values.Table 4
Levels of trace elements (µg/L) in water from selected protected springs in Kampala city in comparison to WHO guideline values [30, 33, 34].
B
Sb
Ni
Cu
Zn
Cd
Ba
Pb
WHO guidelines
2400
20
70
2000
3000
3
700
10
Ugandan standards
—
—
—
1000
5000
10
1000
50
Canadian guidelines
5000
6
—
1000
5000
5
1000
10
Sample site
Nakawa division
Nabuze
2.0 ± 0.1
1.44 ± 0.03
9.8 ± 0.3
1.4 ± 0.1
9.4 ± 0.5
0.05 ± 0.002
150 ± 5.5
0.54 ± 0.01
Katarina
2.3 ± 0.4
0.45 ± 0.01
6.8 ± 0.4
3.2 ± 0.2
16.9 ± 0.8
0.04 ± 0.001
146 ± 4.3
0.94 ± 0.02
Buwooya
2.1 ± 0.9
0.38 ± 0.01
3.9 ± 0.6
1.3 ± 0.1
16.0 ± 0.4
0.23 ± 0.011
73 ± 3.4
4.09 ± 0.09
Bukoto 1
2.1 ± 0.5
0.42 ± 0.02
3.2 ± 0.2
0.8 ± 0.2
13.6 ± 0.1
0.04 ± 0.001
140 ± 5.6
0.70 ± 0.01
Bukoto 2
2.5 ± 0.1
0.39 ± 0.02
5.4 ± 0.3
1.8 ± 0.3
26.4 ± 0.4
0.05 ± 0.002
234 ± 7.7
1.91 ± 0.02
Kawempe division
Nabukalu
2.4 ± 0.1
0.40 ± 0.01
7.4 ± 0.1
1.6 ± 0.2
20.9 ± 0.4
0.07 ± 0.01
332 ± 4.5
0.87 ± 0.03
Abdu
2.7 ± 0.2
0.55 ± 0.02
12 ± 0.1
2.0 ± 0.1
22.9 ± 0.6
0.11 ± 0.02
821 ± 8.3
1.55 ± 0.02
SP4306K
2.7 ± 0.2
10.98 ± 0.02
8.6 ± 0.1
2.0 ± 0.2
14.7 ± 0.1
0.06 ± 0.01
422 ± 7.2
1.35 ± 0.01
Kikoni
3.2 ± 0.3
0.21 ± 0.01
3.8 ± 0.3
0.5 ± 0.1
6.9 ± 0.2
0.05 ± 0.01
180 ± 6.3
0.04 ± 0.01
Rubaga division
SP1414R
2.0 ± 0.4
9.19 ± 0.01
9.1 ± 0.2
1.7 ± 0.5
17.1 ± 0.7
0.05 ± 0.01
397 ± 5.1
0.76 ± 0.01
Sentamu
1.7 ± 0.5
0.41 ± 0.02
7.4 ± 0.1
0.6 ± 0.3
9.3 ± 0.0
0.05 ± 0.01
303 ± 7.7
0.22 ± 0.03
Kunnya
2.4 ± 0.1
0.90 ± 0.01
6.1 ± 0.7
1.8 ± 0.4
24.5 ± 0.7
0.07 ± 0.02
249 ± 6.5
1.71 ± 0.02
SP1212R
1.7 ± 0.0
0.86 ± 0.02
8.5 ± 0.4
0.7 ± 0.3
9.8 ± 0.0
0.06 ± 0.02
246 ± 8.0
0.23 ± 0.01
Kibumbiro
3.9 ± 0.1
1.34 ± 0.04
15.3 ± 0.0
3.7 ± 0.5
48.0 ± 0.5
0.16 ± 0.03
454 ± 7.9
5.06 ± 0.05
Kabaale
5.1 ± 0.5
0.90 ± 0.03
4.9 ± 0.1
1.7 ± 0.8
16.5 ± 0.6
0.10 ± 0.02
286 ± 8.3
2.11 ± 002
Nababirye
1.9 ± 0.6
1.80 ± 0.00
4.9 ± 0.2
5.5 ± 0.8
7.7 ± 0.8
0.02 ± 0.01
108 ± 3.1
0.43 ± 0.03
SP1010R
2.2 ± 0.5
0.22 ± 0.01
8.1 ± 0.2
0.7 ± 0.7
12.1 ± 0.1
0.07 ± 0.02
442 ± 5.8
0.34 ± 0.01
Makindye division
Nsambya
2.5 ± 0.2
1.75 ± 0.02
15.2 ± 0.4
1.4 ± 0.6
11.7 ± 0.6
0.06 ± 0.01
506 ± 6.3
0.72 ± 0.02
Kapeke
2.8 ± 0.7
4.15 ± 0.03
25.5 ± 0.8
3.4 ± 0.8
38.0 ± 0.4
0.14 ± 0.02
1132 ± 8.9
1.81 ± 0.04
Yusuf
2.6 ± 0.1
0.64 ± 0.01
2.1 ± 0.1
0.9 ± 0.5
11.5 ± 0.3
0.04 ± 0.01
118 ± 5.3
0.78 ± 0.05
Kasanvu
7.2 ± 0.8
0.44 ± 0.01
3.5 ± 0.0
0.9 ± 0.2
4.1 ± 0.2
0.02 ± 0.00
117 ± 6.9
0.12 ± 0.04
Central division
Nabagereka
3.5 ± 0.2
0.38 ± 0.02
8.94 ± 0.4
1.5 ± 0.9
15.9 ± 1.3
0.08 ± 0.01
508 ± 9.0
1.72 ± 0.02
Barracks
3.0 ± 0.8
5.74 ± 0.08
8.22 ± 0.3
1.1 ± 0.8
7.6 ± 0.7
0.05 ± 0.01
213 ± 5.1
0.51 ± 0.01
SP5003C
2.3 ± 0.2
0.52 ± 0.05
4.52 ± 0.1
1.4 ± 0.4
25.1 ± 1.5
0.19 ± 0.02
424 ± 6.4
2.82 ± 0.01Table 5
A summary of the percentage of selected protected springs in Kampala city with levels of trace elements in water above and below the WHO guidelines, Canadian guidelines, and Ugandan standards.
Element
B
Sb
Ni
Cu
Zn
Cd
Ba
Pb
Springs above Ugandan guidelines
—
—
—
0
0
0
0
0
Springs below Ugandan guidelines
—
—
—
100
100
100
100
100
Springs above WHO guidelines
0
0
0
0
0
0
8.3
0
Springs below WHO guidelines
100
100
100
100
100
100
91.7
100
Springs above Canadian guidelines
0
8.3
—
0
0
0
0
0
Springs below Canadian guidelines
100
91.7
—
100
100
100
100
100For Canadian guideline values, 8.3% of the springs had antimony levels above the guideline value. The contaminated protected springs were located on the peripheral of a busy urban market, car washing bay, and motorcycle service workshop which were suspected to be the sources of contamination.The protected springs that had elevated levels of trace elements were characterised by nearness to motorways and residential areas where wearing of car parts, surface runoff, and domestic wastewater are assumed to impact the metal levels. The mobility of trace metals increases under acidic conditions with high dissolved organic matter content, but contamination of the acidic shallow groundwater was not alarming due to low dissolved organic matter content. The sampled shallow groundwater from Kampala had elevated levels of trace metals and was not contaminated; nevertheless, groundwater quality monitoring will ensure adherence to the WHO guidelines to inhibit water contamination and imminent trace metal poisoning.Tables6 and 7 show the other parameters of water that were studied. The temperature of the water varied but was within the guideline value 25°C; moreover, the pH values were all below the guideline values range of 6.5–8.5. The shallow groundwater is therefore generally acidic with pH < 7.0, whereas acidic water increases the weathering of rocks and release of metals from soil surfaces into soil water.Table 6
Mean values of other parameters of shallow groundwater and associated surface runoff from periurban Kampala compared to Guidelines for Canadian Drinking Water Quality and Ugandan Standards.
Spring name
Analysis of spring water
Surface runoff analysis
T (°C)
pH
DOC (mg/L)
EC (µS/cm)
NO3− (mg/L)
Cl− (mg/L)
F− (mg/L)
EC (µS/cm)
Cd2+ (µg/L)
Pb2+ (µg/L)
Canadian guidelines
—
6.5–8.5
—
—
45
—
0.5
—
5
10
Ugandan standards
—
6.0–8.5
—
1000
10
250
1.0
1000
10
50
Nakawa division
Nabuze
25.0
5.46
1.0
665
34.1
11.9
0.1
750
1.18
178
Katarina
24.0
5.36
1.0
372
19.9
6.9
0.1
450
1.30
81
Buwooya
25.0
5.45
1.0
211
10.4
3.8
0.2
350
2.62
560
Bukoto 1
26.0
5.07
1.0
226
27.0
13.3
0.3
300
2.52
915
Bukoto 2
25.0
4.80
2.0
470
64.3
24.2
0.2
520
3.10
905
Kiddumu
25.0
5.72
1.0
862
44.8
16.8
0.1
1208
0.32
108
Kawempe division
Nabukalu
25.0
4.93
2.0
873
78.7
30.3
0.1
980
2.39
129
Abdu
26.0
4.74
1.0
2650
78.5
46.5
0.1
3050
2.64
1294
SP4306K
25.0
4.98
1.0
786
38.6
16.6
0.1
824
1.35
95.8
Kikoni
26.0
5.35
1.0
497
42.5
18.2
0.1
532
8.00
519
Bukuku
26.0
5.86
2.0
643
65.4
31.2
0.1
835
1.19
92.1
Rubaga division
SP1414R
26.0
4.93
1.0
774
63.6
27.0
0.1
812
1.82
121
Sentamu
25.0
4.98
1.0
722
74.6
32.3
0.1
820
0.42
69
Kunnya
25.0
5.30
1.0
574
107.3
41.7
0.1
642
0.31
11
SP1212R
25.0
5.03
1.0
631
1.0
10.2
1.0
722
0.13
28
Kibumbiro
24.0
5.14
2.0
586
68.4
40.1
0.1
650
0.96
185
Kabaale
25.0
5.32
1.0
607
70.2
28.4
0.2
600
0.90
45
Nababirye
25.0
5.68
1.0
272
42.5
18.3
0.1
472
0.35
31
Nsereko
26.0
4.89
1.0
786
24.7
8.8
0.1
786
24.7
8.8
Lugala
25.0
5.18
1.0
272
57.9
21.6
0.1
1090
0.30
30.8
SP1010R
25.0
5.18
1.0
916
64.5
28.4
0.1
1200
0.03
78
Makindye division
Nsambya
25.0
5.37
1.0
1098
101.2
42.1
0.2
1250
0.68
140
Kapeke
25.0
5.18
1.0
1472
102.5
64.4
0.2
1670
0.29
106
Yusuf
25.0
5.45
1.0
648
101.4
42.7
0.2
1210
0.43
215
Kasanvu
25.0
5.68
1.0
764
38.7
11.8
0.5
825
0.18
36
Kibuuka
25.0
5.89
1.0
873
45.6
18.6
0.2
972
1.20
201.4
Kisugu
25.0
5.68
1.0
764
125.3
58.5
0.2
1250
0.68
140.0
SP7009M
26.0
5.24
2.0
607
45.6
18.6
0.2
648
0.82
141.0
Central division
Nabagereka
25.0
5.54
2.0
1208
58.3
35.6
0.3
779
0.03
34
Barracks
25.0
5.36
1.0
779
74.7
23.2
0.1
864
0.22
121
SP5003C
24.0
5.55
2.0
1051
53.7
35.5
0.3
1251
0.29
57
Kisekka
26.0
4.97
2.0
772
5.1
49.6
5.0
820
18.3
15.4
Kinyoro
24.0
5.20
1.0
421
18.0
5.9
0.1
774
1.05
294.9
Bativa
26.0
4.95
1.0
832
38.8
14.8
0.1
870
0.68
55.7
SP5508C
25.0
5.24
1.0
680
44.4
29.4
0.2
680
44.4
29.4
SP5303C
26.0
5.25
2.0
648
53.7
36.5
0.3
648
53.7
36.5
SP4902C
26.0
4.92
1.0
786
60.5
23.2
0.1
1670
0.29
105.8Table 7
A summary of the percentage of samples of shallow groundwater and associated surface runoff from periurban Kampala above and below the Guidelines for Canadian Drinking Water Quality and Ugandan Standards.
Sample site
Protected spring water
Surface runoff
Parameter
EC
NO3−
Cl−
EC
Cd2+
Pb2+
Springs above Ugandan guidelines
13.5
94.6
—
21.6
2.7
81.1
Springs below Ugandan guidelines
86.5
5.4
—
78.4
97.3
18.9
Springs above Canadian guidelines
—
73
0
—
5.4
97.3
Springs below Canadian guidelines
—
27
100
—
94.6
2.7Acidic water is aggressive to surfaces and has a high capacity to corrode ferrous materials which explain why surface water in the catchment areas exhibits a flimsy rusty layer. On the contrary, Olade [14] stated that groundwater tapped from weathered regolith is acidic which may promote oxidation and corrosion of steel casings and screens. The DOC levels were all below the contamination level (2.0 mg/l). Mobility of trace metals is known to be dependent on the dissolved organic matter content and pH although redistribution of trace metals in groundwater may be affected by other factors such as redox conditions.The electrical conductivity (EC) values were high and exceeded the guideline value of 1000µS/cm in almost 13.5% of the shallow groundwater case studies and 21.6% of the surface runoff samples studied which indicated that inorganic species occurred mainly in the ionic form especially in the high population density periurban areas where those particular protected springs were located. Only 5.4% of the sampled spring water had nitrate levels below the Ugandan standard of 10 mg/l, and the rest was highly polluted with 11–125 mg/l which implied that there was enrichment of the shallow groundwater with nutrients from urbanisation and industrialisation activities. Of the sampled shallow groundwater, 52.8% had nitrate levels above the drinking water guideline value of 50 mg/l and 21.6% of them had elevated levels. The Canadian guideline value of 45 mg/l was exceeded by 73% of all sampled springs. These results were in agreement with studies by Taylor and Howard [32], where nitrate levels of 26 mg/l were reported in groundwater, and in another study by Kulabako et al. [35], the mean nitrate values reported in shallow groundwater were 67 mg/l. These high nitrate levels are indicative of nutrient loading of the shallow aquifers which could be attributed to anthropogenic sources such as onsite sanitation, domestic sewage disposal habits, waste dumpsites, and others in the spring catchment areas. All the chloride levels in the spring water samples were below the guideline values although they were elevated and indicated increasing salinity probably due to weathering since the groundwater is acidic; however, these results were similar to the high salinity reported by Kulabako et al. [35] which was 59 mg/l, whereas Moulodi and Thorsell [20] reported 4.6–54.6 mg/l of chloride levels in shallow groundwater. One of the most serious inorganic contaminants reported was fluoride with concentrations above the guideline value, 1.5 mg/l for samples of groundwater in interaction with crater lakes in Uganda [8, 36], although the fluoride levels in shallow groundwater in Kampala were lower than the guideline values, which indicated a difference in sources of fluorine which are of geochemical origin. All the surface runoff associated with the protected springs had high electrical conductivity with 21.6% of them above the guideline value and 27% with elevated levels but below the guideline value of 1000 µS/cm. Weathering, wearing, and corrosion of metals dissolve metals in the wash down and increase the electrical conductivity of surface runoff. About 2.7% of the surface runoff samples were above the Ugandan guideline value of 10 µg/l for cadmium, while 5.4% of the samples were above the Canadian guideline value of 5 µg/l. All fluoride levels were below the Ugandan guideline values and Canadian standards. When the levels of metals in surface runoff were compared to the effluent discharge standards [37], 81.1% of them were above the guideline value of 50 µg/l for lead. As per the Canadian standards [38], 97.3% of the samples had lead levels above the guideline value of 10 µg/l. The suspected source of lead contamination is mainly anthropogenic activities since there are a lot of scrap yards, motor service centres, and metal workshops in addition to wearing of parts of vehicles that may contribute to the elevated levels. Otherwise continued discharge of untreated surface runoff, wastewater, and leachate will negatively impact the shallow groundwater when the soil water is laden during the rainy season; the surface water interacts with the groundwater in shallow aquifers without reacting with the soil chemicals and thence groundwater contamination.Table8 shows the levels of major elements and other parameters in surface water, wastewater, and landfill leachate from selected sources in the Lake Victoria basin. Table 9 shows a summary of the levels above and below the guideline values, respectively. The pH for all the sampled sources was within the limits of the WHO guideline values (6.5–8.5). The electrical conductivity values for 53.3% of the surface water, surface runoff, and landfill leachate samples were higher than the guideline value of 1000 µS/cm, whereas samples from the hot springs and municipal landfills leachate were 3–6 times higher than the WHO guideline value. These values could be due to mobilisation of conducting ions during the decay processes of landfills and thermal mobilisation of ions as hot water rises up through mineralised soils in hot springs; moreover, the salt lake has a rich matrix of conducting ions. The mine tailings from an old copper mine had higher EC values that were attributed to copper contamination of water. The temperatures of surface water sources were within the guideline values. The exceedance above the WHO guideline values for major elements in surface water was 33.3% for sodium, 13.3% for magnesium, 33.3% for aluminium, 53.3% for potassium, 80% for manganese, and 93.3% for iron. For Ugandan standards, the samples exceeding the guideline values were 6.7% for magnesium, 13.3% for calcium, 13.3% for manganese, and 6.7% for iron. Therefore, the surface water from different sources is contaminated with major elements. The levels of metals in the surface water samples were higher than those in a study by Walakira and Okot-Okumu [39] which were reported as 17–39 mg/l for calcium, 0.6–53 mg/l for sodium, 0.05–0.26 mg/l for lead, 0.02–0.56 mg/l for copper, and below the detection level for cadmium. The main source of these elements could be weathering of mineralised soils and rocks as well as mobilisation during sorption-desorption processes for trace elements onto organic matter and soil particles.Table 8
Mean levels of major elements (mg/L) and other parameters of surface water from selected streams and waterways in Lake Victoria basin, Uganda, compared to the WHO guidelines and Ugandan standards (maximum concentrations).
Sampling site
WHO water guidelines
pH
EC (µS/cm)
T (C°)
Na
Mg
Al
K
Ca
Mn
Fe
6.5–8.5
1000
25
200
50
0.1
10
200
0.1
0.3
Ugandan standards
6.0–8.0
1000
23–25
—
100
0.5
—
100
1.0
10
Lubigi Channel
7.49
1530
29
51.5
5.1
0.066
25.03
26.3
0.80
2.61
Mulago Channel
7.02
1420
25
50.7
4.6
0.062
22.60
25.5
0.83
2.63
Nakivubo Channel
7.20
1723
28
56.4
5.4
0.154
28.62
24.3
0.53
2.84
Lugogo stream
7.16
930
26
31.8
5.7
0.001
17.32
26.3
0.83
3.49
Bugoloobi stream
7.09
700
25
19.9
5.1
0.002
6.28
18.0
0.13
0.33
Kiteezi Landfill
8.44
5100
30
5245
82.8
0.140
0.03
26.2
0.29
5.35
Lugazi Steel Mills
7.68
133
25
40.7
4.6
0.739
27.06
27.5
0.62
14.98
Jinja Landfill
7.89
3120
27
400
184.8
0.002
0.07
135.4
2.87
6.49
Jinja Steel Mills
7.46
1772
27
36.1
22.5
0.001
4.66
62.6
0.68
1.14
Jinja Walukuba
7.90
300
26
11.9
1.7
0.001
3.49
5.8
0.01
0.20
River Mpanga
6.80
768
25
27.8
15.2
0.001
6.84
82.7
1.57
1.27
Kibenge Hot Springs
7.60
924
46
600.2
4.4
0.040
19.99
199
0.03
0.97
River Nyamwamba
7.03
127
22
6.4
3.8
0.002
3.62
10.0
0.13
1.21
Kilembe Mines
7.45
1569
26
509.8
25.1
0.924
518.10
78.6
0.45
0.93
Kitagata Hot Springs
7.80
1182
59
205.6
0.2
0.001
10.50
30.5
0.02
0.33Table 9
A summary of the percentage of samples of surface water from selected streams and waterways in Lake Victoria basin, Uganda, with mean levels of major elements and other parameters of surface water from selected streams and waterways in Lake Victoria basin, Uganda, above and below the WHO guidelines and Ugandan standards.
Element
EC
Na
Mg
Al
K
Ca
Mn
Fe
Springs above Ugandan guidelines
53.5
—
6.7
26.7
—
13.3
13.3
6.7
Springs below Ugandan guidelines
46.7
—
93.3
73.3
—
86.7
86.7
93.3
Springs above WHO guidelines
53.5
33.3
13.3
33.3
53.5
0
80
93.3
Springs below WHO guidelines
46.7
66.7
86.7
66.7
46.7
100
20
6.7Figures4 and 5 give a synopsis of the levels of cadmium and lead in the shallow groundwater in comparison to the levels in surface runoff associated with the protected spring catchment areas.Figure 4
Outline of Cd(II) levels in the shallow groundwater and associated surface runoff from Kampala city (where the red line indicates the guideline value for levels of cadmium in surface water).
(a)
(b)
(c)
(d)Figure 5
Outline of Pb(II) levels in the shallow groundwater and associated surface runoff from Kampala city (where the red bars indicate that the levels of lead in surface runoff were all the above guideline value).
(a)
(b)
(c)
(d)The levels of Cd2+ ions in shallow groundwater samples were below allowable limits for groundwater, whereas the Cd2+ ions levels in surface runoff were 12% elevated and 12% above the limit of 3 µg/L. For Pb2+ ions in shallow groundwater, 24% of the levels were elevated, whereas 100% of the levels of Pb2+ ions in surface runoff were by 3–130 times higher than the allowable limit of 10 µg/L. The results in this study were higher than those for Lake Victoria water reported by Tole and Shitsama [40] which were 0.12–0.45 µg/l for Pb and 0.01 µg/l for Cd. Although the vertical mobility of the trace metals is controlled by the soil pH and organic matter content, the flood zones of the periurban areas where the shallow groundwater samples were picked tend to have mixing of surface water and shallow groundwater during the rainy seasons which may cause detrimental effects to the water quality of the shallow aquifers.Tables10 and 11 show the levels of trace elements in the surface water from various sample sites and the percentage of those samples above the guideline values, respectively. The trace elements levels exceeding the WHO guideline values in surface water were 33.3% for nickel, 25% for antimony, 31% for nickel, 6% for copper, 13% for zinc, 25% for arsenic, 6.7% for selenium, 13.4% for barium, and 40% for lead, whereas those exceeding the Ugandan guideline values were only 6.7% for copper although Taylor and Howard [32] reported minor exceedance above the WHO guideline values for barium, nickel, lead, uranium, and cadmium in their study of groundwater in Uganda. The urban streams and landfill leachate have elevated levels of trace metals: boron, antimony, arsenic, nickel, selenium, barium, and lead. The mine tailings are contaminated with copper and nickel. However, the pollution trends depict anthropogenic contamination although natural mobilisation of metal ions from the parent rock is possible. Nickel contamination results from the usage of electric cells and industrial wastewater, whereas copper was high in the copper mine tailings. Arsenic levels were evidently high in landfill leachates and Lubigi Channel which implied that anthropogenic pollution of the environment occurred since the levels in the shallow groundwater were all below the WHO guideline values.Table 10
Trace metal elements (µg/L) in surface water from selected streams and waterways in Lake Victoria basin, Uganda, compared with WHO guidelines [30] and Ugandan standards [28, 37].
Sampling site
WHO water guidelines
B
Ni
Cu
Zn
As
Se
Cd
Ba
Pb
2400
70
2000
4000
10
40
3
700
10
Ugandan standards
5000
1000
1000
5000
200
1000
100
10000
100
Lubigi stream
485
178.9
133.2
584.7
25.15
27.71
1.110
6227
97.7
Mulago stream
14
5.8
4.9
25.9
0.70
0.88
0.047
215.1
2.9
Nakivubo stream
32
10.9
10.9
66.2
1.0
1.19
0.255
181.9
10.9
Lugogo stream
18
6.9
3.3
15.7
0.88
1.02
0.024
218.7
0.9
Bugoloobi stream
199
126.8
38.4
506.8
6.11
16.46
2.307
2723.7
27.4
Kiteezi Landfill leachate
1338
271.2
119.6
248.3
23.32
71.37
1.143
214.5
99.3
Lugazi Steel Mills effluent
126
19.6
16.4
210.3
2.08
0.69
0.193
73.3
29.0
Jinja Landfill leachate
953
104.7
74.1
241.1
11.98
25.62
0.436
186.3
29.7
Jinja Steel Mills effluent
29
6.2
1.0
4.9
0.46
2.55
0.030
104.8
0.3
Jinja Walukuba effluent
10
0.9
0.5
6.1
0.21
0.21
0.004
30.2
1.0
River Mpanga
11
5.5
1.8
15.2
0.38
0.47
0.477
341.7
5.1
Kibenge Hot Springs
296
9.1
7.6
12.8
2.96
23.18
0.136
25.8
2.0
River Nyamwamba
7.5
18.0
172.7
24.2
0.27
0.29
0.188
28.6
2.3
Kilembe Mines effluent
6.8
90.0
1604
53.4
2.03
0.60
0.445
31.0
2.6
Kitagata Hot Springs
375
2.4
3.6
21.5
0.82
2.60
0.471
36.8
4.9Table 11
A summary of the percentage of samples of surface water from selected streams and waterways in Lake Victoria basin, Uganda, with mean levels of trace elements above and below the WHO guidelines and Ugandan standards.
Element
B
Ni
Cu
Zn
As
Cd
Ba
Pb
Springs above Ugandan guidelines
0
0
6.7
0
0
0
0
0
Springs below Ugandan guidelines
100
100
93.3
100
100
100
100
100
Springs above WHO guidelines
0
33.3
0
0
0
0
13.4
40
Springs below WHO guidelines
100
66.7
100
100
100
100
86.6
60Table12 shows results of metal speciation studies for selected streams, waterways, and landfill leachates done by modelling the levels of elements using Visual MINTEQ. The results indicated that, in the landfill leachates, 74% of the metal ions are bound to dissolved organic matter (DOM) except for aluminium; 70% exists as inorganic aluminium, whereas most metal contaminants show toxic effects in their inorganic forms. The dominant ionic species in the landfill leachate are fulvic acid bound metals and metal hydroxides for nickel, copper, zinc, cadmium, lead, and iron, whereas manganese is a free ion and aluminium is in form of aluminium tetrahydroxyl radical. For the urban streams, 25% of the metal ions are bound to dissolved organic matter, 38% metal species are free metal ions, and 19% are in form of inorganic species.Table 12
Percentage composition of metal ions in aqueous media as determined by speciation studies of selected surface water samples from streams in Lake Victoria basin, Uganda.
Sampling site
Ni2+
Cu2+
Zn2+
Cd2+
Pb2+
Al3+
Mn2+
Fe3+
Jinja Landfill leachate
Bound to DOM
92.5
100
96.3
87.7
99.9
46.9
24.5
100
Free ion
7.0
—
2.9
5.2
—
—
65.5
—
Inorganic
0.5
—
0.8
7.1
0.01
54.1
10.0
—
Dominant ion
FANi+
FA2CuOH
FA2Zn
FA2Cd
FA2Pb
Al(OH)4−
Mn2+
FA2FeOH
Kiteezi Landfill leachate
Bound to DOM
96.5
100
99.4
97.5
100
13.5
37.1
100
Free ion
3.4
—
0.4
0.9
—
—
61.9
—
Inorganic
0.1
—
0.2
1.8
—
86.5
1.0
—
Dominant ion
FANi+
FA2CuOH
FA2Zn
FA2Cd
FA2Pb
Al(OH)4−
Mn2+
FA2FeOH
Lubigi Channel
Bound to DOM
58.5
98.3
35.1
31.8
97.7
4.7
8.2
97.5
Free ion
40.0
0.7
59.8
58.4
1.6
—
86.3
—
Inorganic
1.5
1.0
6.1
10.8
1.3
95.3
5.5
2.4
Dominant ion
Ni2+
FA2Cu
Zn2+
Cd2+
FA2Pb
Al(OH)4−
Mn2+
FA2FeOH
Nakivubo Channel
Bound to DOM
9.2
47.1
3.2
2.8
42.6
0.5
0.9
45.7
Free ion
86.9
27.6
87.9
76.6
38.7
—
90.3
—
Inorganic
3.9
25.3
8.9
20.6
18.7
99.5
8.8
54.3
Dominant ion
Ni2+
FA2Cu
Zn2+
Cd2+
FA2Pb
Al(OH)4−
Mn2+
Fe(OH)3The prominent ionic species in urban streams are manganese, nickel, zinc, and cadmium ions, iron(III) hydroxide, aluminium tetrahydroxyl radical, and fulvic acid bound copper and lead. The speciation of metal ions shows that they will be bound to DOM or fulvic acid; however, if the pH, DOC, and calcium content are lowered, the metal binding to the biotic ligand will increase causing toxicity effects to sensitive water plants and animals.In Figure6, a comparison of the trace metal elements in surface water with the Swedish environmental guidelines for lakes and watercourses is presented, whereas Table 13 showed the criteria used. Figure 7 presents the description of the colour codes used in the criteria. The results showed that Lubigi Channel that traverses the periurban area of Kawempe Division and Bugoloobi Channel, whose catchment areas are in the industrial area of Kampala, has been shown to pose a high risk of negative effects on life support systems even for short-time exposure of exposure to Zn, Cu, Pb, and Cd metals. The leachate from Jinja and Kiteezi municipal landfills pose a high risk of exposure to Zn, Cu, Pb, and Cd metals. The effluent from Lugazi Steel Mills poses high risk of negative effects on life support systems even for short-time exposure to Pb, whereas the water from Kilembe Mine tailings and River Nyamwamba poses a greater risk of exposure to copper. The results from these case studies showed high risk of negative effects on life support systems even for short-time exposure. According to the results of this study, the water samples from Lugogo Channel in Kampala, Walukuba Channel in Jinja, River Mpanga in Kasese, and Kitagata Hot Springs presented metal concentrations in water that were suspected to have no anthropogenic contribution or trace metals contamination and no significant effects to life. Documented toxicity studies in surface water from Lake Victoria basin are scarce although in studies by Ljung [19] the trace metal levels that exceeded the lower limits for acute effects on organisms reported were 55% for cadmium, 5% for nickel, 77% for copper, 100% for zinc, and 33% for lead as compared to 46% for cadmium, 30% for nickel, 76% for copper, 46% for zinc, and 46% for lead for the current study.Figure 6
Comparison of concentrations of selected trace metal elements (µg/L) in surface water from particular water sources in Lake Victoria basin, Uganda, with Swedish environmental guidelines.Table 13
The Swedish Environmental Protection Agency (Naturvårdsverket) criteria.
Metal (µg/l)
Class 1 (very low)
Class 2 (low)
Class 3 (moderate)
Class 4 (high)
Class 5 (very high)
Cd
<0.01
0.01–0.1
0.1–0.3
0.3–1.5
>1.5
Cu
<0.5
0.5–3
3–9
9–45
>45
Ni
<0.7
0.7–15
15–45
45–225
>225
Pb
<0.2
0.2–1
1–3
3–15
>15
Zn
<5
5–20
20–60
60–300
>300Figure 7
Colour codes used for the Swedish Environmental Protection Agency (Naturvårdsverket) criteria.The effects of selected trace metals on life support systems have been done basing on the criteria from the Swedish Environmental Protection Agency [29] and are shown in Figure 6. These results of the comparison and classification of predicted risks were more general for environmental health effects. The description of the criteria used in the classification of risks due to levels of metal ions in the aquatic environment is shown in Table 13. In the selected waterways, streams, and landfill leachate, there were suspected toxicity effects due to lead, copper, and zinc with Bugoloobi and Lubigi waterways being most risky. Due to the colour codes described in Figure 7, the levels of the metals in the aquatic environment that show no effects to moderate effects were accorded colours from yellow to blue. The values in blue such as those for arsenic are suspected to cause environmental disturbance, but values close to guideline values normally show no effects in organisms; moreover, the values in yellow are concentrations to which local sources or long distance atmospheric contributions have contributed although it may represent natural deviations and no significant effects to life.The green coloured values are concentrations in water that have no anthropogenic contribution and are below guideline values. Therefore, continued discharge of untreated contaminated wastewater and landfill leachate will continue to impact on the quality of water in urban streams. The highest risk of exposure is due copper and lead followed by zinc and cadmium, whereas the water that poses the greatest risk of exposure is that from Lubigi Channel, Kiteezi Landfill leachate, Bugoloobi Channel, and Jinja Landfill leachate.Tables14 and 15 present results of modelling values of levels of elements in the surface water using the Bio-met software tool that is applied over a range of different organisms to calculate the 5th percentile of the species sensitivity distribution (SSD).Table 14
Results for risk assessment with respect to zinc and lead for selected surface water samples.
Sample name
Local HC5 (dissolved) (µg/L)
BioF
Bioavailable zinc concentration (µg/L)
RCR
Local HC5 (dissolved) (µg/L)
BioF
Bioavailable lead concentration (µg/L)
RCR
River Mpanga
75.47
0.14
2.05
0.19
65.88
0.02
0.09
0.08
Nakivubo Channel
149.16
0.07
4.76
0.44
75.30
0.02
0.17
0.14
Lubigi Channel
183.54
0.06
34.68
3.18
78.08
0.02
1.50
1.25
Kibenge Hot Springs
105.39
0.10
1.22
0.11
68.61
0.02
0.03
0.03
River Nyamwamba
66.13
0.16
3.82
0.35
65.57
0.02
0.04
0.04
Kitagata Hot Springs
233.22
0.05
0.96
0.09
86.05
0.01
0.07
0.06
Kilembe Mine tailings
84.19
0.13
6.73
0.62
30.24
0.04
0.10
0.09
Mulago Channel
62.55
0.17
4.34
0.40
40.48
0.03
0.09
0.07
Bugoloobi Channel
74.31
0.15
74.19
6.81
66.34
0.02
0.50
0.41
Lugogo Channel
75.77
0.14
2.11
0.19
40.80
0.03
0.03
0.02
Lugazi Channel
150.28
0.07
15.16
1.39
67.58
0.02
0.51
0.43
Jinja Landfill leachate
111.33
0.10
23.50
2.16
77.56
0.02
0.46
0.38
Kiteezi Landfill leachate
623.74
0.02
4.32
0.40
92.51
0.01
1.29
1.07Table 15
Results for risk assessment with respect to copper and nickel for selected surface water samples.
Sample name
Local HC5 (dissolved) (µg/L)
BioF
Bioavailable copper concentration (µg/L)
RCR
Local HC5 (dissolved) (µg/L)
BioF
Bioavailable nickel concentration (µg/L)
RCR
River Mpanga
119.21
0.01
0.02
0.02
53.20
0.08
0.41
0.10
Nakivubo Channel
185.25
0.01
0.06
0.06
59.21
0.07
0.74
0.18
Lubigi Channel
191.68
0.01
0.69
0.69
57.50
0.07
12.45
3.11
Kibenge Hot Springs
227.55
0.00
0.03
0.03
56.31
0.07
0.65
0.16
River Nyamwamba
131.48
0.01
1.32
1.32
42.11
0.09
1.71
0.43
Kitagata Hot Springs
159.16
0.01
0.02
0.02
53.90
0.07
0.18
0.04
Kilembe Mine tailings
54.56
0.02
29.40
29.40
29.95
0.13
12.02
3.00
Mulago Channel
75.42
0.01
0.06
0.06
30.80
0.13
0.75
0.19
Bugoloobi Channel
144.60
0.01
0.27
0.27
43.10
0.09
11.79
2.95
Lugogo Channel
82.05
0.01
0.04
0.04
31.76
0.13
0.87
0.22
Lugazi Channel
117.74
0.01
0.14
0.14
39.35
0.10
1.99
0.50
Jinja Landfill leachate
474.12
0.00
0.16
0.16
151.90
0.03
2.77
0.69
Kiteezi Landfill leachate
173.20
0.01
0.69
0.69
100.41
0.04
10.80
2.70HC5 aims at protecting at least 95% of the species and reflects the bioavailability conditions of a specific site according to the water chemistry. In Tables14 and 15, the local HC5 values were in the ranges of 54.56–474.12 µg/L for Cu2+, 29.95–151.90 µg/L for Ni2+, 62.55–623.74 µg/L for Zn2+, and 30.24–92.51 µg/L for Pb2+ for selected surface water samples. The bioavailable metal concentration is the concentration of a metal that is bioavailable at the site or water body and were in the ranges of 0.02–29.40 µg/L for Cu2+, 0.18–12.45 µg/L for Ni2+, 0.96–74.19 µg/L for Zn2+, and 0.03–1.50 µg/L for Pb2+. The risk characterisation ratio (RCR) values that identified potential environmental risks for the selected surface water samples were 15.4% for Cu2+, 30.8% for Ni2+, 30.8% for Zn2+, and 15.4% for Pb2+. These results require more detailed risk assessments to inform policy on appropriate action.The water source with the highest potential risk was Lubigi Channel. Johnson et al. [41] studied twelve metals in UK surface waters and found that the relative risk to organisms was highest for copper, aluminium, and zinc, whereas in this report, the highest risk of exposure to metals in surface waters was due to zinc and nickel.Tables16 and 17 present results of modelling values of levels of elements in the selected shallow groundwater sources using the Bio-met software tool that is applied over a range of different organisms to calculate the 5th percentile of the species sensitivity distribution (SSD). The local HC5 values in Tables 16 and 17 were in the ranges of 4.15–8.55 µg/L for Cu2+, 8.20–9.67 µg/L for Ni2+, 10.90–14.81 µg/L for Zn2+, and 2.70–5.38 µg/L for Pb2+ for selected shallow groundwater samples. The bioavailable metal concentration values were in the ranges of 0.13–1.13 µg/L for Cu2+, 1.03–12.20 µg/L for Ni2+, 2.94–34.88 µg/L for Zn2+, and 0.10–1.13 µg/L for Pb2+. The risk characterisation ratio (RCR) values that identified potential environmental risks for the selected surface water samples were 4.1% for Cu2+, 45.8% for Ni2+, 62.5% for Zn2+, and 8.3% for Pb2+. These results require more detailed risk assessments to inform policy on appropriate action since the water sources are used for domestic purposes. The shallow groundwater source with the highest potential risk was Kibumbiro in Lubaga Division, whereas those that had RCR values below 1 required no action.Table 16
Results for risk assessment with respect to copper and nickel for selected shallow groundwater samples.
Sample name
Local HC5 (dissolved) (µg/L)
BioF
Bioavailable copper concentration (µg/L)
RCR
Local HC5 (dissolved) (µg/L)
BioF
Bioavailable nickel concentration (µg/L)
RCR
Nabuze
4.95
0.20
0.28
0.28
8.20
0.49
4.78
1.20
Katarina
4.95
0.20
0.64
0.64
8.20
0.49
3.34
0.83
Buwooya
4.95
0.20
0.26
0.26
8.20
0.49
1.93
0.48
Bukoto 1
4.95
0.20
0.17
0.17
8.20
0.49
1.57
0.39
Bukoto 2
7.10
0.14
0.26
0.26
9.67
0.41
2.25
0.56
Nabukalu
7.10
0.14
0.22
0.22
9.67
0.41
3.05
0.76
Abdu
4.15
0.24
0.48
0.48
8.20
0.49
5.91
1.48
SP4306K
4.95
0.20
0.40
0.40
8.20
0.49
4.20
1.05
Kikoni
4.95
0.20
0.09
0.09
8.20
0.49
1.87
0.47
SP1414R
4.95
0.20
0.33
0.33
8.20
0.49
4.45
1.11
Sentamu
4.95
0.20
0.13
0.13
8.20
0.49
3.62
0.90
Kunya
4.95
0.20
0.37
0.37
8.20
0.49
3.01
0.75
SP1212R
4.95
0.20
0.15
0.15
8.20
0.49
4.17
1.04
Kibumbiro
7.10
0.14
0.53
0.53
9.67
0.41
6.33
1.58
Kabaale
4.95
0.20
0.36
0.36
8.20
0.49
2.40
0.60
Nababirye
4.95
0.20
1.13
1.13
8.20
0.49
2.40
0.60
SP1010R
4.95
0.20
0.16
0.16
8.20
0.49
3.96
0.99
Nsambya
4.95
0.20
0.29
0.29
8.20
0.49
7.42
1.85
Kapeke
4.95
0.20
0.70
0.70
8.20
0.49
12.20
3.05
Yusuf
4.95
0.20
0.19
0.19
8.20
0.49
1.03
0.26
Kasanvu
4.95
0.20
0.19
0.19
8.20
0.49
1.71
0.43
Nabagereka
8.55
0.12
0.17
0.17
9.67
0.41
3.70
0.92
Barracks
4.15
0.24
0.26
0.26
8.20
0.49
4.01
1.00
SP5003C
7.10
0.14
0.20
0.20
9.67
0.41
1.87
0.47Table 17
Results for risk assessment with respect to zinc and lead for selected shallow groundwater samples.
Sample name
Local HC5 (dissolved) (µg/L)
BioF
Bioavailable zinc concentration (µg/L)
RCR
Local HC5 (dissolved) (µg/L)
BioF
Bioavailable lead concentration (µg/L)
RCR
Nabuze
11.56
0.94
7.93
0.73
2.70
0.44
0.24
0.20
Katarina
10.90
1.00
15.90
1.46
2.70
0.44
0.42
0.35
Buwooya
10.90
1.00
15.00
1.38
2.70
0.44
1.82
1.51
Bukoto 1
10.90
1.00
12.60
1.16
2.70
0.44
0.31
0.26
Bukoto 2
14.81
0.74
18.70
1.72
5.38
0.22
0.43
0.36
Nabukalu
14.81
0.74
14.65
1.34
5.38
0.22
0.19
0.16
Abdu
11.56
0.94
20.74
1.90
2.70
0.44
0.69
0.57
SP4306K
11.56
0.94
12.91
1.18
2.70
0.44
0.60
0.50
Kikoni
11.56
0.94
5.56
0.51
2.70
0.44
0.02
0.01
SP1414R
11.56
0.94
15.18
1.39
2.70
0.44
0.34
0.28
Sentamu
11.56
0.94
7.82
0.72
2.70
0.44
0.10
0.08
Kunya
10.90
1.00
23.60
2.17
2.70
0.44
0.76
0.63
SP1212R
11.56
0.94
8.29
0.76
2.70
0.44
0.10
0.09
Kibumbiro
14.81
0.74
34.67
3.18
5.38
0.22
1.13
0.94
Kabaale
11.56
0.94
14.70
1.35
2.70
0.44
0.94
0.78
Nababirye
10.90
1.00
6.80
0.62
2.70
0.44
0.19
0.16
SP1010R
11.56
0.94
10.46
0.96
2.70
0.44
0.15
0.13
Nsambya
11.56
0.94
10.18
0.93
2.70
0.44
0.32
0.27
Kapeke
11.56
0.94
34.88
3.20
2.70
0.44
0.80
0.67
Yusuf
11.56
0.94
9.90
0.91
2.70
0.44
0.35
0.29
Kasanvu
11.56
0.94
2.94
0.27
2.70
0.44
0.05
0.04
Nabagereka
19.34
0.56
8.40
0.77
5.38
0.22
0.38
0.32
Barracks
11.56
0.94
6.23
0.57
2.70
0.44
0.23
0.19
SP5003C
14.81
0.74
17.74
1.63
5.38
0.22
0.63
0.52


## 4. Conclusions

The shallow groundwater from protected springs in Kampala city had elevated levels of major and traces metals although some cases were below and others above the WHO guideline values, Ugandan standards, and Canadian standards. The levels of metals in surface water, landfill leachate, and surface runoff showed anthropogenic contamination and revealed increased risks of negative biological effects on organisms as well as the general environmental health. Speciation studies for selected streams, waterways, and landfill leachates using Visual MINTEQ indicated that 74% of the metal ions in the landfill leachates and 25% of the metal ions in urban streams are bound to DOM and were not available as free metal ions. Toxicity studies using the Bio-met software tool showed that selected surface water sources and shallow groundwater sources had potential environmental risks and require further detailed risk assessments to inform policy on appropriate action. However, the current state of the surface water quality indicates that the shallow groundwater in Kampala which is tapped from weathered regolith is acidic and vulnerable to contamination when episodes of acidic rain increase desorption of metal ions from organic matter and soil particles and thence the mobility of trace metals and contamination. The surface water, wastewater, landfill leachates, and surface runoff from several subcatchments of the Lake Victoria catchment zone are contaminated with trace and major elements most likely due to anthropogenic activities and natural mobilisation of metals through weathering of rocks. Otherwise continued discharge of untreated surface runoff, wastewater, and landfill leachate will negatively impact the shallow groundwater when the soil water is laden during the wet seasons, and the surface water interacts with the groundwater in shallow aquifers without reacting with the soil chemicals and thence groundwater contamination. There is need for intervention measures including legislature enforcement, monitoring, and alternative wastewater remediation action to curb water environment contamination.


## 5. Recommendations

To ensure guaranteed groundwater quality, the urban streams need be protected through treating the surface runoff, wastewater, and landfill leachate before discharge. The impending water disaster can be deterred with proactive measures such as building a time series data base on total water quality, regular monitoring of groundwater quality, and enforcing regulation preventive remediation. Further research will aim at modelling prediction of trace metal contaminants’ mobility and distribution in the environment to be able to contaminate the meagre resource and avert environmental trace metal toxicity effects.



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*Source: 6734017-2019-05-23.xml*