Seasonal Hydrological Inputs of Major Ions and Trace Metal Composition in Streams Draining the Mineralized Lom Basin, East Cameroon: Basis for Environmental Studies

  • Mumbfu Ernestine Mimba
  • Takeshi Ohba
  • Salomon César Nguemhe Fils
  • Mengnjo Jude Wirmvem
  • Nozomi Numanami
  • Festus Tongwa Aka
Original Article



The aim of this study is to assess the seasonal variation in major ion distribution patterns and identify the origin and geochemical behavior of some trace metals of streamwaters bathing the mineralized Lom Basin.


Eighty-one water samples were collected during the dry and wet seasons and analyzed for major ions using AAS and 12 trace metals (Fe, Mn, V, Cr, Co, Ni, Cu, Zn, As, Cd, Pb, Hg) by ICP-MS.


All physicochemical parameters besides pH and Cl varied narrowly between both seasons. No seasonal variability was observed for Cl given its conservative nature, while NO3 levels decreased in the wet period due to the dilution effect. Similarly, SO4 2– concentrations were low for both seasons reflecting the dissolution of low sulphide minerals associated with gold deposits. In contrast, the concentration of Ca2+, Mg2+, Na+, K+ and HCO3 slightly increased during the wet season as they are flushed from the soil layers by rain. Water samples had very low concentrations (< 1 µg/l) of V, Cr, Co, Cu, Zn, Cd, Pb and significant concentrations of Fe and Mn.


The seasonal regime of streamwater chemistry is controlled by groundwater supply of major cations and HCO3 from chemical weathering, leaching of ions from surface soil layers during precipitation and dilution of nitrate by surface runoff during the wet season. In this tropical basin, low acidity and trace metal loadings revealed lateritic weathering of sulphides, entrapment of trace metals in Fe and Mn oxides and leaching into deep groundwater. Although the streams have not been impacted, these findings may guide policymakers for water chemistry evaluation in Cameroon.


Seasonal variation Major ions Trace metals Lom Basin Cameroon 

1 Introduction

Hydrogeochemical processes help to unravel changes in surface water quality relating to water–rock interaction or anthropogenic impacts (Singh et al. 2005; Kumar et al. 2006; Franz et al. 2014; Nganje et al. 2015; Kamtchueng et al. 2016). The geochemical properties of surface water also depend on the chemistry of the recharging source as well as the various geochemical processes occurring within the drainage basin. The latter is often responsible for seasonal variations in surface water chemistry (Eneji et al. 2012); hence, the chemistry of streamwater flowing through a basin can evolve through interaction with weathering products and precipitation. In addition, dissolution and ion exchange reactions as well as anthropogenic actions including artisanal mining activities, which have the potential to damage the environment through water pollution, do play an important role in modifying the chemical composition of streamwater along flow paths (Hook 2005; Ako et al. 2014; Agyarko et al. 2014; Kpan et al. 2014; Simbarashe and Reginald 2014; Nganje et al. 2015; Rakotondrabe et al. 2017).

The Lom Basin constitutes part of the Precambrian ore deposits in Cameroon (Milesi et al. 2006). Undoubtedly, water is the principal transport route for dissolved solutes derived from both the chemical weathering of the mineralized basement and small-scale mining activities in the area. Streamwater and boreholes are the major sources of water supply for domestic and mining activities in this basin. Considering the importance of surface water in the area and the associated environmental problems with artisanal mining, Mimba et al. (2017) reported low concentrations of major ions and revealed that mineral weathering, ion exchange and anthropogenic inputs were the key factors influencing water chemistry. However, the seasonal hydrological inputs of these ions can be influenced by the growing population and increased mining activities within the catchment. Thus, seasonal estimation of dissolved ions is necessary to understand the contribution of ions and the long-term effects of changes in land use.

Trace metals are common environmental pollutants in mineralized drainage basins and their concentrations in streams can be of natural or anthropogenic origin. Small-scale mining, as well as the weathering of ore deposits, are well known to release elevated concentrations of trace metals into the soil and water systems (Van Straaten 2000; Nganje et al. 2011; Edet et al. 2014). Moreover, there are growing concerns about the impact of dissolved trace metals on the aquatic ecosystem and human health (Uwah et al. 2013; Dan et al. 2014; Bortey-Sam et al. 2015). No comprehensive survey has been conducted to determine metal levels in streamwater of the study area.

The present study, therefore, assesses the seasonal variation in major ion distribution patterns of streamwater and examines the origin and geochemical behavior of some trace metals in streamwater draining the lower Lom Basin.

1.1 Study Area

The study area is characterised by a mountainous relief that ranges from 600 to 1100 m above sea level. It is covered by shrubs and herbaceous savanna, and has a well-developed dendritic drainage. All examined streams flow within the basin and discharge into the Lom River which flows south–west, and eventually empties into the Atlantic Ocean. The area experiences the humid equatorial climate characterised by alternating dry (December to March, July to August) and wet (April to June, September to November) seasons with relatively high humidity and cloud cover (Braun et al. 1998; Neba 1999). Annual rainfall varies from 1500 to 2000 mm, while the mean temperature is 24.7 °C (Neba 1999). This typical tropical climate enhances prolonged chemical weathering of the parent rocks and the development of thick lateritic overburden.

In a geological context, the Lom Basin is a post-collisional basin dominated by younger volcaniclastic schists, metasedimentary rocks and ubiquitous S-type granitoids which intrude the Pan-African basement (Soba et al. 1991; Toteu et al. 2001, 2006; Ngako et al. 2003). The tectonic evolution of this pull-apart basin and hydrothermal alteration around the plutons account for the widespread sulphide-bearing quartz vein gold deposits (Toteu et al. 2004). Accordingly, alluvial gold is worked from the streams draining this catchment (Omang et al. 2015). Small-scale gold mining constitutes the major industry in the area and dates back to the 1930s (Foumena and Bamenjo 2013). The study area encompasses the Garoua-Boulai and Betare-Oya towns with a total population of about 230,000. Over 80% of the inhabitants are subsistence farmers and depend on surface water and groundwater for domestic purposes.

2 Materials and Methods

2.1 Streamwater Sampling and Field Measurements

Streamwater sampling was carried out during the dry (February to March) and wet (September to October) seasons in 2016, covering the lower Lom Basin (Fig. 1). During these surveys, 81 water samples were collected from lower order streams: 52 samples were collected during base-flow conditions and 29 samples during periods of high flow, for feasibility studies. Field sampling was done in accordance with the FOREGS (Forum of European Geological Surveys) Geochemical field mapping manual (Salminen et al. 1998). A sampling density of 1 sample every 5–10 km was used. The geographical parameters of each sampling site were obtained using a Garmin eTrex GPS. Field measurements were conducted for the physicochemical parameters including pH, electrical conductivity (EC), total dissolved solids (TDS), temperature using the HI 9811–5 Portable pH/EC/TDS/T meter, which was calibrated before and during the campaign. Alkalinity was conducted using a Hach field titration kit within 8 h of sample collection, whereby a volume of 0.16 N H2SO4 was added dropwise to the sample, while continuously stirring with a pH meter to reach the end-point titration (pH 4.5). Water sampling within this tropical basin is discussed in detail elsewhere (Mimba et al. 2017). All samples were collected in previously-washed new 50-ml polyethylene bottles after rinsing severally with the sampled water prior to collection.
Fig. 1

Location map of the Lom Basin indicating points of sample collection

2.2 Major Ions and Trace Element Determination

Laboratory analyses were done at the Laboratory of Geochemistry and Volcanology at Tokai University, Japan. Streamwater samples were analysed for major cations (Ca2+, Mg2+, Na+, K+) by flame atomic absorption spectrometer (AAS) (ContrrAA700) and major anions (F, Cl, NO2 , NO3 , Br, PO4 3–, SO4 2–) using ion chromatography (ICS–900). Laboratory standard solutions of these ions were prepared to calibrate the system. The cation–anion ionic balance error (Appelo and Postma 1996) was used to assess analytical precision. An ionic balance error within ± 5% and an overall precision better than 4% relative standard deviation were considered in further analysis and discussion. Trace element (Fe, Mn, V, Cr, Co, Ni, Cu, Zn, As, Cd, Pb, Hg) concentrations were determined by inductively coupled plasma mass spectrometry (ICP–MS) (ThermoScientific). Certified reference materials JA–3, JB–3, JG–3 (Japan Geological Survey) and blanks were simultaneously analysed to check for analytical precision and accuracy.

3 Results and Discussions

3.1 Seasonal Variation of Major Ions

All analyzed parameters except pH and Cl showed a wide range of values between the sampling periods (Table 1). This seasonal variability suggests that diverse geological and geochemical conditions probably govern the observed drainage signatures (Omang et al. 2014). Concentrations of Cl, which is of anthropogenic origin (Mimba et al. 2017), were invariable throughout the sampling seasons (Table 1) due to its conservative nature and limited potential sources (Grasby et al. 1997; Garizi et al. 2011). Like Cl, Na+ showed only a slight increase during the rainy season. Contrarily, NO3 levels decreased in the wet period owing to dilution by surface runoff during periods of high flow. Sulphate loadings were low for both seasons. Sources of dissolved SO4 2– in surface water include dissolution of SO4 minerals, oxidation of pyrite and organic sulphides in natural soil processes, and sulphur-based fertilisers (Hem 1985; Grasby et al. 1997; Kumar et al. 2006; Nganje et al. 2015). Since agricultural activities are practiced on a fairly small scale in this area, the use of sulphur-based fertilisers is not common. Furthermore, the cluster of points around the near neutral pH field and low SO4 2– content (Fig. 2) is typically associated with low-sulphide gold quartz vein deposits (Ashley 2002). Thus, a plausible origin of dissolved SO4 2– is the dissolution of sulphide minerals, excluding pyrite as a major source. Enhanced dissolution of these minerals and leaching of soils rich in iron oxides (Freyssinet et al. 1989) during the wet season accounts for the seasonal variations (Table 1) observed in the area.
Table 1

Seasonal variation of selected streamwater quality parameters


Dry season

Wet season














EC (µS/cm)







TDS (mg/l)







Na+ (mg/l)







K+ (mg/l)







Ca2+ (mg/l)







Mg2+ (mg/l)







Cl (mg/l)







NO3 (mg/l)







SO4 2− (mg/l)







HCO3 (mg/l)







Na/(Na + Ca)







Fig. 2

Low intensity of acid generation and SO4 2− concentration in the mineralized Lom Basin

Figures 3 and 4 show the evolution of streamwater chemistry in response to seasonal changes. Streamwater draining the Lom catchment remained near neutral (5.5–6.7) all year round although the pH increased by 0.2 units during the wet season (Table 1; Fig. 3a). Despite this uniform hydrogen ion activity, EC and HCO3 were responsive to seasonal changes (Fig. 3b and c). These patterns revealed a shift from dilute (30.61 µS/cm) solution during the dry season to a solution with increased dissolved solids (53.89 µS/cm) during the months of heavy rainfall. An increase in the HCO3 content during high-flow conditions of the wet season was also observed, neutralizing the mild acidity recorded during the dry season. In support of previous report by Mimba et al. (2017), the concentrations of Na+, K+ and Ca2+ slightly increased with increasing flow (Fig. 4a–c), exhibiting a similar seasonal pattern as HCO3 alkalinity (Fig. 4c).
Fig. 3

ac Seasonal trends showing an overall increase in pH, EC and alkalinity during the wet season. Dry and wet seasons correspond to periods of base flow and high flow, respectively. GB Garoua Boulai–Betare-Oya

Fig. 4

Slight increase in Na+, K+ and Ca2+ concentrations in streamwater during the wet season ac; d the mineral weathering indices for both seasons: Low Na/(Na + Ca) ratios indicate mineral weathering, while higher ratios signify other sources. GB, Garoua Boulai–Betare-Oya

It is well known that streamwater cation content usually increases during the dry season. During this period of low stream discharge, high concentrations of major cations derived from silicate weathering are fed into the streams primarily by groundwater. With the advent of the wet period, stream discharge is expected to increase by surface or lateral flows during precipitation and dilute the streams (Meybeck 1987; Drever 1997; Khazheeva et al. 2007; Kelepertzis et al. 2012). Contrarily, a positive correlation was observed between solute concentration and stream discharge similar to observations for streams draining the Amazonian watershed in Brazil (Markewitz et al. 2001). The high levels of HCO3 observed were attributed to the weathering of bedrock and the dissociation of carbonic acid resulting from increased root and microbial respiration during the wet season, with the latter generating the greater annual influx. In such tropical landscapes with highly weathered soils, the ratio of Na/(Na + Ca) has been used to determine the contribution of mineral weathering to streamwater cation content. Higher ratios indicate low rates of chemical weathering and vice versa. In the Lom Basin, the majority of samples had Na/(Na + Ca) ratios approaching one during the rainfall season and dropped during decreased flow (Fig. 4d). The mineral weathering index patterns (Fig. 4d) revealed that inputs from bedrock weathering dissolved in groundwater are predominant during base flow. In addition, slightly higher concentrations of major cations during the wet season are likely related to precipitation effects as they are flushed from soil surface layers by heavy rainfall. Therefore, inputs of cations for the two sampling periods are derived from both the chemical weathering of primary minerals and their leaching from the cation-exchange complexes in surface soils.

3.2 Sources and Geochemical Behaviour of Trace Metals in Streamwater

The most significant metal loadings were those of Fe (20–5011 µg/l) and Mn (0.2–248 µg/l) reflecting metalliferous dissemination and weathering of pyrite within the basin. All water samples characterized by low concentrations (< 1 µg/l) of V, Cr, Co, Cu, Zn, Cd, Pb, and significant concentrations of As (up to 5.45 µg/l), Ni (up to 5.01 µg/l) and Hg (up to 4.98 µg/l) were within the WHO (2011) guidelines for drinking water (Table 2). The low levels and mobility of these elements are probably due to the very low aqueous solubility of the sulphide minerals in the ore deposits. Besides, these elements could likely be associated with suspended colloids or ferric oxides through adsorption phenomena (Smedley and Kinniburgh 2002). Trace metal loadings were lower than their mean concentrations in soils from the study area and the adjacent Batouri gold district (Table 2). In this strongly lateritic environment, the weathering of vein gold mineralization results in sulphide oxidation at the base of the profile. However, a significant portion of the trace metals released in the soils are trapped as lattice components in secondary mineral phases such as ferruginous oxides (Freyssinet et al. 1989) and could be released by migration via adsorption, complexation and co-precipitation in a largely acidic environment. The overall low concentration of trace metals can also be attributed to leaching into deep groundwater. This is in agreement with the high levels of trace metals reported for wells within part of the study area (Rakotondrabe et al. 2017).
Table 2

Mean concentrations of trace metals (µg/l) in streamwater compared to concentrations (ppm) in soils of the Betare-Oya and Batouri gold districts. The mean concentration of Fe in soils is expressed in wt% oxide





WHO (2011) in mg/l





























































Fe and Mn levels in some samples were above the WHO standards for drinking water. Data for soils from Betare-Oya gold district are adapted from Freyssinet et al. (1989) and for Batouri from Edith-Etakah et al. (2017)

N/A not available

Principal component analysis (PCA) of metals in streamwater conducted produced four factors explaining about 70% of the total variance (Table 3). Factor 1 had strong positive loadings on Fe, V, Cr, pH, Ni and a strong negative loading on Zn. Factor 2 was made up of strong positive loadings on Mn, As and Co, while Factor 3 showed strong positive loadings of the elements Pb-Cu-Cd. These factors represent the oxidation and hydrolysis of sulphide minerals associated with gold deposits in the study area. However, in F1, Fe plays a major role in scavenging the other trace metals at low pH. The negative contribution of Zn suggests no co-precipitation effect of Fe on it. In contrast, Mn plays a major role in scavenging As in F2 which represents a different phase of mineralization (Omang et al. 2014). Also, Mn hydroxides have been reported to precipitate at high pH than Fe (Siegel 2002) which implies that Fe and Mn scavenge at different pH of streamwater within the Lom Basin. This is because the precipitation of Fe and Mn is pH-dependent, while that of trace metals depends on their co-precipitation with Fe and Mn. Higher concentrations of dissolved As compared to the chalcophile elements Cu, Zn, and Pb; and its disassociation from this group can be attributed to the weathering of arsenopyrite or the dissolution of metals from stream sediment in near neutral to slightly alkaline waters (Nganje et al. 2011; Kelepertzis et al. 2012). Under such pH conditions as observed in the study area, As becomes more mobile compared to other metals. Although arsenopyrite has been identified as a major sulphide mineralization event within this catchment, the relatively low dissolved concentrations of As can be related to its strong tendency to adsorb on hydrous Mn oxide mineral surfaces (Smedley and Kinniburgh 2002; Cheng et al. 2009). Factor 4 is composed of Hg and pH and could likely be as a result of its adsorption to very fine colloidal particles and dissolved organic matter, which could not be retained by the 0.45 µm membrane filter. Besides, near neutral pH conditions and soil organic material tend to reduce Hg mobility (Van Straaten 2000). Gold amalgamation practiced illegally in the region has been reported as a possible source of Hg (Rakotondrabe et al. 2017).
Table 3

Factor analysis (with varimax rotation and Kaiser normalisation) and total variance explained









− 0.096


− 0.198








− 0.233






− 0.003











− 0.174





− 0.013










− 0.208







− 0.191

− 0.130









− 0.057

− 0.055



Eigen value





% Variance





Cumulative % Variance





N = 52. Values in bold represent loadings > 0.500

The metal composition of the Lom catchment based on the traditional Ficklin diagram (Ficklin et al. 1992) is shown on Fig. 5. From this plot, it is obvious that low pH is necessary for significant high metal load to occur through sulphide oxidation. Most trace metals are amphoteric and tend to dissolve forming cations at low pH, or anions at high pH (Salomons 1995), than at the near neutral pH (5.5–6.7) condition of the study area whereby the transport of most suspended and dissolved trace metals is expected to be attenuated (Cravotta 2000). Thus, the neutral pH of the streamwater accounts for the low dissolution of trace metals. Besides, greater dilution and reduced solid to water ratio occurs in wetter climates such as in the tropics. These processes result in the generation of surface water from acid generating deposits such as sulphides with low acidity and trace element content (Plumlee and Logsdon 1999). Hence, despite the past and active small scale mining operations within this area, acid generation remains low and this accounts for the low concentrations of dissolved trace metals. On the other hand, there is also a possibility that the acid generated from suphide weathering may have been consumed through reactions with silicate minerals (long-term buffering capacity) occurring in the parent rocks (Salomons 1995). In summary, the rate of acid generation is usually determined by chemical factors such as pH, temperature, gaseous and aqueous oxygen concentrations, chemical activity of ferric iron and the surface area of exposed metal sulphides as well as biologic parameters.
Fig. 5

Ficklin’s diagram of streamwater samples showing low base-metal content

4 Conclusions

For the first time, the seasonal variation of major ions and trace metal concentration of streamwater in the lower Lom Basin have been investigated. From this study, the following observations were made:
  • All measured physicochemical parameters showed no pronounced variation between the dry and wet seasons.

  • Overall, the seasonal pattern of streamwater chemistry is controlled by three key processes: (a) contribution of major cations and HCO3 from chemical weathering supplied by ground water flow, (b) leaching of salts from surface soil layers during rain events and (c) dilution by surface runoff during the wet season.

  • Trace element geochemistry revealed very low concentrations of V, Cr, Co, Cu, Zn, Cd, Pb and are attributed to deep chemical weathering and leaching into the groundwater.

  • Iron and Mn concentrations in most samples exceeded the WHO (2011) guideline values for drinking water and are associated with the occurrence of pyrite. The dissolution of sulphides into the drainage system is the principal source of base metals in streamwater.

  • Arsenic is believed to be leached from a different mineralization source and co-precipitated with Mn owing to its disassociation from the base metals Cu, Zn and Pb.

  • Drainage signatures of the basin are marked by low acidity, SO4 2− levels and base metal loadings reflecting low sulphide solubility and the likely buffering capacity of silicate minerals.

Although this study showed a relatively low seasonal variation in dissolved solutes, identifying the sources and processes governing their contribution is necessary for understanding the effects of future land use changes in the study area. Besides, despite many years of past and present small-scale mining activities, the area is currently under no risk of contamination by trace metals. Nonetheless, these findings may be considered by policymakers as a reference for setting safe limits and continuous monitoring of mining activities in the Lom Basin and other mineralized areas in Cameroon.



This paper constitutes part of the Ph.D. thesis of the corresponding author, under the auspices of the Japanese Government (MONBUKAGAKUSHO) Scholarship at the Ministry of Education, Culture, Sports, Science and Technology (MEXT). The authors thank the Japan Science and Technology Agency (JST) for funding the project and the Institute of Geological and Mining Research (IRGM) Cameroon for providing transportation facilities.


  1. Agyarko K, Dartey E, Kuffour RAW, Sarkodie PA (2014) Assessment of trace elements levels in sediment and water in some artisanal and small-scale mining (ASM) localities in Ghana. Current World Environ 9(1):07–16CrossRefGoogle Scholar
  2. Ako TA, Onoduku US, Oke SA, Adamu IA, Ali SE, Mamodu A, Ibrahim AT (2014) Environmental impact of artisanal gold mining in Luku, Minna, Niger State, North Central Nigeria. J Geosci Geomat 2(1):28–37Google Scholar
  3. Appelo CAJ, Postma D (1996) Geochemistry, groundwater and pollution. AA Balkema, LeidenGoogle Scholar
  4. Ashley RP (2002) Geoenvironmental model for low-sulfide gold-quartz vein deposits. U.S. Geological Survey Open-file Report 02–195 K, 2002, pp 176–195. Accessed 21 February 2017
  5. Bortey-Sam N, Nakayama SMM, Ikenaka Y, Akoto O, Baidoo E, Mizukawa H, Ishizuka M (2015) Health risk assessment of heavy metals and metalloid in drinking water from communities near gold mines in Tarkwa, Ghana. Environ Monit Assess 187:397CrossRefGoogle Scholar
  6. Braun JJ, Viers J, Dupré B, Polve M, Ndam J, Muller JP (1998) Solid/Liquid REE fractionation in the lateritic system of Goyoum, East Cameroon: the implication for the present dynamics of the soil covers of the humid tropical regions. Geochim Cosmochim Acta 62:273–299CrossRefGoogle Scholar
  7. Cheng H, Hu Y, Luo J, Xu B, Zhao J (2009) Geochemical processes controlling fate and transport of arsenic in acid mine drainage (AMD) and natural systems. J Hazard Mater 165:13–26CrossRefGoogle Scholar
  8. Cravotta CAIII (2000) Relations among sulfate, metals and stream flow data for a stream draining a coal-mined watershed in east-central Pennsylvania. In: Proceedings of the International Conference on Acid Rock Drainage (ICARD), Denver, Colorado: Soc Mining Metallur Explor vol 1:p 401–410Google Scholar
  9. Dan SF, Umoh UU, Osabor VN (2014) Seasonal variation of enrichment and contamination of heavy metals in the surface water of Qua Iboe River Estuary and adjoining creeks, South-South Nigeria. J Oceanogr Mar Sci 5(6):45–54CrossRefGoogle Scholar
  10. Drever JI (1997) The geochemistry of natural waters; surface and groundwater environments, 3rd edn. Prentice Hall, Upper Saddle River, pp 138–196Google Scholar
  11. Edet A, Ukpong A, Nganje T (2014) Baseline concentration and sources of trace elements in groundwater of Cross River State, Nigeria. Int J Environ Monit Anal 2(1):1–13CrossRefGoogle Scholar
  12. Edith-Etakah BT, Shapi M, Penaye J, Mimba ME, Nguemhe Fils SC, Nadasan DS, Davies TC, Jordaan MA (2017) Background concentrations of potentially harmful elements in soils of the Kette-Batouri region, Eastern Cameroon. Res J Environ Toxicol 11:40–54. Google Scholar
  13. Eneji IS, Onuche AP, Sha’Ato R (2012) Spatial and temporal variation in water quality of River Benue, Nigeria. J Environ Prot 3:915–921CrossRefGoogle Scholar
  14. Ficklin WH, Plumlee GS, Smith KS, McHugh JB (1992) Geochemical classification of mine drainages and natural drainages in mineralised areas. In: Kharaka YK, Maest AS (Eds.) Proceedings of 7th International Symposium, Water Rock Interaction, p 381–384Google Scholar
  15. Foumena WC, Bamenjo JN (2013) Artisanal Mining—a challenge to the Kimberly process: a case study of the Kadey Division, east region of Cameroon, RELUFA extractive industries programme team. Accessed 24 February 2017
  16. Franz C, Abbt-Braun G, Lorz C, Roig HL, Makeschin F (2014) Assessment and evaluation of metal contents in sediment and water samples within an urban watershed: an analysis of anthropogenic impacts on sediment and water quality in Central Brazil. Environ Earth Sci 72:4873–4890CrossRefGoogle Scholar
  17. Freyssinet PH, Lecompte P, Edimo A (1989) Dispersion of gold base metals in the Mborguene lateritic profile, East Cameroon. J Geochem Explor 32:99–116CrossRefGoogle Scholar
  18. Garizi AZ, Sheikh V, Sadoddin A (2011) Assessment of seasonal variations of chemical characteristics in surface water using multivariate statistical methods. Int J Environ Sci Tech 8(3):581–589CrossRefGoogle Scholar
  19. Grasby SE, Hutcheon I, Krouse HR (1997) Application of the stable isotope composition of SO4 2− to tracing anomalous TDS in Nose Creek, southern Alberta. Canada. Appl Geochem 12(5):567–575CrossRefGoogle Scholar
  20. Hem JD (1985) Study and interpretation of the chemical characteristics of natural water. United States Geological Survey Water Supply Paper 2254Google Scholar
  21. Hook Z (2005) An assessment of the quality of drinking water in rural districts in Zimbabwe. The case of Gokwe South, Nkayi Lupene and Nwenezi districts. Phys Chem Earth 30:859–866CrossRefGoogle Scholar
  22. Kamtchueng BT, Fantong WY, Wirmvem MJ et al (2016) Hydrogeochemistry and quality of surface water and groundwater in the vicinity of Lake Monoun, West Cameroon: approach from multivariate statistical analysis and stable isotopic characterization. Environ Monit Assess 188(9):524. CrossRefGoogle Scholar
  23. Kelepertzis E, Argyraki A, Daftsis E (2012) Geochemical signature of surface and stream sediments of a mineralized drainage basin at NE Chalkidiki Greece: a pre-mining survey. J Geochem Explor 114:70–81CrossRefGoogle Scholar
  24. Khazheeva ZI, Tulokhonov AK (2007) Dashibalova LT (2007) Seasonal and spatial dynamics of TDS and major ions in the Selenga River. Water Resour 34(4):444–449CrossRefGoogle Scholar
  25. Kpan DK, Opoku AB, Gloria A (2014) Heavy metal pollution in soil and water in some selected towns in Dunkwa-on-Offin District in the Central Region of Ghana as a result of small scale gold mining. J Agric Chem Environ 3:40–47Google Scholar
  26. Kumar M, Ramanathan Al, Roa MS, Kumar B (2006) Identification and evaluation of hydrogeochemical processes in the groundwater environment of Delhi, India. Environ Geol 50:1025–1039CrossRefGoogle Scholar
  27. Markewitz D, Davidson EA, Figueiredo RO, Victoria RL, Krusche AV (2001) Control of cation concentrations in stream waters by surface soil processes in an Amazonian watershed. Nature 410:802–805CrossRefGoogle Scholar
  28. Meybeck M (1987) Global chemical weathering of surficial rocks estimated from river dissolved loads. Am J Sci 287:401–428CrossRefGoogle Scholar
  29. Milesi JP, Toteu SF, Deschamps Y et al (2006) An overview of the geology and major ore deposits of Central Africa: explanatory note for the 1:4,000,000 map ‘‘Geology and major ore deposits of Central Africa”. J Afr Earth Sci 44:571–595CrossRefGoogle Scholar
  30. Mimba ME, Ohba T, Nguemhe Fils SC, Wirmvem MJ, Bate Tibang EE, Nforba MT, Aka FT (2017) Regional hydrogeochemical mapping for environmental studies in the mineralized Lom Basin, East Cameroon: a pre-industrial mining survey. Hydrology 5(2):15–31. CrossRefGoogle Scholar
  31. Neba A (1999) Modern geography of the Republic of Cameroon, 3rd edn. Neba, BamendaGoogle Scholar
  32. Ngako V, Affaton P, Nnange JM, Njanko TH (2003) Pan-African tectonic evolution in central and southern Cameroon: transpression and transtension during sinistral shear movements. J Afr Earth Sci 36:207–221CrossRefGoogle Scholar
  33. Nganje TN, Adamu CI, Ygbaja AN, Ebieme E, Sikakwe G (2011) Environmental contamination of trace elements in the vicinity of Okpara coal mine, Enugu, Southeastern Nigeria. Arab J Geosci 44:199–205CrossRefGoogle Scholar
  34. Nganje TN, Hursthouse AS, Edet A, Stirling D, Adamu CI (2015) Hydrochemistry of surface water and groundwater in the shale bedrock, Cross River Basin and Niger Delta Region, Nigeria. Appl Water Sci. doi:10.1007/s13201–015–0308–9Google Scholar
  35. Omang BO, Bih CV, Fon NN, Suh CE (2014) Regional geochemical stream sediment survey for gold exploration in the upper Lom basin, eastern Cameroon. Int J Geosci 5:1012–1026CrossRefGoogle Scholar
  36. Omang BO, Suh CE, Lehmann B, Vishiti A, Chombong NN, Fon A, Egbe JA, Shemang EM (2015) Microchemical signature of alluvial gold from two contrasting terrains in Cameroon. J Afr Earth Sci 112:1–14CrossRefGoogle Scholar
  37. Plumlee GS, Logsdon MJ (1999) An earth-system science toolkit for environmentally friendly mineral resource development. In: Plumlee GS, Logsdon MJ (eds) The environmental geochemistry of mineral deposits, part a. Processes, techniques, and health issues. Soc Econ Geologists, Littleton, pp 1–27Google Scholar
  38. Rakotondrabe F, Ndam Ngoupayou JR, Mfonka Z, Rasolomanana EH, Nyangono Abolo AJ, Ako Ako A (2017) Water quality assessment in the Betare-Oya gold mining area (East Cameroon): multivariate statistical analysis approach. Sci Total Environ 610–611(2018):831–844Google Scholar
  39. Salminen R, Tarvainen T, Demetriades A et al (1998) FOREGS Geochemical mapping field manual. Geol Surv Finl Guide 47:16–21Google Scholar
  40. Salomons W (1995) Environmental impact of metals derived from mining activities: processes, predictions, prevention. J Geochem Explor 52:5–23CrossRefGoogle Scholar
  41. Siegel FR (2002) Environmental geochemistry of potentially toxic metals. Springer-Verlag, Berlin, HeidelbergGoogle Scholar
  42. Simbarashe M, Reginald K (2014) Environmental monitoring of the effects of conventional and artisanal gold mining on water quality in Ngwabalozi River, southern Zimbabwe. Int J Eng Appl Sci 4(10):8269Google Scholar
  43. Singh AK, Mondal GC, Singh PK, Singh TB, Tewary BK (2005) Hydrochemistry of reservoirs of Damodar River basin, India: weathering processes and water quality assessment. Environ Geol 8:1014–1028CrossRefGoogle Scholar
  44. Smedley PL, Kinniburgh DG (2002) A review of the source, behaviour and distribution of arsenic in natural waters. Appl Geochem 17:517–568CrossRefGoogle Scholar
  45. Soba D, Michard A, Toteu SF, Norman DI, Penaye J, Ngako V, Nzenti JP, Dautel D (1991) Donnéés géochronologiques nouvelles (Rb–Sr, U–Pb et Sm–Nd) sur la zone mobile pan-africaine de l’Est Cameroun: âge Proterozoïque superieur de la série du Lom. Comptes Rendus Acad Sci 312:1453–1458Google Scholar
  46. Toteu SF, Van Schmus RW, Penaye J, Michard A (2001) New U–Pb and Sm–Nd data from north central Cameroon and its bearing on the pre-pan-African history of Central Africa. Precambr Res 108:45–73CrossRefGoogle Scholar
  47. Toteu SF, Penaye J, Poudjom DY (2004) Geodynamic evolution of the Pan-African belt in Central Africa with special reference to Cameroon. Can J Earth Sci 41:73–85CrossRefGoogle Scholar
  48. Toteu SF, Penaye J, Deloule E, Van Schmus WR, Tchameni R (2006) Diachronous evolution of volcano-sedimentary basins north of the Congo craton: insights from U-Pb ion microprobe dating of zircons from the Poli, Lom and Yaounde Series (Cameroon). J Afr Earth Sci 44:428–442CrossRefGoogle Scholar
  49. Uwah IE, Dan SF, Etiuma RA, Umoh UU (2013) Evaluation of status of heavy metals pollution of sediments in Qua-Iboe River Estuary and associated creeks, south-eastern Nigeria. Environ Pollut 2(4):110–122CrossRefGoogle Scholar
  50. Van Straaten P (2000) Mercury contamination associated with small-scale gold mining in Tanzania and Zimbabwe. Sci Total Environ 259:105–113CrossRefGoogle Scholar
  51. WHO (2011) Guidelines for drinking water quality, 4th edn. WHO, Geneva, p 564pGoogle Scholar

Copyright information

© Springer International Publishing AG, part of Springer Nature 2017

Authors and Affiliations

  • Mumbfu Ernestine Mimba
    • 1
    • 2
  • Takeshi Ohba
    • 1
  • Salomon César Nguemhe Fils
    • 2
  • Mengnjo Jude Wirmvem
    • 2
  • Nozomi Numanami
    • 1
  • Festus Tongwa Aka
    • 2
  1. 1.Department of Chemistry, School of ScienceTokai UniversityHiratsukaJapan
  2. 2.Institute of Geological and Mining Research (IRGM)YaoundeCameroon

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