Water is the most consumed food; it is a vital element for the human being. It is necessary for health, agriculture, industry, tourism, leisure and navigation. Having water in both quality and quantity is important to ensure a safe and healthy life in the long term [1].

Despite its importance and low exploitable availability, water is subject to anthropogenic pressures that modify its quality and lead to an imbalance or disappearance of aquatic ecosystems (fauna and flora). Human activities are likely dangerously to compromise the quality of surface water and groundwater include agriculture [2] [3].

At the same time, agriculture is an important sector for global development. It is the second largest source of employment in the world. From a historical standpoint, cotton production is the main driver of the national economy growth in West Africa. Around 3 millions of people live directly and indirectly on cotton production in Benin [4]. It contributed to the earnings from official export for about 70% in Benin and to the GDP for about 20% in 2017 in Benin according to European Union Speech of September 2018.

At the current stage of development, the use of agricultural inputs is essential to increase the yield and protection of cotton. The negative effects from agricultural inputs were noted 20 years after their first synthesis in the 1940s [5]. Cotton production consumes about 80% of chemical fertilizers and 90% of pesticides used in Benin. To the best knowledge of several authors [2] [6] [7] [8], the use of Organochlorine pesticides (prohibited products), including endosulfan, DDT and its derivatives by farmers is common in Benin. The impacts of organochlorine pesticides on the environment in Benin were noted by these authors. For the agricultural campaign 2008-2009, about 1000,000 liters of pesticides were used to produce 210,000 tons of cotton CSPR 2010 [9] (Agbohessi, 20 11) against a production of 269,222 tons 2015-2016 and 597,986 tons in 2017-2018 which induces an increase in pesticide use.

The dispersion of non-usable pesticides contaminates water, soil, and air; this could affect humans (toxicological) and other living organisms (ecotoxicological effects) [10]. Non-usable chemical fertilizers by plants contribute to eutrophication of water bodies and lead to anarchic proliferation of unwanted organisms (aquatic plants) [2] (Soclo, 2003). These phenomena lead to an imbalance of the ecosystem and generate pollutants that can affect the physico-chemical and biological quality of the receiving aquatic areas. It is well known that the quality of water of an aquatic ecosystem influences its biological diversity [11] [12] [13]. The impact of pollutants on the environment is complex; their toxic actions can be direct or indirect on ecosystems. The sources of the degradation of the environment and that of human health are the same. Unlike organic pollutants that are very persistent, Trace Metal Components (TMC) are persistent and may accumulate in sediments. The sources of the TMC can include phosphate based chemical fertilizers [14] [15], pesticides, and also domestic and industrial wastes [16]. Cu and Zn, which are trace elements, can become toxic at high concentrations [17]. Hg and Pb, which have no known biological utility, are dangerous and toxic even in very small quantities [18]. Thus, the water pollution by TMC is an important factor of aquatic ecosystems destruction. Sediments are often a reservoir of chemical components such as persistent organic pollutants (POPs) and metals, which fixe to suspended particles owing to their hydrophobicity and/or high affinity for organic matter or metal oxyhydroxides, [19]. The assessment of the surface water quality is based on the measurement of physico-chemical parameters, toxicity tests and the presence or absence of aquatic organisms and micro-organisms, which are indicators of water quality [20].

Water was collected from river using 1.5-L plastic vials, which were pre-washed with a 10% acid solution and then rinsed three times using simple water and distilled water. Prior to sampling, the plastic vials were thoroughly rinsed with the river’s water from each site. Water was then collected in the washed plastic vials about 5 cm from the surface of the river and stored in cool boxes for use in laboratory.

Sediment was sampled from medium-depth horizons, packed in bags (polyethylene bag) and then stored in cool boxes.

Sample preparation and analysis

The Different physicochemical parameters (PH, temperature, TDS) were determined in the field using a multiparamètre device and pH meter.

The sampled water was directly analyzed in the laboratory using a DR 2800 spectrophotometer for determination of the chemical parameters including NH 4 + , NO 3 − , NO 2 − , PO 4 3 − as well as Cu and Zn. The measurement of Pb and Cd in the water was carried using DR 3000 Metalyser.

The sampled sediments were dried at 105˚C for 24 hours (constant weight), then crushed, sieved at 2 mm and homogenized. A sample of 1g of the sediment was mineralized with aqua regia (mixture of hydrochloric and nitric acid), then analyzed for Cu²⁺ and Zn²⁺ using spectrophotometer DR 2800, and for Pb and Cd by Métalyser.

The analysis in Table 1 shows that the temperature of the river varied with season and sampling time, ranging from 24.80˚C to 27.60˚C during the rainy season and from 30.00˚C to 32.00˚C during the dry season. Thus, the temperature of the sampled water exceeded the standards of 25.00˚C set for the dry season.

SS: Dry season; SP: Rainy season; FSP: End of the Rainy season.

Water pH increased from the dry season to the rainy season, ranging from 6.37 to 6.62 in the dry season, from 6.40 to 7.10 in the rainy season and from 6.90 to 7.40 at the end of the rainy season. Water pH recorded in the rainy season (6.50 - 8.50) was consistent with the standards set by the World Health Organization standards for drink water, by the IGBE for surface water and for water resources protection.

The TDS value recorded in the dry season is superior to that recorded in the rainy season.

ü Nitrite

From Figure 3, the nitrite concentrations in the river varied from 1.00 mg·L⁻¹ to 20.00 mg·L⁻¹ in the rainy season, which exceeded the standards set by WHO (3 mg·L⁻¹) and IGBE (3 mg·L⁻¹) with the exception of site 2.

ü Nitrate

The nitrate concentrations of the river ranged from 2 mg·L⁻¹ to 7.20 mg·L⁻¹ in the rainy season and from 0.40 mg·L⁻¹ to 2.25 mg·L⁻¹ in the dry season (Figure 4). These values were lower than the WHO standard (50 mg·L⁻¹) and the simplified assessment grid for river’s water quality.

ü Phosphate

The analysis in Figure 5 shows that the phosphate concentrations in the river’s water in the dry season were superior to those recorded in the rainy season, ranging from 1.07 mg·L⁻¹ to 2.53 mg·L⁻¹. The river’s water is of poor quality according to grid-quality of surface water as the recorded concentrations in phosphate were between 1 mg·L⁻¹ and 5 mg·L⁻¹.

Trace metal elements

ü Zinc in the waters

From Figure 6 the Zn concentrations in the river’s water during the dry season were higher than in the rainy season and varied from 1.51 to 4.79 mg·L⁻¹. They exceeded the standards set by the IBGE (0.30 mg·L⁻¹) and for heavy metal concentrations in surface waters (EC Directive).

ü Copper in the waters

Copper concentrations in the river’s waters were very low whatever the season with the exception of the sites S3 and S6 of which copper concentrations at the end of the rainy season were superior to 47.60 mg·L⁻¹ and 55.60 mg·L⁻¹, respectively (Figure 7). The copper concentrations in the river’s water at the sites S3 and S6 were over the standards set for heavy metal concentrations in surface water (EC Directive) (mg·L⁻¹).

ü Lead in the waters

Figure 8 shows that the Concentrations of Pb in the waters of the river during the dry season were superior to the standards set by the IBGE and for heavy metal concentrations in surface waters (EC Directive) (0.05 mg·L⁻¹).

Cadmium in the waters

From Figure 9 the Cadmium concentrations in the river’s waters were low during the rainy season with the exception of the site 2 of which cadmium concentrations was 4.32 mg·L⁻¹. During the dry season, cadmium concentrations in the river’s water were over the standards set by the IBGE and for heavy metal concentrations in surface waters (EC Directive) (0.005 mg·L⁻¹).

Sediment

ü Zn in the sediment

The concentrations of the Zn in sediments during the rainy season are higher than in the dry season (Figure 10). They vary from 102.00 to 175.00 mg·kg⁻¹ during the rainy season, from 20.00 to 35.00 mg·kg⁻¹ at the end of the rainy season and 0.01 to 15.6 mg·kg⁻¹ in the dry season. The concentrations of the Zn in sediments during the rainy season exceeded France standards (80.00 mg·kg⁻¹).

Copper in the sediment

Copper concentrations in sediments during the rainy season were higher than in the dry season (Figure 11). They varied from 69.00 to 231.00 mg·kg⁻¹ in the rainy season, which were superior to the France standards (26 mg·kg⁻¹).

Lead in sediment

Concentrations of Pb in sediments were high during and at the end of the rainy season at sites S1 (9.42 - 18.32 mg·kg⁻¹) and S2 (20.58 - 14.40 mg·kg⁻¹), and in the dry season at sites S6 (4.05 mg·kg⁻¹) and S7 (23.00 mg·kg⁻¹) (Figure 12). Lead concentrations in sediments were lower than France standards (22 mg·kg⁻¹) with the exception of site S7 where the Pb concentrations in sediments during the dry season.

ü Cadmium in the sediment

Figure 13 shows that the Concentrations of Cd in sediments were 52.50 mg·kg⁻¹ during the rainy season at the site S7 and 10.50 mg·kg⁻¹ during the dry season at the site S6. They were low at other sites. In contrast to river’s waters at the sites S6 and S7, the presence of metal in the sediment is related to the bioavailable fraction.

The vulnerability of rivers in the cotton zone of Benin is in increase, due to the

common and intensive use of chemical fertilizers and pesticides, which are known to exhibit harmful effects on the environment (soil, air, surface water and underground). Surface waters are the most vulnerable to pollution resulting from the use of these chemical products.

The average temperatures recorded were 31.47˚C in the dry season, 27.02˚C during the rainy season and 26.26˚C, which were lower than the temperature of 28˚C found in 2012 for the same river [21] at the end of the rainy season in the period from October to December. In agreement with the present study, recorded temperatures of 21.00˚C to 25.40˚C in the rainy season and 30.10˚C to 32.10˚C in the season dry in 2002 in ponds, rivers and hunting zones of the reserve of W and its hunting. Djibril (2002) reported temperatures of 27.94˚C to 28.20˚C for the waters from ponds and rivers of the Biosphere Reserve of Pendjari in 2002 [22], and Bassirou reported temperatures of 21.60˚C to 26.40˚C for the Niger River in 2003, which are consistent with our results as regards temperatures measured during the rainy season. The observed increase of the temperature in the dry season is related to climate; it can lead to a reduction in gases solubility in water including oxygen and influence water density. According to the France standards (26.50˚C; 35.00˚C) and Dedjiho (2011), various temperatures recorded exhibit no effect on the growth of aquatic species [23].

The temperature influences the pH of a solution, which is an important parameter in the assessment of water quality and the form of certain chemical species. The pH indicates the quantity of ions H₃O⁺ as well as the nature of the solution. The average values of the pH recorded in river’s waters were 6.48 in the dry season, 6.71 in the rainy season and 7.24 at the end of the rainy season. The low pH observed in the dry season may be due to a decrease in the volume and the increase in the temperature of the river’s waters. The recorded pH is lower than those reported by Agblonon; in 2012 for the same river [21] and Soclo in 2003 for the pools and rivers of the W reserve and its hunting areas [2]. These differences may arise due to differences in the amount of the chemical substances resulting from an intensive use of chemical fertilizers and pesticides during those years. Our results are also slightly lower than the pH found by Chouti in 2016 for the coastal lagoon (7.32) [24] and the river Mono (7.76) in 2018 [25], and that recorded by Wahalaa in 2016 for the river Litani in Lebanon (7.70) [26], where agriculture activities were not developed.

The present study reveals the average concentrations in nitrite in Alibori river’s waters were 6.72 mg·L⁻¹ in the rainy season and 3.57 mg·L⁻¹ at the end of the season rainy. They are higher than those measured by Agblonon in 2012 in the same river’s waters (0.04 mg·L⁻¹) [25], Soclo in 2003 in the pools and rivers of the W reserve and its hunting areas (0.08 mg·L⁻¹- 0.56 mg·L⁻¹) [2] and Djibril in 2002 in the same zone (0.31 mg·L⁻¹ - 200 mg·L⁻¹) [22]. The divergence between our results and these previous studies conducted in the same region and season may be due to the increase in the chemical fertilizers and pesticides amount used and cropland area during the recent years.

Our results also contradict other authors who reported the concentrations in nitrite of 0.002 - 0.005 mg·L⁻¹ for waters from an affluent of the Alibori river known as Niger River in 2006 (Bassirou, 2009) [27], and 0.13 mg·L⁻¹ for waters from the delta of the Ouémé River [28].

The average nitrate concentrations in the river’s waters were 0.96 mg·L⁻¹ during the dry season, 4.20 mg·L⁻¹ during the rainy season and 4.76 mg·L⁻¹ at the end of the rainy season, which suggest a lack of oxygen necessary for the oxidation of the nitrite ions to nitrate by Nitrobacter. The author previously reported that nitrification and dénitrification reactions were incomplete in some water rich in nitrite and classified that kind of water suspicious. Thus, the findings from the current study indicate a pollution of the waters from Alibori River by nitrite during cultivation period. The observed decrease in nitrite concentration and increase in nitrate concentration in Alibori river’s waters at the end of the rainy season may be due to a slow oxidation of the nitrites ions to nitrate [29] [30] [31]. The authors reported in their previous works that eutrophication and degradation of organic matter may lead to oxygen deficiency and hence the limitation of the nitrification reaction. Nitrites are specifically harmful to young fishes and cause a dramatic drop in oxygen in the environment up to anoxia, which entailed a loss of biodiversity [29]. The observed disappearance of certain species in waters of Alibori River in 2012 by Agblonon [25].

Besides nitrite and nitrate, phosphate ions are part of elements responsible for eutrophication. The average concentrations of phosphate ions measured in waters of the Alibori River were 1.86 mg·L⁻¹ in dry season, 0.21 mg·L⁻¹ during the rainy season and 0.16 mg·L⁻¹ at the end of the rainy season. They are over 0.10 mg·L⁻¹ and may cause eutrophication in waters of the Alibori River.

In sum, the relatively high concentrations of nitrite and phosphate in the waters of Alibori River are pollution indexes and may make their quality unfit for drinking, aquatic life and watering animals.

The average concentrations of Zn and Cu in the waters of the Alibori River were, respectively, 2.96 mg·L⁻¹ and 0.72 mg·L⁻¹ in the dry season, 0.05 mg·L⁻¹ and 0.19 mg·L⁻¹ in the rainy season, and 0.07 mg·L⁻¹ and 14.74 mg·L⁻¹ at the end of the rainy season. In the sediments, the average concentrations of Zn and Cu were, respectively, 5.90 mg·kg⁻¹ and 10.85 mg·kg⁻¹ in the dry season, 121 mg·kg⁻¹ and 120 mg·kg⁻¹ during the rainy season and 28.14 mg·kg⁻¹ and 12.61 mg·kg⁻¹ at the end of the rainy season. Our results reveal that metals such as Zn, Cu, Cd and Pb were more concentrated in sediments during the rainy season, which may be explained by the fact that they are bound to organic matter mixed into the soil and drained by run-off in the river and also depend on the pH of the environment. The MTC is released in the water along with organic maters degradation, entailing the increase of their concentrations during the dry season. The highest concentrations of the MTC were recorded at the sites highly populated and dominated by the cultivation of the river bank without the recommended minimum interval. The concentrations in Zn and Cu in waters and sediments from Alibori river recorded here were higher than those measured in coastal lagoon in 2016 (Zn: 0.15 mg·L⁻¹ and 64.40 mg·kg⁻¹; Cu: 0.13 mg·L⁻¹ and 27.23 mg·Kg⁻¹) by Chouti [28]. These differences may arise due to the use of the chemical fertilizers and pesticides for agriculture purposes as the river is located in a rural area dominated by agricultural activities.

This study has enabled a better understanding of the degree of pollution of the Alibori River. The results reveal that the physico-chemical parameters of the river’s water and sediments did not meet almost all the standards. Thus, the waters and sediment of the Alibori river were of poor quality and hence unfit for aquatic species and fauna whatever the period. The river of Alibori was polluted by metal since concentrations of the waters and sediments in TMC (Cu, Zn, Pb, Cd) exceeded the standards set for aquatic species protection and drinking water. The concentrations of the nitrites in the river’s water and sediments were over the standards in the cultivation period during the rainy season due to the intensive use of chemical fertilizers and pesticides for agriculture purposes. However, a better assessment of the chemical fertilizers and pesticides’ impacts on the environment in the region requires the evaluation of the availability of pesticides in the different matrices, the mobility of MTC and their transfers in the food chain.

The authors declare no conflicts of interest regarding the publication of this paper.

Chitou, N.E., Chouti, W.K., Kouazounde, J. and Mama, D. (2019) Physico-Chemical Characterization of Waters and Sediments of Basins in the Cotton Area in Benin: Case of the Alibori Basin in the Commune of Banikoara North of Benin. Journal of Environmental Protection, 10, 1436-1449. https://doi.org/10.4236/jep.2019.1011085