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How much do the conventional parameters contribute to the biological toxicity of surface water in different types of villages?



In rural areas, the surface water quality is seriously threatened by pollution from agriculture, breeding, industrial and tourism activities. Even though many strategies and programs were launched for rural environment management, it is challenging to tackle the serious surface water pollution in villages. Since pollution status varies with the type of villages, there is no single parameter that defines environment quality completely. Until recently, most of rural surface water quality monitoring programs focus only on the conventional parameters, while can these conventional parameters reflect comprehensive status of water quality? To study how much the conventional parameters contribute to biological toxicity of surface water in villages, the in situ parameters of pH, DO, EC, ORP, laboratorial parameters of COD, TN, NO3-N, NO2-N, NH4+-N, TP, and PO43−-P and acute toxicity were analyzed for the surface water samples those were collected from six types of villages, named breeding, agricultural, handicraft, industrial, agricultural and breeding, and tourism. The correlation analysis was applied to establish the linkages and contributions of each parameter.


The results showed that all detected surface waters were alkaline, and the concentration of TN and most of COD concentrations in all six types of villages were higher than the Class V limits specified in environmental quality standards for surface water (GB3838-2002). Pearson’s correlation analysis showed that significantly positive correlations were found for the acute toxicity effects and laboratorial parameters of NO2-N, NH4+-N and PO43−-P in agricultural villages, and negative correlations were found for the acute toxicity effects and laboratorial parameters of TN and NO3-N. No significant correlation was observed in breeding villages and industrial villages.


The problems of nitrogen pollution and aerobic pollution are still serious in villages, and more attention should be paid in further rural environment management. NH4+-N could contribute to the acute toxicity of surface water in the most of investigated villages, while no significant correlation was observed between acute toxicity and conventional parameters in industrial villages and tourism villages. Environmental monitoring programs focusing just on the classical conventional parameters are far from sufficient, since the main toxic contributors are quite different in diverse villages. The outcomes of the present study contribute to demonstrate the performance and usefulness of bioanalytical techniques for water quality assessment.


With the increase in requirement of food and natural resources from rural regions to sustain burgeoning number of urban residents, rural environments are seriously polluted by contaminants from agriculture, breeding, industrial, tourism and so on. It is reported that in China, the total emission of chemical oxygen demand (COD), nitrogen and phosphorus from agriculture account for 43.7%, 57.2% and 67.3% of the total national emissions, respectively [1]. In 2010, the COD and ammonia nitrogen discharged by the livestock and poultry breeding accounted for 45% and 25% of the nationwide emissions in China [2]. Thus, rural environment management, as one of the most important components of rural development, has aroused wide concern in recent years [3].

United States Department of Agriculture [4] office released a series of programs, such as Rural Decentralized Water Systems Grant Program, Solid Waste Management Grants, Water & Waste Disposal Grants to Alleviate Health Risks on Tribal Lands and Colonias, SEARCH—Special Evaluation Assistance for Rural Communities and Households, Water & Waste Disposal Technical Assistance & Training Grants and so on to protect water and environment in rural areas [4]. In China, the project of “green livable village program” was launched in 2018 by the Ministry of Science and Technology of the People’s Republic of China (MOST) to improve the rural living environment and to promote the coordination of agricultural production, living condition and ecological conservation [3]. However, studies on the harmful effects of objective water quality and measures aimed at controlling environmental pollution have been taken mainly in cities, since the rural residents' weak awareness of environmental protection and less judgement on the harm of environmental pollution [1]. The monitoring of water quality is always time-consuming, and a cumbersome task requiring manual laboratory analysis and statistical inferences, since there is no single parameter that defines environment quality completely [5]. The laboratory facilities and test are normally quite limited in rural areas. In addition, most of the water supply and drainage are decentralized and differed distinctly with type of villages. For instance, in farming villages, pesticides and fertilizers are main pollutants; in breeding villages, livestock is the major pollution source; in industrial villages, the dominant pollutants are often related to the corresponding industrial production; and in mixed villages which involve agriculture, breeding, industry, the environmental pollutants are usually mixture of different kinds of chemicals. These different types of villages and pollutants increased the difficulty of water quality monitoring in rural areas. Thus, most of rural surface water quality monitoring programs just focus on the comprehensive conventional parameters, such as pH, dissolved oxygen [6], electrical conductivity (EC) and oxidation reduction potential (ORP) which are easily and quickly tested in situ, and chemical oxygen demand (COD), total nitrogen (TN), and total phosphorus (TP) which require less laboratory facilities during parameter detection. While can these conventional parameters reflect comprehensive status of water quality and direct water quality management in rural areas?

The ultimate objective of water quality monitoring, evaluation, management is to ensure the safety of water environment. Bioanalytical techniques of effect-based bioassays which account for the toxic effects of complex environmental mixtures could evaluate the safety of tested samples directly [7]. To study how much the conventional parameters contribute to biological toxicity of surface water in villages, surface water samples were collected from six types of Chinese villages, named breeding, agricultural, handicraft, industrial, agricultural and breeding, and tourism. In situ parameters of pH, DO, EC, ORP and laboratorial parameters of COD, TN, NO3-N, NO2-N, NH4+-N, TP, and PO43−-P were detected for the collected samples. The luminescent bacteria 502 which were reported to be an ideal model for acute toxicity evaluation, and closely resemble the enzyme activity levels of the current population [6] were applied to indicate the safety of water samples in the current study. Finally, correlations between acute toxicity and water conventional parameters were analyzed to establish the linkages and contributions of each parameter during water quality monitoring.


Study area

In the current study, 13 study villages located in four provinces (Liaoning, Qinghai, Sichuan and Shanghai) with representative different geographic characteristics in China. The frequent underground/surface water interaction (U/S interaction), alternation of drying and wetting (D/W alternation), and freezing–thawing transition (F/T transition) are typical rural natural environmental processes in river network regions, mountainous regions and cold regions of China, respectively. These biogeochemical processes play important roles for pollutants transportation, transformation, and source-to-sink patterns of pollutants, which may result in variations of hazards in rural environments [3]. In each province, 3–4 villages of different types were selected for surface water sample collection (Fig. 1 and Additional file 1: Table S1). Each village is of medium size locally, no wastewater management systems have been built with the exception for the villages in Shanghai. The backbone industry of study villages includes agricultural, industrial, breeding, handicraft and tourism.

Fig. 1

Location of the study area

In situ parameter determination

The parameters of pH, dissolved oxygen (DO), oxidation–reduction potential (ORP) and electrical conductivity (EC) were measured in the field by a multiparameter water quality monitoring instrument (YSI Professional Plus, USA) [8].

Sample collection and storage

Sample collection in this study was conducted between July and September 2020. At least three sampling sites were set up in each village. A total of 1000 mL water sample was collected from each sampling site, among which 500 mL sample was collected and stored in a plastic bottle at -20 °C for conventional parameters detection, and the other 500 mL sample were filtrated via 0.45 μm PES syringe filter (Jinteng, Tianjin, China) and stored in a glass bottle at -20 °C for toxicity evaluation.

Laboratorial parameters analysis

The total nitrogen (TN) was detected by ultraviolet spectrophotometry with basic potassium persulfate [9]. Firstly, 10 mL sample was added with 5 mL basic potassium persulfate, and was then digested at 121 °C for 30 min. After cooling, 1 mL hydrochloric acid (HCl:deionized water; v:v = 1:9) was added into the solution, following by filling up the solution to 25 mL by deionized water. The analysis was done by measuring the absorbance of the treated sample at 220 nm and 275 nm, and the values was obtained by calculation (A = A220 − 2A275).

The nitrate (NO3-N) was measured via sulfamic acid spectrophotometric method [10]. Firstly, 5 mL water sample was added to a volumetric flask and fixed up to 50 mL with deionized water, followed by added with 1 mL hydrochloric acid (1 mol/L). After sufficiently shaking, 0.1 mL sulfamic acid was added into the flask. The absorbances at 220 nm and 275 nm were measured by spectrophotometer with the sample in a quartz cuvette, and the two absorbance values were subtracted to obtain A (A = A220 − 2A275).

N-(1-naphthyl)-2 Ethylenediamine photometric method was used to determine the concentration of nitrite (NO2-N) in water samples [10]. Briefly, 1 mL of water sample was placed in a 50 mL colorimetric tube and diluted with deionized water up to 50 mL. Afterwards, 1.0 mL of chromogenic agent containing 0.17 g/mL phosphoric acid, 40 g/mL p-aminobenzenesulfonamide and 2 g/mL N-(1-naphthyl)-ethylenediamine dihydrochloride was added to the solution. The solution was sufficiently mixed and left to stand for 20 min. Using deionized water as reference, the absorbance at 540 nm was measured with a cuvette of 10 nm optical path.

The concentration of ammonium (NH4+-N) was obtained by salicylic acid–hypochlorite spectrophotometric method [6, 11]. Briefly, 5 mL water sample was transferred into a 10 mL colorimetric tube, diluted to 8 mL with deionized water. And then, 1.00 mL chromogenic agent (50 g/L salicylic acid, 50 g/L potassium sodium tartrate and 1.28 g/L sodium hydroxide) and 2 drops of sodium nitrosoferricyanide solution (0.1 g/mL) were added into the tube. After sufficiently mixed, 2 drops of sodium hypochlorite solution were added into the solution, and finally the solution was diluted up to 10 mL. After standing for 1 h, the absorbance was measured at 697 nm using a cuvette of 10 nm optical path [11].

The total phosphorus (TP) was analyzed by ammonium molybdate spectrophotometric method with potassium persulfate as the digestion oxidant [8]. Briefly, 25 mL water sample was added into a 50-mL colorimetric tube, and then 4 mL of potassium persulfate was added. After digestion at 121 °C for 30 min, 1 mL of 10% ascorbic acid was added and mixed intensively, followed by adding 2 mL of molybdate solution. After sufficiently mixing and then standing for 15 min, the sample was placed in a 10-mm cuvette and the absorbance was measured at 700 nm.

To determine the concentration of phosphate (PO43−-P), 10 mL of the sample was placed in a 50-mL colorimetric tube, in which 2 mL of ammonium molybdate solution and 3.0 mL of ascorbic acid solution were added as chromogenic agent, and the solution was diluted up to 50 mL with deionized water. After sufficiently mixing and standing for 10 min at room temperature, the absorbance of sample was measured at 710 nm using a cuvette with an optical range of 1 cm and zeroed with a blank without the tested solution [8].

The chemical oxygen demand (COD) was determined by a colorimetric dosing method using a spectrophotometer. Firstly, 1 mL mercury sulfate was added into the dry cuvette to shield the Cl. Then 2.25 mL of solution A (concentrated sulfuric acid containing silver sulfate, where the concentration of sulfuric acid is 98%, and the ratio of silver sulfate to concentrated sulfuric acid is 10 g:1L), 0.75 mL of solution B (potassium dichromate solution with a concentration of 0.167 mol/L) and 2 mL of water sample were added to the cuvette in turn, and the bottle was tightly capped and shaken sufficiently. The COD concentration was determined after digestion at 150 °C for 2 h, and then cooled to room temperature. The total organic carbon (TOC) concentration was measured using a TOC analyzer (Shimadzu TOC-L, Japan) [12]. Each sample was subjected to at least three parallel independent experiments. Except for TOC, the value of each physicochemical parameter was determined by finding the concentration value corresponding to the absorbance on a standard curve, which was plotted using a standard solution with a known concentration gradient. The ranges of detection are 0.05–4 mg/L, 0.08–4 mg/L, 0.003–0.2 mg/L, 0.01–1 mg/L, 0.01–0.6 mg/L and 0.05–1000 mg/L for TN, NO3-N, NO2-N, NH4+-N, TP and COD, respectively.

Toxicity evaluation

For the toxicity evaluation, luminescent bacteria 502 was utilized. The lyophilized powder of luminescent bacteria was taken out from the − 80 °C and placed at 20 °C for 10 min. Then, the recovery medium was added for rehydration at 20 °C for 15 min. The luminescent bacteria acute toxicity assay protocol was based on the method described by Chen et al.[6]. Toxicity of surface water samples were evaluated by measuring the inhibition of bioluminescence of luminescent bacterial strains. The luminescence inhibition assay was performed in test tubes using a luminometer (BHP9514, Beijing Hamamatsu Photon Techniques INC.). For each test, 10 test tubes were prepared, eight for different water samples, one for negative control (recovery liquid) and one for positive control (ZnSO4·7H2O at 5 mg/L). Sample or control liquid (1 mL) was added after pretreated with osmotic pressure regulator, and the bacterial suspension (50 μL) was added with 10 s intervals. After 15 min exposure of the bacteria to the sample at 20 °C, the relative light unit (LU) of luminescent bacterium 502 was measured. The acute toxicity of the sample on strain 502 was expressed as an inhibition ratio, calculated by the following formulation [6]:

$${\text{X}}\% {\text{ }} = {\text{ }}\left( {{\text{1 }}{-}{\text{ LU}}/{\text{LU}}_{0} } \right){\text{ }} \times {\text{ 1}}00,$$

where LU0 was the RLU of strain 502 exposed to the negative control and LU was the RLU of the samples. Each test was carried out with three independent replicates.

Statistical analysis

Spatial visualization of all data was analyzed based on ArcGIS 10.4.1 (ESRI, USA). All the experimental data were analyzed by Microsoft Excel™ 2016 and Origin 2019 (Origin Lab Corporation). One-way analysis of variance (ANOVA) was applied for statistically significant differences testing. The correlation analysis was run based on the R programming language (R Development Core Team 2018). Pearson’s correlation analysis was applied to reveal the correlation between the acute toxicity of luminescent bacteria 502 and each conventional parameter [6]. Two significance levels of p < 0.05 and p < 0.01 were used to define statistical significance.

Results and discussion

In situ parameters of aquatic environment

The results of in situ detected parameters are shown in Fig. 2. The concentrations of DO in rural surface water ranged from 1.40 mg/L to 15.50 mg/L, with the mean value of 8.58 mg/L (Fig. 2A). The highest DO concentration was obtained in an agriculture village in Sichuan, and the lowest one was found in a tourist village (SH-03) in Shanghai. The diverse DO concentrations could be related to the different hydrological features as well as varied aquatic vegetation patterns in villages [13]. Besides, the ORP values in Shanghai were slightly less than that in other study sites (Fig. 2B), which may indicate that reductive substances are in the majority in Shanghai surface water [14]. We found that the EC value in rural surface water amounted from 0.118 mS/cm to 1.47 mS/cm (Fig. 2C). The highest EC appeared in the industrial village in Xining (Qinghai) where is surrounded with metallurgical industry and mineral industry. All the observed pH values were between 7 and 9, which means that surface water in China rural areas is weak alkaline (Fig. 2D). The pH of the water sample has little effect on acute toxicity [15].

Fig. 2

In situ parameters of A dissolved oxygen (DO) concentration, B oxidation–reduction potential (ORP) value, C electrical conductivity (EC) value and D pH value in different types of village surface water. Ag.: agricultural village; A.&B.: agriculture and breeding mixed village; Br.: breeding village; Ha.: handicraft village; In.: industrial village; To.: tourism village

Laboratorial parameters of aquatic environment

As can be seen from Fig. 3, the TN, NO3-N, NO2-N and NH4+-N concentrations of all 13 sites ranged from 2.37 mg/L to 11.31 mg/L, 0.93 mg/L to 6.96 mg/L, 0.20 mg/L to 0.04 mg/L, and 0.07 mg/L to 1.11 mg/L, respectively. It is noticed that the concentrations of TN in all studied areas were beyond the limits (2.0 mg/L) for Class V water that specified by GB3838-2002 (environmental quality standard for surface water, Additional file 1: Table S2) [16], indicating that all of these studied surface water cannot be used for agriculture, industry, landscape and entertainment [16]. The concentration of TN, NO3-N and NO2-N in the site HQ-04 which located in an industrial village in Ganhetan, north of Lushaer, Huanzhong County, Qinghai Province, was significantly higher than that in other sites. The industrial village takes smelting, building materials and in particular chemical industry as the main industries, which could be a reason for nitrogen pollution in this area. The lowest mean value of TN and NO3-N concentration was found in the tourist village (SH-03), which indicates that the tourism may contribute less to nitrogen pollution in rural areas when compared to agriculture, breeding, handicraft and industry. Besides, the highest NH4+-N concentration was found in the site SH-02 which located in an agricultural village in Shanghai. The possible reason could be that the main agricultures in Caijianong village is vegetable cultivation, such as cabbage, papaya and lotus root. The rapid growth of these vegetables requires a lot of nitrogen fertilizers, and more than 95% of synthetic nitrogen fertilizers are urea and ammonium nitrogen [17]. Concerning the proportions of NH4+-N in TN, agricultural villages are significantly higher than industrial villages, which give an further evidence for that ammoniated fertilizer is one of most important sources of nitrogen pollution in agricultural villages [18].

Fig. 3

The concentration of A total phosphorus (TP), B NO3-N, C NO2-N and D NH4+-N in different types of village surface water. Ag.: agricultural village; A.&B.: agriculture and breeding mixed village; Br.: breeding village; Ha.: handicraft village; In.: industrial village; To.: tourism village

Figure 4 shows the detected concentrations of TP, PO43−-P, COD and TOC in 13 sampling sites. The lowest TP and PO43−-P were observed in an industrial village (SC-02) with the concentration of 0.071 mg/L and 0.049 mg/L, respectively (Fig. 4A, B). The industry of this village is mainly for construction materials and auto parts. These results indicate that the industry of construction materials and auto parts could be less contributing to phosphorus pollution [19]. Interestingly, the lowest TOC concentration was detected in a breeding village (SC-01) with swine as the main farmed specie. The concentrations of COD ranged from 26.58 mg/L to 119 mg/L in 13 sampling sites (Fig. 4C). Most of these COD concentrations exceeded the Class V limits (40.0 mg/L) that specified by GB3838-2002, and thus the waters cannot be used for agriculture, industry, landscape and entertainment [16]. Significantly, the highest concentrations of TP, PO43−-P, COD and TOC were found in the site QH-04 (Fig. 4D) which exhibited the highest concentrations of TN, NO3-N and NO2-N. These results demonstrated that smelting, building materials and chemical industry could be a vital source of carbon, nitrogen and phosphorus pollution [20], which should be of concern during environment management and development in rural areas.

Fig. 4

The concentration of A total nitrogen (TP), B PO43−-P, C chemical oxygen demand (COD) and D total organic carbon (TOC) in different types of village surface water. Ag.: agricultural village; A.&B.: agriculture and breeding mixed village; Br.: breeding village; Ha.: handicraft village; In.: industrial village; To.: tourism village

Toxicity of aquatic environment

To evaluate the toxicity of surface water samples from different types of villages, the luminescent bacteria acute toxicity test was applied in the current study. Six out of 48 samples induced significantly toxicity on luminescent bacteria 502, as shown in Fig. 5. The highest inhibition rate of luminescence intensity was observed in the SH-02 of Caijianong which is located at an agricultural village in Shanghai. This result indicates that pollution from agriculture could be one of important environmental risk sources, of which the relative high concentrations have been found in the surface water in these areas [21]. A large number of pesticides such as insecticides, herbicides and fungicides are used in the process of cultivating crops. Organochlorine pesticides (OCPs) are one of the most widely used pesticides [22]. They interfere with the membrane transport system of sodium, potassium, calcium or chloride ions, thereby inhibiting the selective enzymatic activity of chemical transmission at nerve endings [23]. Herbicides can affect photosynthesis, respiration, growth, cell and nuclear division, or protein or lipid synthesis processes [24]. Fungicides interfere with fungal energy supply processes and inhibit spore germination [25, 26]. Except for agricultural pollution, pollutants from tourism should not be ignored, since significant luminescence inhibition was observed in all tourism water samples. With the rapid development of tourism industry, more and more urban residents would like to travel to rural villages. Accordingly, lots of domestic wastewater and household waste were released irregularly, since very limited drainage system and refuse collector are available in rural villages. These may lead to serious problems for rural environments. For instance, the West Lake in Hangzhou, as one of the most famous tourist city in China, carried a large number of visitors and an increasing loads of garbage and domestic sewage. According to the Tourism Bureau, the comprehensive pollution index of West Lake from 2007 to 2018 is on an upward trend, and the ecological environment has been significantly affected [27]. In addition, a survey of Santa Marta Beach in the Colombian Caribbean found a significant increase in the amount of litter and microplastics during the peak tourist season [28].Tourism in Cyprus (North) also increases the amount of local pollutant emissions, which leads to environmental degradation [29].

Fig. 5

Luminescent bacterial acute toxicity of surface water in different types of villages. Ag.: agricultural village; A.&B.: agriculture and breeding mixed village; Br.: breeding village; Ha.: handicraft village; In.: industrial village; To.: tourism village

Correlation analysis

The correlation between acute toxicity and each conventional parameter was analyzed by Pearson correlation test for the 48 surface water samples from different kinds of villages. Significant linkages between acute toxicity effects and conventional parameters were obtained (Fig. 6).

Fig. 6

Bar graph of correlations between acute toxicity and conventional parameters in A agricultural village surface water, B breeding village surface water, C industrial surface water, D tourism village surface water and E agriculture and breeding mixed village surface water. *p < 0.05; **p < 0.01. The gray dashed lines were set at correlation coefficient values of 1 and − 1, which means maximum positive and negative correlations, respectively

In agricultural villages, the acute toxicity effects of surface water were significantly positive correlated with laboratory parameters including NO2-N (r = 0.72, p < 0.05), NH4+-N (r = 0.90, p < 0.05) and PO43−-P (r = 0.68, p < 0.05) (Fig. 6A). These results suggest that the acute toxicity of surface water from agricultural villages may be induced by inorganic nitrogen and phosphorus pollutants [30]. In particular, the correlation coefficient for NH4+-N and acute toxicity was 0.90. This result provided a further evidence that ammoniated fertilizer is a hazardous material, which has to be taken seriously. In breeding villages, except for NH4+-N, the current observed conventional parameters were negatively correlated with the toxicity of surface water (Fig. 6B). These observations indicate that the acute toxicity of surface water in the breeding villages may not be caused by the conventional parameters. It is reported that besides carbon, nitrogen and phosphorus, heavy metals and antibiotics which can induce toxic effects on aquatic organisms/microorganisms were also frequently detected in breeding villages [9]. For instance, quinolones, one of widely used antibiotics in livestock breeding, can inhibit protein synthesis and interfere with DNA replication; erythromycin can restrain photosynthesis-related processes, such as electron transport, photosynthetic phosphorylation and carbon assimilation [31]; tetracyclines may be related to the inhibition of chloroplast metabolism-related pathways, which ultimately affect cell growth by interfering with the function of photosynthetic organs [32]. Cu causes a decrease in Na+ concentration in fish gill tissue, and affects the expression of oxidative stress-related genes such as catalase, glutathione reductase and glutathione S-transferase [33]. Zinc can affect the development, sexual maturation and reproduction of aquatic organisms by disrupting thyroid hormones [34]. Similar results were also found in industrial villages (Fig. 6C), which suggested that in breeding and industrial villages, the toxicity of surface water may not cause by the carbon, nitrogen and phosphorus pollution. The main toxic contributors are quite difference in diverse industrial fields. In electronic industry, the main toxic contributors could be heavy metals [35]. While in the village with dyeing industry as a pillar industry, the organic dyes may contribute to the toxicity of surface water [36]. In tourism villages, except for TN, NO2- N, TP and EC, other conventional parameters are negative correlated with the acute toxic effects, while no significant correlation was observed. In mixed villages which agriculture and breeding are mainstay industry, the acute toxicity was significantly correlated with the TP and PO43−-P with the coefficient of 0.96 and 0.99, respectively. The possible reason could be that both agricultural production and livestock breeding can produce lots of phosphorus pollutants [37]. It is noticed that positive correlation was obtained for NH4+- N and acute toxicity in agriculture villages, breeding villages and industrial villages, which further proved that NH4+- N is a serious problem in rural areas.


The surface water involved in the hydrological cycle is the basis for many human uses. In rural areas, pollutants induced great variation in surface water quality may lead to serious problems for aquatic ecosystem and even human health. Our study found that NH4+-N could contribute to the acute toxicity in most of villages, and the harmful influence of ammoniated fertilizer should be taken seriously. In agricultural villages, classical water quality parameters of NO2-N, NH4+-N and PO43−-P could contribute to the toxicity of surface water, while no significant correlation was observed between acute toxicity and conventional parameters in industrial villages and tourism villages. These results indicate that environmental monitoring programs focus just on the classical conventional parameters is far from enough, since the main toxic contributors are quite different in diverse villages. More toxic parameters could be added and seasonal variations should be taken into consideration in further monitoring programs during environmental management to assess the safety of water quality directly. The outcomes of the present study contribute to demonstrate the performance and usefulness of bioanalytical techniques for water quality assessment. These efforts provide the scientific underpinnings and regulatory reference for derivation of environmental quality standards. These works, combined with long-term monitoring data, could provide scientific underpinnings and regulatory reference for derivation of environmental quality standards, and thus contribute to environmental management in rural areas around the world.

Availability of data and materials

The datasets used and/or analyzed during the current study are available from the corresponding author on reasonable request.



Chemical oxygen demand


United States Department of Agriculture


Ministry of Science and Technology of the People’s Republic of China


Dissolved oxygen


Electrical conductivity


Oxidation reduction potential


Total nitrogen


Total phosphorus

NO3 -N:


NO2 -N:


PO4 3 -P:



Total organic carbon


Light unit


Relative light unit


  1. 1.

    Zhang W-L, Wu Y (2018) An analysis of the significance of protecting the village and town environment and its benefit in the new period. Acad Res 44:250–251

    Google Scholar 

  2. 2.

    Wang H, Xu J, Liu X, Sheng L, Zhang D, Li L, Wang A (2018) Study on the pollution status and control measures for the livestock and poultry breeding industry in northeastern China. Environ Sci Pollut Res 25(5):4435–4445.

    Article  Google Scholar 

  3. 3.

    Chen Z, Shao Y, He M, Liang J, Jiang Y, Wang Y, Zhou M, Gong Z, Zhou X, Guo J, Fang F (2020) The EMR-rural project: key techniques and devices’ development for rural environmental monitoring and remediation in China. Environ Sci Eur 32:11.

    Article  Google Scholar 

  4. 4.

    USDA (2021) Rural Utilities Service - Water & Environmental Programs.

  5. 5.

    Ahmed U, Mumtaz R, Anwar H, Mumtaz S (2020) Qamar AM (2020) Water quality monitoring: from conventional to emerging technologies (vol 20, pg 28. Water Sup 20(4):1580–1580.

    Article  Google Scholar 

  6. 6.

    Chen Z, Zhu Z, Song J, Liao R, Wang Y, Luo X, Nie D, Lei Y, Shao Y, Yang W (2019) Linking biological toxicity and the spectral characteristics of contamination in seriously polluted urban rivers. Environ Sci Eur 31:174.

    CAS  Article  Google Scholar 

  7. 7.

    Shao Y, Xiao H, Di Paolo C, Deutschmann B, Brack W, Hollert H, Seiler TB (2019) Integrated zebrafish-based tests as an investigation strategy for water quality assessment. Water Res 150:252–260.

    CAS  Article  Google Scholar 

  8. 8.

    Bouaissa M, Ghalit M, Taupin JD, Khattabi JE, Gharibi E (2020) Assessment of groundwater quality in the Bokoya Massif (Central Rif, Northern Morocco) using several analytical techniques. Euro-Mediterr J Environ Integr 6(1):9.

    Article  Google Scholar 

  9. 9.

    Su H, Xu W, Hu X, Xu Y, Wen G, Cao Y (2021) Spatiotemporal variations and source tracking of antibiotics in an ecological aquaculture farm in Southern China. Sci Total Environ 763:143022.

    CAS  Article  Google Scholar 

  10. 10.

    Wu C, Huang X, Witter JD, Spongberg AL, Wang K, Wang D, Liu J (2014) Occurrence of pharmaceuticals and personal care products and associated environmental risks in the central and lower Yangtze river, China. Ecotoxicol Environ Saf 106:19–26.

    CAS  Article  Google Scholar 

  11. 11.

    Ministry of Ecology and Environment, PRC (2012) National Environmental Protection standards of the People’s Republic of China (2012) in Water quality-Determination of total nitrogen-Alkaline potassium persulfate digestion UV spectrophotometric method. Ministry of Ecology and Environment, the People’s Republic of China

  12. 12.

    Chen X, Wang Y, Sun T, Chen Y, Zhang M, Ye C (2021) Evaluation and prediction of water quality in the dammed estuaries and rivers of Taihu Lake. Environ Sci Pollut Res.

    Article  Google Scholar 

  13. 13.

    Li X-F, Ai J-Y, Lin C-H, Guan H-B (2018) Prediction model of dissolved oxygen in ponds based on ELM neural network. IOP Conf Ser: Earth Environ Sci 121:022003.

    Article  Google Scholar 

  14. 14.

    Jin Z, Ding S, Sun Q, Gao S, Fu Z, Gong M, Lin J, Wang D, Wang Y (2019) High resolution spatiotemporal sampling as a tool for comprehensive assessment of zinc mobility and pollution in sediments of a eutrophic lake. J Hazard Mater 364:182–191.

    CAS  Article  Google Scholar 

  15. 15.

    Andriano KP, Taylor MS, Felix BA, Hamber EA, Daniels AU, Heller J (1995) Technical note: bioluminescent bacterial test for acute toxicity: the effect of pH and buffer solutions. J Appl Biomater 6(2):145–146.

    CAS  Article  Google Scholar 

  16. 16.

    Ministry of Ecology and Environment, PRC (2002) Environmental quality standers for surface water. Ministry of Ecology and Environment, the People’s Republic of China

  17. 17.

    Huang G-Q, Wu L, Li Y-X, Zhang W-F, Zhang F-S (2013) Development situation and suggestions on nitrogen fertilizer industry in China. Mod Chem Ind 33(10):5–9

    Google Scholar 

  18. 18.

    Liu B, Wang X, Ma L, Chadwick D, Chen X (2021) Combined applications of organic and synthetic nitrogen fertilizers for improving crop yield and reducing reactive nitrogen losses from China’s vegetable systems: a meta-analysis. Environ Pollut 269:116143.

    CAS  Article  Google Scholar 

  19. 19.

    Zhao Z-L, Li W-W, Wang F, Zhang Y-Q (2018) Using of hydrated lime water as a novel degumming agent of silk and sericin recycling from wastewater. J Clean Prod 172:2090–2096.

    CAS  Article  Google Scholar 

  20. 20.

    Liu W, Yao H, Xu W, Liu G, Wang X, Tu Y, Shi P, Yu N, Li A, Wei S (2020) Suspect screening and risk assessment of pollutants in the wastewater from a chemical industry park in China. Environ Pollut 263:114493.

    CAS  Article  Google Scholar 

  21. 21.

    Chen C, Li TT, Zou WB, Chen SS, Zhang K, Ma LM (2020) Spatial distribution and sources of organochlorine pesticides in surface waters of Shanghai. China SN Appl Sci 2:1739

    CAS  Article  Google Scholar 

  22. 22.

    Tsygankov V-Y (2019) Organochlorine pesticides in marine ecosystems of the Far Eastern Seas of Russia (2000–2017). Water Res 161:43–53.

    CAS  Article  Google Scholar 

  23. 23.

    Correia TG, Narcizo AM, Bianchini A, Moreira RG (2010) Aluminum as an endocrine disruptor in female Nile tilapia (Oreochromis niloticus). Comp Biochem Phys C 151(4):461–466.

    CAS  Article  Google Scholar 

  24. 24.

    Mondal S, Subramaniam C (2020) Xenobiotic contamination of water by plastics and pesticides revealed through real-time, ultrasensitive, and reliable surface-enhanced Raman scattering. ACS Sustain Chem Eng 8(20):7639–7648.

    CAS  Article  Google Scholar 

  25. 25.

    Briceno G, Lamilla C, Leiva B, Levio M, Donoso-Pinol P, Schalchli H, Gallardo F, Diez MC (2020) Pesticide-tolerant bacteria isolated from a biopurification system to remove commonly used pesticides to protect water resources. PLoS ONE 15(6):20.

    CAS  Article  Google Scholar 

  26. 26.

    Tsui MTK, Chu LM (2003) Aquatic toxicity of glyphosate-based formulations: comparison between different organisms and the effects of environmental factors. Chemosphere 52(7):1189–1197.

    CAS  Article  Google Scholar 

  27. 27.

    Sun Q, Liu Z (2020) Impact of tourism activities on water pollution in the West Lake Basin (Hangzhou, China). Open Geosci 12(1):1302–1308.

    Article  Google Scholar 

  28. 28.

    Garcés-Ordóñez O, Espinosa Díaz LF, Pereira Cardoso R, Costa Muniz M (2020) The impact of tourism on marine litter pollution on Santa Marta beaches Colombian Caribbean. Mar Pollut Bull 160:111558.

    CAS  Article  Google Scholar 

  29. 29.

    Katircioglu S, Saqib N, Katircioglu S, Kilinc CC, Gul H (2020) Estimating the effects of tourism growth on emission pollutants: empirical evidence from a small island. Cyprus Air Qual Atmos Hlth 13(4):391–397.

    CAS  Article  Google Scholar 

  30. 30.

    Saeck EA, O’Brien KR, Weber TR, Burford MA (2013) Changes to chronic nitrogen loading from sewage discharges modify standing stocks of coastal phytoplankton. Mar Pollut Bull 71(1–2):159–167.

    CAS  Article  Google Scholar 

  31. 31.

    Välitalo P, Kruglova A, Mikola A, Vahala R (2017) Toxicological impacts of antibiotics on aquatic micro-organisms: a mini-review. Int J Hyg Envir Heal 220(3):558–569.

    CAS  Article  Google Scholar 

  32. 32.

    Wang X, Ryu D, Houtkooper RH, Auwerx J (2015) Antibiotic use and abuse: a threat to mitochondria and chloroplasts with impact on research, health, and environment. BioEssays 37(10):1045–1053.

    CAS  Article  Google Scholar 

  33. 33.

    Castaldo G, Delahaut V, Slootmaekers B, Bervoets L, Town RM, Blust R, De Boeck G (2020) A comparative study on the effects of three different metals (Cu, Zn and Cd) at similar toxicity levels in common carp. Cyprinus carpio J Appl Toxicol.

    Article  Google Scholar 

  34. 34.

    Li J, Liu Y, Zuo R, Teng Y, Ai Y, Yang J (2018) Influences of dissolved humic acid on Zn bioavailability and its consequences for thyroid toxicity. Ecotoxicol Environ Saf 166:132–137.

    CAS  Article  Google Scholar 

  35. 35.

    Gao L, Li R, Liang Z, Wu Q, Yang Z, Li M, Chen J, Hou L (2020) Mobilization mechanisms and toxicity risk of sediment trace metals (Cu, Zn, Ni, and Pb) based on diffusive gradients in thin films: A case study in the Xizhi River basin South China. J Hazard Mater.

    Article  Google Scholar 

  36. 36.

    Tkaczyk A, Mitrowska K, Posyniak A (2020) Synthetic organic dyes as contaminants of the aquatic environment and their implications for ecosystems: a review. Sci Total Environ 717:19.

    CAS  Article  Google Scholar 

  37. 37.

    Nesme T, Withers PJA (2016) Sustainable strategies towards a phosphorus circular economy. Nutr Cycl Agroecosystems 104(3):259–264.

    Article  Google Scholar 

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The authors would like to thank Yilun Gao, Xianyu Hou, Jin Tang, Wei Zhang from Chongqing University for sample collection and in situ parameters investigation.


This work was founded by the EMR-rural project (No: 2019YFD1100500) from the National Key R&D Program of China.

Author information




JSG was responsible for the general design of the review; YS performed the majority of data evaluations and wrote the first draft of the manuscript. FF and YXJ supported data interpretation and drafted the manuscript; CCW, YJY and ZLC contributed on field sampling and data evaluations; YTF, TTL and MZ contributed on the laboratorial analysis. All authors read and approved the final manuscript.

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Correspondence to Jinsong Guo.

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Supplementary Information

Additional file 1. Table S1:

Location information of sampling sites. Table S2. Environmental quality standards for surface water (GB3838-2002).

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Shao, Y., Fan, Y., Yang, Y. et al. How much do the conventional parameters contribute to the biological toxicity of surface water in different types of villages?. Environ Sci Eur 33, 76 (2021).

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  • Rural surface water
  • Conventional parameter monitoring
  • Bioanalytical techniques
  • Acute toxicity