Derivation of Water Quality Criteria for Carbamazepine and Ecological Risk Assessment in the Nansi Lake Basin

Abstract

Carbamazepine, as one of several pharmaceutical and personal care products, has gained much attention in recent years because of its continuous discharge in natural waters and toxicity to aquatic ecosystems. However, it is difficult to evaluate and manage carbamazepine pollution because of the lack of a rational and scientific Water Quality Criteria (WQC) of carbamazepine. In this study, the carbamazepine toxicity data of thirty-five aquatic species from eight taxonomic groups were selected, and the species sensitivity distribution (SSD) method was applied to derive the WQC for carbamazepine based on the Log-logistic model, which was 18.4 ng/L. Meanwhile, the occurrence and distribution of carbamazepine in the Nansi Lake basin was studied. Results showed that concentrations of carbamazepine in 29 sampling sites were in the range of 3.3 to 128.2 ng/L, with the mean of 17.3 ng/L. In general, the levels of carbamazepine in tributaries were higher than those in the lakes. In addition, qualitative and quantitative ecological risk assessment methods were applied to assess the adverse effect of carbamazepine on aquatic systems. The hazard quotient (HQ) method showed that there were 24 and 5 sampling sites, in which risk levels were low and moderate, respectively. The joint probability curve (JPC) method indicated that ecological risks might exist in 1.4% and 1.0% of surface water, while a 5% threshold and 1% threshold were set up to protect aquatic species, respectively. Generally, carbamazepine posed a low risk to the aquatic organisms in the Nansi Lake basin.

1. Introduction

Pharmaceuticals and personal care products (PPCPs), as one of the most important groups of emerging contaminants, have become a global research hotspot due to their potential threats to the aquatic ecosystem and human health in recent years [1,2]. Currently, because of its daily or even excessive consumption for treating epilepsy and nerve pain, long half-life (900 h), and the low processing efficiency in the sewage treatment plant, carbamazepine is one of the most frequently detected PPCPs in the aquatic environment, and has been successfully proved to be a typical indicator that is able to trace the source of PPCPs in a large number of countries and regions [3,4,5]. Meanwhile, several researchers have introduced the fact that the overuse of carbamazepine can significantly affect aquatic animals both biochemically and physiologically [6,7,8]. Jarvis et al. [9] also reported that long-time exposure to carbamazepine could affect the abundance of Cyclopoida via the aquatic environment. Consequently, carbamazepine has been added to the priority list of the European Demonstration Program due to their frequency and toxicity [10]. However, carbamazepine, as an emerging pollutant, has not yet been included in the environmental quality standard system for surface water by America, China, and other countries. Therefore, it is very necessary and urgent to derive the Water Quality Criteria (WQC) of carbamazepine and to assess its ecological risk to aquatic system.

Water Quality Criteria (WQC) provides fundamental information of surface water for setting an environmental quality standard, ecological risk assessment, and environmental management [11]. Therefore, WQC research has been regarded as an important indicator, reflecting the progress of the environmental science research of one country. WQC-related studies have been carried out for several decades in developed countries and regions, such as the United States, the European Union, and Australia. In these areas, existing WQC guidance documents and related methodological systems are relative systematic and comprehensive [12,13,14,15,16,17]. However, WQC studies have just emerged in China, and the systematic research has only began in recent years. Based on the international derivation method of WQC, Chinese scholars have investigated and derived the WQC of target pollutants in Chinese surface water, such as ammonia-nitrogen [18], trivalent and pentavalent arsenic [19], nitrobenzene [20], plasticizer [21], and various heavy metals [22]. At the national level, the Ministry of Ecology and Environment issued a technical guideline for deriving the water quality criteria for the protection of freshwater aquatic organisms in 2017 by consulting the methodology of WQC derivation from developed countries [23] and revised the technical guideline in 2022 [24]. The undergoing WQC research in China is on the right track.

In this study, concentration and distribution of carbamazepine were analyzed in the Nansi Lake basin. By collecting and screening the toxicity data of carbamazepine, the WQC of carbamazepine was derived using the species sensitivity distribution (SSD) method. In addition, a tiered ecological risk assessment for carbamazepine was carried out by using qualitative and quantitative analysis. Taking carbamazepine as an example, the environmental investigation and evaluation system of merging pollutants was established preliminarily through field sampling, laboratory analysis, WQC derivation, and risk assessment.

2. Materials and Methods

2.1. Environmental Concentrations

2.1.1. Study Area

The Naisi Lake (34°27′–35°20′ N, 116°34′–117°21′ E) is the largest shallow freshwater lake in China, which is also a real-time storage reservoir on the East Route of the South-to-North Water Diversion Project. It consists of four small lakes, namely, the Weishan Lake, Zhaoyang Lake, Dushan, Lake and Nanyang Lake, from south to north. The total drainage area of the Nansi Lake basin is 30,453 km², and the water area is 1266 km², with an average depth of 1.46 m [25]. The Nansi Lake Basin has a warm, temperate continental monsoon climate, with an average annual precipitation of 690 mm. Moreover, it is also one of the most important agricultural regions in the Shandong province of China, with major cash crops such as corn, rice, wheat, soybean, and cotton [26].

2.1.2. Sample Collection and Extraction

A total of 29 surface water samples (NS01-SN29) were collected from the Nansi Lake basin in 2019 (Figure 1). The samples were taken from 0.5 m below the water surface, given a recovery indicator of carbamazepine-D8 (50 ng), and then filtered by a 70 mm GF/F glass fiber membrane within 24 h [27]. A solid-phase system (SPE) was used to extract carbamazepine with Oasis HLB cartridges which were pre-activated with 5 mL methanol and 5 mL ultra-pure water. The Oasis HLB cartridges absorbing carbamazepine were dried by vacuum (1.0 h) and eluted by 12 mL methanol. The eluent was concentrated 1.0 mL by high pure nitrogen and then spiked with caffeine-D3 as internal standard. Finally, the levels of carbamazepine in all samples were detected by using a high-performance liquid chromatography–triple quadrupole tandem mass spectrometry (HPLC-MS/MS, Waters, USA, Table S1) [28,29].

2.1.3. Quality Assurance and Quality Control

All chemical analyses were strictly conducted following the quality assurance and quality control procedures. In this study, six different carbamazepine standard solutions (1.0–1000 ng/L) were applied to construct a calibration curve with a good linearity (r² > 0.999). A solvent blank, a procedure blank, and an intermediate concentration of calibration curve were conducted for every bench of ten samples in order to check interference and cross-contamination. The method detection limit (MDL) of carbamazepine was 1.0 ng/L, and the recovery in all water samples ranged from 78% to 94%.

2.2. Derivation of Carbamazepine WQC

2.2.1. Toxicity Data Collection and Selection

The chronic toxicity data of carbamazepine were selected from the USEPA ECOTOX database (https://cfpub.epa.gov/ecotox/, accessed on 18 May 2022), Web of Science database, and China Knowledge Resource Integrated Database (https://www.cnki.net, accessed on 26 May 2022). No observed effect concentration (NOEC) was the first choice as endpoint; meanwhile, the lowest observed effect concentration (LOEC) and maximum acceptable toxicant concentration (MATC) were also applied when NOEC was not sufficient. The screening criterion for chronic toxicity data referred to previous literature [16].

2.2.2. Derivation WQC of Carbamazepine

WQC is derived by the SSD method, which is widely used throughout the world. Firstly, toxicity values (X axis) and their cumulative frequencies (Y axis) are employed to construct SSD curves. One sample Kolmogorov–Smirnov test is applied to test whether log-transformed field exposure concentrations and toxicity data conformed to normal distribution using SPSS 24.0. The HC₅ refers to 5% hazard concentration, at which 95% aquatic organisms could be protected, which can be acquired at the tail of the SSD curve. Then, WQC is calculated as HC₅ divided by an assessment factor of 2 [19].

2.3. Ecological Risk Assessment

Three-tiered methods were employed to evaluate the carbamazepine ecological risk in this study.

Tiered 1 was a qualitative risk assessment method called Hazard Quotient (HQ), which was the ratio of environmental exposure concentrations and WQC [30]. The assumption of this method is that a potential negative effect on the aquatic system may occur if the exposure level of a pollutant is greater than its WQC. There are four risk categories which are introduced below.

HQ > 10, the risk is high;

1.0 ≤ HQ < 10, the risk is moderate;

0.1 ≤ HQ < 1.0, the risk is low;

HQ < 0.1, the risk is negligible.

In tiered 2, a quantitative probabilistic risk method named margin of safety (MOS₁₀) was applied to describe the risk level [31]. MOS₁₀ was calculated using exposure and toxicity data distributions by the following equation:

MOS₁₀ = SSD₁₀/ECD₉₀(1)

where SSD₁₀ is the 10th percentile concentration for the toxicity data distribution, ECD₉₀ is the 90th percentile concentration for the environmental exposure distribution. Generally, an MOS₁₀ greater than one demonstrates that toxicity data distribution and exposure concentration distribution have a low interval overlap degree, and little environmental risk will be posed to aquatic species, whereas MOS₁₀ less than one will lead to a high risk to aquatic organisms.

In tiered 3, a joint probability curve (JPC) method developed based on tiered 2 was used. Exceedance probability function is achieved by transforming the exposure concentration distribution and combining it with the SSD to generate a JPC. JPC describes the relationship between the probability that aquatic species would be affected (X axis) and the exceeded frequency of exposure concentrations (Y axis). The closer JPC is to the X axis, the lower the probability of an adverse effect [32].

3. Results and Discussion

3.1. Spatial Distribution of Carbamazepine in Nansi Lake Basin

The concentrations of carbamazepine are illustrated in Figure 2. In all 29 surface water samples, the detection rate of carbamazepine was 100%, which indicated that carbamazepine was ubiquitous in the Nansi Lake basin. The concentrations of carbamazepine from different tributaries ranged from 3.3 to 128.2 ng/L, with an average of 23.3 ng/L; the levels of carbamazepine from lakes varied from 5.5 to 21.1 ng/L, with the mean concentration of 9.9 ng/L. Aqueous residues of carbamazepine were higher than Yellow River (3.57–4.82 ng/L) [33], Taihu Lake (5.16 ng/L) [34], and Dongting Lake (0.06 ng/L) [35]; were in the same level to Baiyangdian Lake (60.3 ng/L) [36]; were lower than that reported in Yangtze River (up to 1090 ng/L) [37] and Hai River (456 ng/L) [38]. Overall, the concentrations of carbamazepine in this study were at a medium level in China (for the detailed exposure data, please see Table S2).

From the perspective of distribution, carbamazepine showed the characteristics of non-homogeneity. In general, the concentration of carbamazepine in the rivers was higher than that in the lakes. The Web of Rxlist (https://www.rxlist.com, accessed on 21th June 2022) showed that 72% of carbamazepine ingested by living organisms was degraded, and the remaining 28% was directly excreted through feces. By field observation, sampling points such as NS01, NS03, NS13, and NS14 were densely populated. Subsequently, carbamazepine was used more frequently. Carbamazepine is a strongly water-soluble compound (112 mg/L) [39]. These may account for the higher concentrations of carbamazepine in several tributaries. Then, the concentration of carbamazepine was reduced after being diluted by water from the lake. Given that carbamazepine is an emerging pollutant, higher concentrations of carbamazepine in the environment will pose a potential risk to aquatic life.

3.2. Derivation of WQC for Carbamazepine

The data of the chronic toxicity of carbamazepine to aquatic organisms are listed in Table S3. The toxicity endpoints were NOEC and LOEC, with the effect indexes of population, growth, behavior, development, etc. Finally, the toxicity data of 35 species from eight taxonomic groups (e.g., amphibians, crustaceans, fishes, algae, higher plants, molluscs, insects, and invertebrates) were screened. The toxicity values of carbamazepine varied from 0.91 to 100,000 μg/L, with the mean concentration of 3201 μg/L, and the most and least sensitive specie was Gobiocypris rarus and Raphidocelis subcapitata, respectively [40,41]. In this study, the most used extrapolation model based on Log-logistic was used to construct the SSD curves of carbamazepine [42,43,44] (Figure 3). The HC₅ was calculated to be 36.8 ng/L. In consideration of the uncertainty of deriving WQC, HC₅ was divided by a factor of 2 as the final carbamazepine WQC, which was 18.4 ng/L.

3.3. Ecological Risk Assessment of Carbamazepine

3.3.1. Tiered 1 Assessment

The HQ method, in which the carbamazepine concentration at each sampling site is divided by the derived WQC, is used to describe the risk level qualitatively. Among the 29 samples, there were 5 with HQs between 1.0 and 10, which were NS01, NS03, NS13, NS14, and NS18, respectively; the other HQs were between 0.1 and 1.0 (Figure 4). The highest risk region was located in NS14, with an HQ of 7.0. In general, the ecological risks of carbamazepine in rivers were higher than those in lakes. The moderate ecological risk areas were mainly concentrated in the eastern and northern parts of the Nansi Lake basin. Considering that the HQ method cannot accurately quantify the degree and probability of ecological risk, tiered 2 and 3 (probabilistic method) are generated subsequently.

3.3.2. Tiered 2 Assessment

As mentioned above, M0S₁₀ is the ratio of the 10th concentration of toxicity effect distribution to the 90th concentration of environmental exposure distribution. In this research, M0S₁₀ was calculated to be 14.2 (Figure 5). The result showed that carbamazepine did not pose a threat to aquatic species in the Nansi Lake basin. On the other hand, although MOS₁₀ was greater than 1, there were still some regions with higher carbamazepine exposure concentration than WQC, indicating that potential ecological risk for aquatic organisms in some waters of the Nansi Lake basin existed.

3.3.3. Tiered 3 Assessment

The JPC method is a curve fitted by the concentration of the toxic effect and the concentration of environmental exposure. Compared with HQ and MOS₁₀, JPC is a more robust risk assessment method, and can further quantify the ecological environment risk. The Y axis represented the proportion of contaminated surface water bodies, and the X axis represented the proportion of aquatic species being affected (Figure 6). In this study, probabilities of exceeding NOEC or LOEC for 1–5% of the species ranged from 1.4% to 1.0% for carbamazepine in the Nansi Lake basin.

In this study, HQ, MOS₁₀, and JPC methods were used to evaluate the risk of carbamazepine to aquatic organisms in the Nansi Lake basin of China. The results all showed that the environmental risk of carbamazepine to the hydrophytic ecosystem was at a low level. The HQ method is a qualitative risk assessment method which is simple to operate and can easily identify the chemical substances that may cause risk to aquatic species. Considering that HQ is a relatively conservative method and the evaluation result is only a single-value estimation which cannot be explained in terms of probability, it is often used as the primary risk assessment. Probabilistic risk assessment methods including MOS₁₀ and JPC are developed on the basis of qualitative risk assessment methods, which make full use of all pollutant toxicity data and environmental monitoring data and take into account the effects of other factors on aquatic biosafety, such as the concentration distribution of pollutants, the total amount of pollutants, the type of aquatic organisms, as well as species’ susceptibility to contaminants. For the convenience of environmental management, experts and scholars have suggested the use of qualitative and quantitative risk-assessment methods to assess the ecological risk of pollutants [44].

3.4. Uncertainty Analysis

Uncertainty was inevitable in the process of performing ecological risk assessment, which mainly originated from the following factors: carbamazepine environmental exposure, toxicity effect, and the risk characterization method. The uncertainty of environmental exposure included deviation during sample collection and analysis and a lack of information on spatial and temporal variation in carbamazepine field concentrations. Then, the difference between SSD fitting models and limited chronic toxicity data were also vital yet uncertain sources of carbamazepine’s toxicity effect. Furthermore, the NOEC or LOEC used in this study was obtained based on a controlled laboratory experiment, which was somewhat different from that acquired by field experiment. Finally, there were various ecological risk assessment methods, and different researchers had different understandings and applications, which would lead to different risk results in the same situation. Considering these, a tiered method was used to reduce the uncertainty of risk assessment to a large extent.

4. Conclusions

Twenty-nine samples from the largest shallow freshwater lake in China were analyzed to identify carbamazepine’s residual and ecological risk to aquatic species. The concentrations of carbamazepine from samples ranged from 3.3 to 128.2 ng/L. The major cause of carbamazepine in the environment might be due to anthropogenic activities. Meanwhile, toxicity data of thirty-five aquatic species were screened to construct SSD curves to determine the WQC of carbamazepine, which was 18.4 ng/L. Moreover, a tiered approach was used to assess carbamazepine’s ecological risk. The HQ method showed that the highest risk region was located in NS14, with an HQ of 7.0. In general, the ecological risks of carbamazepine in rivers were higher than those in lakes. M0S₁₀ showed that carbamazepine did not pose a threat to aquatic species in the target area. The JPC method indicated that ecological risks might exist in 1.4% of surface water, while a 5% threshold was set up to protect aquatic species. In this work, both qualitative and quantitative methods indicated that carbamazepine posed a low ecological risk to aquatic systems in the Nansi Lake basin. This study could provide some useful information for decisionmakers to control carbamazepine pollution.

Author Contributions

J.W.: Writing—Original draft preparation, Investigation. D.S.: Software, Investigation. S.W.: Formal analysis, Investigation, Resources. X.Y.: Formal analysis, Investigation, Resources. H.Z.: Visualization. T.Z.: Writing—Review and editing. L.Z.: Conceptualization, Methodology, Software, Formal analysis, Data curation. Y.Z.: Writing—Review and editing, Funding acquisition. All authors have read and agreed to the published version of the manuscript.

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

The data of this study are available from the corresponding author upon reasonable request.

Conflicts of Interest

The authors declare no conflict of interest.

Publisher’s Note: MDPI stays neutral with regard to jurisdictional claims in published maps and institutional affiliations.

Figures

Figure 1. Sampling sites in the Nansi Lake basin.

Figure 2. Spatial distribution of carbamazepine in the surface water of Nansi Lake basin.

Figure 3. Species sensitivity distributions (SSD) for carbamazepine.

Figure 4. The HQs’ distribution of carbamazepine in Nansi Lake basin.

Figure 5. Distribution of exposure concentration and toxicity data of carbamazepine.

Figure 6. Joint probability curve for ecological risk of carbamazepine in the Nansi Lake basin.

Supplementary Materials

The following supporting information can be downloaded at: https://www.mdpi.com/article/10.3390/ijerph191710875/s1, Table S1: Instrument parameter for HPLC-MS/MS; Table S2: Carbamazepine occurrence in surface water of China; Table S3: Chronic toxicity of carbamazepine to freshwater animals. References [45,46,47,48,49,50,51,52,53,54,55,56,57,58,59,60,61,62,63,64,65,66,67,68,69,70,71,72] are cited in the supplementary materials.

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