We conducted a microbiological and toxicological profiling of a pharmaceutical wastewater, one of the major wastes entering the Lagos lagoon. The morphological characterization of seven bacterial isolates from the wastewater indicated that 4 of them were gram positive bacilli while 3 were cocci of both gram reactions. The bacterial isolates exhibited varying degrees of enzyme activities but most were able to hydrolyze starch to yield amylase. Only 3 of the isolates showed prospects as antibacterial agents, given their moderate inhibition to Staphylococcus xylosus relative to 8 other species tested. Overall, 81.3% of the isolates were resistant, and 3.3% were susceptible while 15.4% of the isolates showed intermediate sensitivity to the antibiotics. The assessment of antioxidant activities in liver samples of Nile tilapia, Oreochromis niloticus, exposed to sublethal concentrations of the effluents indicated some form of oxidative stress given the higher levels of lipid peroxidation product, malondialdehyde, in the exposed fishes relative to the control kept in dechlorinate tap water. But for reduced glutathione, activities of the antioxidative stress enzymes, superoxide dismutase (SOD), catalase (CAT), and glutathione-s-transferase (GST), were higher in the effluent exposed tilapia. Responses were not dose dependent and enzyme activities were often higher at day 14 compared to day 28. This relevance of the findings to water quality was discussed.

1. Introduction

The fate of pharmaceutical effluents in aquatic environments is increasingly eliciting scientific inquiry owing to recent findings of their effects in biological systems [1]. Nigeria has a few pharmaceutical companies most of which are situated in Ogun and Lagos States in the country’s south western region, discharging effluents into neighbouring rivers, creeks, and lagoons. Pharmaceutical effluents are wastes generated by pharmaceutical industries during the process of drug manufacturing [2]. These wastes by virtue of their source are composed of a variety of biologically active chemical components including antibiotics, lipid regulators, anti-inflammatories, antiepileptics, tranquilizers, oil and grease [3], heavy metals [4], and myriads of other compounds depending on the drug or personal care products being manufactured. Pharmaceutical effluents particularly those rich in contraceptives have also been linked with endocrine disrupting effects [5]. Microbial actions on effluents often result in products which may also interfere with endocrine functions. Mycobacterium smegmatis is known to metabolize stigmasterol in effluents into a potent androgen, androstenedione [6]. Exposure of aquatic organisms to androgenic or estrogenic compounds in pharmaceutical wastes and sewage is a known cause of sex reversal in fishes which could impair reproductive success [7].

Industrial wastewater management systems in Nigeria are either nonexistent, inappropriate, or at best inefficient. When efforts are made towards effluent management, basic dilution, filtration, sedimentation, and aeration techniques are usually put in place and these may not have the capacity to break down the chemical components of the effluents. These effluents eventually end up in natural water bodies where they cause contamination of water and toxic effects on the biotic communities [8]. Effluents typically contain various components, some of which could have the tendency to combine with the unsaturated fatty acids of the phospholipids of cell membranes leading to oxidative damage and release of byproducts such as malondialdehyde [9]. The resulting oxidative damage and the reactive oxygen species are continually countered by the action of antioxidative stress enzymes such as superoxide dismutase (SOD), catalase (CAT), and glutathione-s-transferase (GST) [9].

In view of the fate of pharmaceuticals in our environment and the growing concerns over their biological effects, we therefore conducted an extensive microbiological profiling and toxicological evaluations using the Nile tilapia, Oreochromis niloticus (a commonly bred fish for laboratory studies in Nigeria), of pharmaceutical wastewater from an industrial estate in the South-West of Nigeria. The term wastewater is used in this study to represent effluents which have not yet been discharged into the environment.

2. Materials and Methods

2.1. Sample Collection

Wastewater was sampled from the reservoir of a pharmaceutical company in industrial estate, at Agbara, the South-West of Nigeria. Untreated wastewater sample from the production of ciprofloxacin was collected directly into a 4-liter sterile plastic container and put on ice and immediately taken to the laboratory for routine microbiological, toxicological, and biochemical analyses. Storage was at 4°C prior to analysis and assays.

2.2. Assessment of the Physicochemical Characteristics of the Effluents

The wastewater sample was analyzed for basic physicochemical characteristics using standard methods as described by APHA-AWWA-WEF [10]. The parameters analysed in the effluent sample included pH, salinity, conductivity, total dissolved solids (TDS), dissolved oxygen (DO), biological oxygen demand (BOD), chemical oxygen demand (COD), iron (Fe), zinc (Zn), copper (Cu), nickel (Ni), and cadmium (Cd). Specifically, the heavy metal concentrations were measured using atomic absorption spectrophotometer, after the samples have been subjected to acid digestion. Determination of DO level was not possible in situ; thus, samples were stored cool (4°C) at the point of collection and transported to the lab for immediate analysis, while other analyses were carried out within 1 week of sampling. Also all glassware was subjected to heat and acid wash before use to prevent contamination and false readings.

2.3. Determination of THC

The analysis for total hydrocarbon content (THC) of the sample was done using ASTM D 2887-93 method [11] on an Agilent 4890D gas chromatograph/flame ionization detector subjected to prior calibration using a known standard (Sigma Aldrich, USA).

2.4. Microbiological Analysis
2.4.1. Isolation of Microorganism

One mL of water sample was added to 9 mL of sterile distilled water and a tenfold serial dilution was done, and the lower, middle, and high dilutions were plated in duplicate into nutrient agar (Biotec; UK), MacConkey agar, and potato dextrose agar plates already prepared. These were incubated at 37°C for 18–24 hrs for total bacteria and coliforms. Also, incubation for 3 to 5 days at 27°C (Rm temp.) was achieved for fungi isolates. Colonies on plates were observed and counted and the population density was estimated; bacterial colonies were picked according to their cultural morphology on the plates and these were streaked on new nutrient agar plates for pure colonies [12].

2.4.2. Morphological and Enzymatic Assay of Bacterial Isolates

The morphological characteristics of isolates were observed and recorded and this was the basis for the isolation of colonies. The cell shape and arrangements of isolates were determined following the standard procedures of basic stain, gram stain [12]. The isolates were screened for the presence of protease, amylase, and phospholipase using methods as described by Talaro [13].

2.4.3. Screening for Antibacterial Agent

All isolates were screened for antibacterial activity against 8 types of clinical bacterial species, obtained from Lagos University Teaching Hospital (LUTH), using the agar well diffusion method as described by John et al. [14]. Overnight bacterial cultures in nutrient broth were standardized and adjusted to a McFarland standard of 0.5 which is equivalent to approximately 108 cfu/mL. The already prepared Mueller Hinton agar plates were swabbed with the different clinical bacterial isolates with a sterile swab stick; this was done by streaking the swab over the entire surface of the Mueller Hinton agar plates and the plates were rotated 60° and the streaking was repeated until the entire plate was swabbed. Complete inoculation was done by running the swab around the rim of the agar plates. The lid of the plates was left open for about 5 minutes to allow any excess moisture to be absorbed before boring the agar with a sterile cork borer. Few drops of about 0.1 mL of the test bacterial isolate were introduced using a 100 μL micropipette into the wells and this was repeated for all the swabbed clinical bacterial isolates. The clinical bacteria used are four gram positive bacteria (Staphylococcus xylosus, Staphylococcus warneri, Staphylococcus epidermidis, and Enterococcus faecalis) and four gram-negative bacteria (Pseudomonas aeruginosa, Proteus mirabilis, Shigella sp., and Salmonella sp.). The plates were incubated at 37°C for 24 hrs. The assay for antimicrobial properties was determined by measuring the diameter of the inhibition zone around the wells and interpretation of results was expressed as moderate (6 to 9 mm), strong (10 to 14 mm), or very strong (15 to 18 mm) according to Liasi et al. [15].

2.5. Determination of the Acute Toxicity of the Effluent
2.5.1. Selection and Acclimatization of Test Fishes

The Nile tilapia Oreochromis niloticus fingerlings, measuring an average of  cm, were obtained from a commercial fish farm in Badagry on the outskirts of Lagos. The fishes were transported in aerated plastic tanks and acclimatized for 1 week in dark plastic tanks (stocking density: 10 fishes per litre, photoperiod: 12 hrs dark 12 hrs light). The fish stock selected for the assay recorded mortality of less than 1% after 1 week of acclimatization in the laboratory.

2.5.2. Bioassay Procedure

Wastewater samples were removed from storage in the fridge (4°C) and allowed to adjust to room temperature, until the temperature of the samples was approximately equal to those of the water in the bioassay tanks (about 26°C). The bioassay tanks had a stocking density of 10 fingerlings per litre and concentrations were set in duplicate, with each bioassay repeated twice after an initial range finding experiment.

Quantal response of mortality was employed in assessing effluent toxicity based on established techniques [16] and the 96-hour LC50 of the effluent samples acting against the tilapia fingerlings was used in determining the sublethal concentrations for the biochemical assays.

2.6. Assessment of Biochemical Responses of O. niloticus Exposed to the Pharmaceutical Effluent

After 14 and 28 days of exposure of the fingerlings to sublethal concentrations of the pharmaceutical effluent (1/10th 96-hour LC50 = 5.120 mL/L; 1/100th 96-hour LC50 = 0.512 mL/L), their liver samples were excised using a sterile dissecting set after a sharp blow to their head to immobilize them. (Ethical permit was in line with the Zoology Department, University of Lagos standard for fair treatment of lab animals.)

The liver samples were collected in unused universal bottles prior to analysis. The samples were assessed for the lipid peroxidation product, malondialdehyde (MDA), using the thiobarbituric acid reaction (TBARS) assay as described by Yagi [17]. Also antioxidative stress enzyme activities were assessed using established techniques as follows: superoxide dismutase [18], catalase [19], reduced glutathione as nonprotein sulfhydryls [20], and glutathione-s-transferase based on their relatively high activity with 1-chloro-2,4-dinitrobenzene as a second substrate [21].

2.7. Statistical Analysis

The Probit assay was used to determine the dose-response of mortality using independent sample -test and two-way ANOVA (SPSS Version 16). The software used was SPSS Version 16 to determine the 96-hour LC50 (i.e., the median lethal concentration that causes 50% mortality of the exposed fingerlings).

3. Results

3.1. Physicochemical Characteristics of the Pharmaceutical Effluent

The physicochemical characteristics of the pharmaceutical effluents showed that it was slightly acidic, with some considerable levels of electrical conductivity. There was also low level of dissolved oxygen and evidence of degradation action of microorganisms with BOD and COD levels of 36.0 and 72.0 mg/L, respectively. The effluent was low on heavy metals except for iron and manganese which were high in concentrations (Table 1).

3.2. Microbiological Assessments of the Pharmaceutical Effluent

The initial characterization of the microbial population densities from the effluent indicated a bacterial and total fungal count of  cfu/mL and  cfu/mL, respectively. There was no evidence of coliform growth when samples were cultured on MacConkey agar, thus implying that there was no faecal contamination in the effluent.

3.2.1. Morphological Characteristics of Isolates

An assessment of the cultural characteristics of the isolates observed on plates indicated that the seven isolates were mostly circular in form except for isolate ME6 (Table 2). The isolates were all opaque and smooth, with two of them being gram negative while the other four were gram positive. Also, cellular morphology showed that four of the isolates are rods while three are cocci. All but one of the cocci were gram negative, while all the rods were gram positive and the pigmentation of isolates ranged from milky white to yellow (Table 2).

3.2.2. Assessment of Enzymatic Assay of Bacterial Isolates

Four isolates (ME2, ME4, ME5, and ME7) were observed to hydrolyze starch, producing amylase, of which two ME4 and ME5 produced high amylase activity. The only bacterial isolates that possessed moderate protease activity and high phospholipase activity were ME4 and ME7, respectively, (Table 3).

3.2.3. Inhibitory Spectrum of Antibacterial-Producing Bacteria on Clinical Isolates

The isolates were tested for their ability to produce inhibitory substances against 8 indicator species (Table 4). Isolates ME2, ME3, and ME7 amongst others showed moderate inhibition zones of 3 mm, 6 mm, and 8 mm, respectively, against gram positive Staphylococcus xylosus.

3.2.4. Antibiotic Susceptibility Pattern of Bacterial Isolates

Susceptibility test of the isolates using the Kirby-Bauer method as shown in Table 5 indicated that bacterial isolates ME3, ME5, and ME6 were resistant to all 13 antibiotics tested, although other isolates revealed some level of resistance to some of the antibiotics as well. The pattern of susceptibility is as shown in Figure 1. Overall, 81.3% of the isolates were resistant, and 3.3% of the isolates were susceptible while 15.4% showed intermediate sensitivity to the antibiotics (Figure 2).

3.2.5. Acute Toxicity of the Pharmaceutical Effluents on Oreochromis niloticus

The results of the acute toxicity studies on O. niloticus indicate a generally low to moderate toxicity. On the basis of derived 96-hour LC50 values, the wastewater was found to have a LC50 value of 51.20 mL/L (Table 6).

Biochemical responses products in Oreochromis niloticus were exposed to sublethal concentrations of pharmaceutical wastewater.

3.2.6. Lipid Peroxidation

The aldehyde byproduct of lipid peroxidation, MDA, was lower in the control at both days 14 and 28 relative to the wastewater exposed tilapia groups (Figure 3). Specifically, the MDA levels at day 14 were significantly lower () in the control group than those exposed to the wastewater. However, by day 28 of the experiments, the levels, though lower in the controls, did not vary significantly with those in the effluent exposed groups. Among the exposed groups, MDA was higher in those exposed to 1/100th 96 hrs LC50 () at day 14 but the reverse was the case by day 28, with those exposed to the 1/10th 96 hrs LC50 having a significantly higher level () of MDA (Figure 3).

3.2.7. Superoxide Dismutase

The activities of SOD in the liver samples from the exposed O. niloticus were observed to reduce significantly (), between the 14th and 28th days of assessments except in the control samples. The least as well as the highest SOD activities in the tilapia fingerlings were recorded at days 14 and 28, respectively, in the control individuals (Figure 4). Also, SOD activity was lower in those exposed to 1/10th 96 hrs LC50 at both days 14 and 28 of exposure but the difference was not significant ().

3.2.8. Catalase

Catalase enzyme activity was least at day 14 in control tilapia fingerlings and its levels were significantly lower () than in those exposed to 1/10th and 1/100th of the LC50 (). Among the wastewater exposed group, 1/10th 96 hrs LC50 concentration induced higher activity at day 14 but the reverse was the case by day 28 (Figure 5).

3.2.9. Reduced Glutathione

The extent of glutathione reduction (GSH) was highest in the control fingerlings at day 14 and least in those exposed to 1/10th 96 hrs LC50 concentrations. The reverse was the case by day 28 with those exposed to 1/10th 96 hrs LC50 having the highest GSH levels while the least was recorded in those exposed to 1/100th 96 hrs LC50 () (Figure 6).

3.2.10. Glutathione-S-Transferase

Much as with SOD, the GST enzyme activities were the least in the control group at day 14 and highest in those exposed to 1/100th 96 hrs LC50 concentration (Figure 7). By the 28th day of the study, the reverse was the case as control fingerlings had the highest GST activity () followed by those exposed to 1/100th LC50 concentrations. In this case, as with SOD, those exposed to 1/10th 96 hrs LC50 concentration of the wastewater recorded the least levels of GST at day 28 (Figure 7).

4. Discussion

In this preliminary study, we have successfully established that the bacterial isolates from the pharmaceutical wastewater investigated revealed multidrug resistant strains probably as a result of selective pressure from drug polluted waste wastewater and this is of public health concern. There is an indication of enzyme and antibiotic production of industrial application from some of the bacterial isolates. Thus there is a need to exploit this opportunity to evaluate them for safety and toxicity to humans, animals, and the environment.

The findings from this study also showed that these bacterial isolates might be a potential source of antibacterial agent used to treat disease caused by Staphylococcus xylosus. The antibacterial substance produced by these isolates (ME2, ME3, and ME7) might be utilized if further work is done to study the possibilities of them being potential therapeutic agents for applications in the pharmaceutical industries.

Further studies will be done to identify the species of all the isolates, and the most widely used method for identification is genetic techniques such as the 16S rRNA gene analysis for phylogenetic study [22].

Nonetheless, the toxicity of the wastewater to fingerlings of the tilapia, O. niloticus, implies that there is a need for proper treatment measures prior to discharge in order to protect sensitive aquatic wild life species. In the Lagos lagoon, for instance, effluent discharge is typically done in the coastal areas where the early life stages of fishes often thrive [8]. Given the current view that fish species in this lagoon are dwindling [8], the challenge of mitigation of effluent discharge becomes daunting.

When fishes are exposed to sublethal concentration of toxicants, depending on the respective constituents and mechanism of action, a variety of physiological and biochemical responses may be elicited in order to maintain the innate homeostatic balance. Typical first line of responses in fishes may include biochemical responses such as changes in the activities antioxidative stress enzymes like SOD, catalase and GST as well as reduction of glutathione in the cells. Given the fact that effluents are an admixture of diverse chemical constituents, it is not unlikely that some of its components may contain reactive oxygen species (ROS) which are precursors of oxidative damage to cell. ROS such as peroxides, superoxides, and singlet oxygen combine with the polyunsaturated fatty acids and their esters in cell membranes, damaging and dislodging their components, resulting in lipid peroxidation. The resulting lipid hydroperoxide decomposes into several components such as lipid alkyl radicals, aldehydes, alkanes, epoxides, and alcohols [23]. The aldehyde, malondialdehyde (MDA), is a principal lipid peroxidation product employed in assessing oxidative damage to cell membranes [24]. There was evidence of peroxidative damage to the cells of the tilapia as indicated by higher levels of MDA in those exposed to both sublethal concentrations of the effluents. One of the microbial isolates indicated high phospholipase activity which could have accounted for the phospholipid peroxidation damage reported in this study. The dynamic nature of damage and repair in cells is exemplified in the variation of the MDA levels over the period of exposure.

Free superoxides upon entrance into cells are faced with the degrading action of superoxide dismutase which catalytically breaks them down into hydrogen peroxide and water [9]. The inhibition of the SOD activities in the fingerlings between the 14th and 28th days of exposure observed in this study is indicative of early signs of oxidative stress. Catalase works in conjunction with SOD in further breaking down the hydrogen peroxide by products of dismutase activity [9]. Although the catalase activities observed in the fingerlings do not show an overall trend, catalase inhibition in those exposed to higher concentrations (1/10th LC50) also points to some level of stress.

The increasing levels of reduced glutathione (GSH) observed across all fingerlings in the study are an indication of active uptake of free anions by the glutathione components of the cells in order to minimize oxidative damage potentials of the peroxides. Among the exposed groups, there was also evidence of inhibition of GST activities by the 28th day of the sublethal assays, relative to the control, where an increase was observed. Leaver and George [25] reported significant inhibition of GST activities in catfishes exposed to crude oils, benzene, toluene, and xylene. GST naturally catalyzes the conjugation of GSH with oxidative products resulting in the oxidative degradation of DNA [25]. Thus increased generation of products of oxidative damage and concomitant increase in conjugation needs would result in increased utilization of GST. This however was not the case because the inhibition was recorded and may be associated with the overwhelming effect of the oxidative stress, which is characterized by inhibition of the activities of enzymes involved in antioxidative stress mechanisms.

The general state of wastewater quality implies that there is need for proper treatment before discharge into the aquatic ecosystem because many of the parameters examined were higher than the FEPA standards for natural water bodies. Although dilution factors in natural water bodies would ease out their eventual concentrations, the high concentrations of manganese for instance are of concern given its link with loss of neuromotor function [26].

5. Conclusion

In this study, we have been able to relate the ability of microorganisms to survive and develop certain antibiotic resistance capabilities due to selective pressure in the drug polluted waste water [27]. The acute toxicity of the wastewater on sensitive fingerlings of O. niloticus raises salient effluent quality concerns. The biochemical responses in the fishes are indicative of the onset of oxidative stress which has the ability of impairing other life functions and the health of the fishes.

Antibiotic resistance acquisition due to selective pressure is of public health concerns as resistance genes can be disseminated in nature and transferred to pathogenic counterparts of bacterial species by genetic mobile elements [28]. Thus there is need to effectively treat drug waste water before discharge into the environment.

Overall, findings from the microbiological assays and consistent trend in most oxidative stress markers from the biochemical assays imply that a combination of both assays could be routinely used in pharmaceutical effluent quality monitoring before discharges into natural water bodies.

Conflict of Interests

The authors declare that there is no conflict of interests regarding the publication of this paper.