Species, Spatial-Temporal Distribution, and Contamination Assessment of Trace Metals in Typical Mariculture Area of North China

Introduction

Trace metals (TMs) are important micronutrients in marine systems and are essential for the growth of organisms (Morel et al., 2003; Li et al., 2017; Posacka et al., 2017). Whether TMs are essential or toxic mainly depends on their concentrations (Herrero et al., 2014). On the one hand, a number of TMs can be limiting factors to the primary production of an ecosystem if their concentrations are too low (Martin et al., 1994; Maldonado et al., 2006). On the other hand, if their concentrations exceed a certain threshold, they may become toxic for marine organisms (Sunda et al., 1987; Moffett et al., 1997; Hook and Fisher, 2001; Rivera-Duarte et al., 2005; Dong et al., 2015). Although many TMs can be found at extremely low concentrations in seawater, through biological accumulation, TM concentrations in seafood can be hundreds of times greater than in seawater (Maity et al., 2017). Once excess TM enters the body through the food chain, it will be detrimental for human health.

Marine metal pollution has become the focus of many scholars (Ellwood and Van den Berg, 2000; Fitzwater et al., 2000; Ellwood, 2008; Croot et al., 2011; Zhang et al., 2014; Heller and Croot, 2015). TM pollutants not only gradually deteriorate the seawater quality, but also cause serious pollution of aquatic products. With the continuing industrial development and population growth, human activities release large amounts of TMs into the marine environment, which seriously harms marine ecosystems (Maity et al., 2017). As a result, the determination and analysis of TMs in seawater are urgently needed. In seawater, only dissolved TMs can be directly absorbed and utilized by organisms. These dissolved TMs can be subdivided into total dissolved TMs, dissolved reactive TMs, and dissolved inert TMs. The total dissolved TM concentration is the sum of the dissolved reactive TM and the dissolved inert TM (Han et al., 2018). So far, environmental measurements have only established the total concentration of target metals in samples (Kot and Namiesńik, 2000), which was proved to be inadequate for assessing their bioavailability, behavior, and toxicity (Huang et al., 2003; Adnívia et al., 2016). In the water body, the degree of TM contamination and its effect on both their biological activity and toxicity are directly related to the TM species present. Hence, it is essential to determine the species of TMs in marine environments. In this experiment, the concentrations of total dissolved TM, dissolved reactive TM, and dissolved inert TM were determined by at least three measurements.

There are many techniques for separation and detection of TMs, including gas chromatography (Wang and Cui, 2016), capillary zone electrophoresis (Kubáň and Timerbaev, 2014), supercritical fluid chromatography (Henry and Yonker, 2006), atomic absorption spectrometry (Ribeiro et al., 2017), inductively coupled plasma mass spectrometry (Zhu et al., 2017), and atomic emission spectrometry (Vidal et al., 2016). Among the analytical techniques, electroanalytical techniques are the most universal analytical tool due to the simultaneous quantitative and qualitative determinations of TMs in various matrices with high levels of convenience and rapid and straightforward analytical processes.

Yantai Sishili Bay is a typical mariculture area of North China and is located in Shandong Province. Its area of about 87 km² include a shallow sea aquaculture area of about 53 km², and mariculture activities are pursued throughout the year. It is an important breeding ground for fish, shrimp, crab, and shellfish, and mainly cultures seafood for the local area, especially scallops. As Sishili Bay is a semi-closed sea area, its water exchange capacity is poor, cargo throughput increases, and mariculture, industrial, agricultural, and domestic sewage discharges exert great pressure on the marine ecosystem of Sishili Bay (Wang et al., 1995; Tang, 2004; Liu et al., 2009; Zhang et al., 2012). Effluent discharge from the sewage treatment plant of Xinan River and Zhifu Island, aquatic animal feed residues and excrement, as well as domestic waste from workers of aquatic farms all contain a certain level of TMs, which pollute the marine environment of Sishili Bay. Chemical drugs are often used in mariculture to control pests, and the residues of these drugs also cause TM pollution of both the marine environment and the marine ecosystem. For example, CuSO₄ is widely used to treat shrimp diseases along the Pearl River Delta, resulting in severe Cu pollution in the aquatic environment of this region (Hu et al., 2007). As a mariculture area, it is very important to investigate the pollution level of seawater, especially the metal levels. Although various studies investigated TMs in seawater (Nimmo et al., 1989; Meng et al., 2008; Mao et al., 2009; Tian et al., 2009; Wang et al., 2012; Su et al., 2015, 2016, 2017; Han et al., 2018), little information is available on the spatial-temporal distributions and species of TMs. However, studying the spatial-temporal distributions and species of TM is helpful to achieve a better understanding of the TM pollution degree in seawater and provides effective data support for aquaculture.

Although Cu, Pb, Cd, and Zn are essential metals for the growth of organisms in marine environments, they are also the main elements that cause marine metal pollution. Once these metal elements occur excess, they cause serious harm to aquatic animals, aquatic plants, and the human body. Excessive Cu and Zn can harm the normal reproduction and growth of aquatic animals and plants, excessive Cu and Pb are teratogenic and carcinogenic, and excessive Cd can lead to kidney damage (Xie et al., 2014). Therefore, the pollutions of Cu, Pb, Cd, and Zn must not be ignored. This study investigated species, spatial-temporal distribution, sources, correlations with physiochemical factors, and contamination of specific TMs (Cu, Pb, Cd, and Zn) in the typical mariculture area of North China. Different species of Cu, Pb, Cd, and Zn were simultaneously analyzed by anodic stripping voltammetry (ASV) with different procedures. The relationships between different species of metals with the micronutrient metal Fe, chlorophyll a, salinity, dissolved oxygen (DO), conductivity, pH, and temperature were investigated in detail.

Materials and Methods

Sample Collection

Samples were collected from the surface seawater of Sishili Bay (Yellow Sea, China, see Figure 1), covering 12 stations and 5 months of 2018 (March, May, July, September, and November). Cleaning procedures are strictly followed with GEOTRACES manual when collecting water samples. All seawater samples were collected with a 2.5-L sample collector (Taiheng Plastics Corporation, Henan, China) into individual polypropylene bottles (Xiangyun Plastic Products Factory, Hebei, China). These polypropylene bottles had been cleaned with 1 M HCI (analytical grade) and thoroughly rinsed with deionized water (18.2 MΩ cm specific resistance). Following collection, they were filtered through 0.45-μm cellulose acetate membranes (Shanghai Xingya Purification Material Factory, Shanghai, China) and were stored in polypropylene bottles at 4°C until further analysis. Chlorophyll a (Chl a) was collected from all seawater samples and stored in 0.45-μm cellulose acetate membranes wrapped with aluminum foil (Xuhuacheng Plastic Co., Ltd., Shanghai, China), and stored at −20°C until use. The temperature, salinity, DO, conductivity, and pH in surface seawater were measured by an YSI MI-parameter Meter (ProPlus, United States).

FIGURE 1

Figure 1. Map of the sampling stations in Sishili Bay. The red stars mark the sampling stations.

All containers used in the experiment were soaked in nitric acid (HNO₃, 5 wt%, analytical grade) for at least 24 h before use, and rinsed thoroughly with deionized water before starting the experiment. All reagents used were of analytical grade and purchased from Shanghai Sinopharm Chemical Reagent Co., China. All deionized water was sourced from the Pall Cascada’s laboratory water system (Port Washington, New York, United States).

Sampling Stations

The semi-closed Sishili Bay is located on the eastern shore of Yantai city and is one of the most intensive scallop aquaculture areas of North China (Dong et al., 2019). The average water depth is less than 15 m. The quality of the marine environment is not only affected by mariculture, but also by industrial, agricultural, and domestic sewage discharges by local Zhifu and Laishan districts. Studies showed that a large quantity of industrial materials and wastewater are discharged by the Zhifu Island sewage treatment plant every year (Sheng et al., 2012). In this experiment, all sampling stations were located in Sishili Bay within the area from 37°26′49.44″N to 37°38′10.14″N and 121°24′0.00″E to 121°40′27.85″E. The details can be found in Supplementary Table S1. The locations of the 12 sampling stations (S1–S12) in this study are shown in Figure 1. These were situated in the nearshore areas (S1–S3, where S3 is near the Xinan River sewage treatment plant), port areas (S4 is near Yantai port), mariculture areas (S5, S6, S8, and S9), sewage outfall areas (S7 is near the Zhifu Island sewage treatment plant), and offshore areas (S10–S12). These locations are severely affected by human activities (Li et al., 2013; Dong et al., 2019).

Determination of Different Species of Cu, Pb, Cd, and Zn

In this study, all voltammetric measurements were carried out using the 797 VA Computrace system with software (version 1.3) from Metrohm (Beijing, China). A three-electrode system was used, consisting of a working electrode, a reference electrode, and a counter electrode. A standard addition method (Illuminati et al., 2010) was adopted for all TM detections.

The concentrations of different species of Cu, Pb, Cd, and Zn in seawater samples were determined by ASV, which imposes detection limits of 28.87, 1.06, 2.97, and 12.70 ng L^–1, respectively (Han et al., 2018). Seawater samples were pretreated, as shown in Figure 2. The filtered samples were transferred to quartz tubes, and then, UV digested for 45 min. When the sample had cooled, 10 mL were transferred into the voltammetric cell and DO was removed with high-purity nitrogen for 5 min. Finally, the total dissolved TM concentration was obtained by ASV (Achterberg and van den Berg, 1994). The UV digestion apparatus was provided by van den Berg’s research group (Oceanography Laboratories, University of Liverpool, United Kingdom). Dissolved reactive TM concentrations were obtained via direct electrochemical detection of the filtered samples. Filtered samples (10 mL) were placed into the voltammetric cell and DO was removed with high-purity nitrogen for 5 min; then, the dissolved reactive TM concentration was obtained by ASV (Han et al., 2018). Dissolved inert TMs were obtained via the difference between total dissolved TMs and dissolved reactive TMs (Florence, 1986).

FIGURE 2

Figure 2. Diagram showing the speciation analysis processes for trace metals (TMs).

The detailed parameters of the differential pulse voltammetry were as follows: deposition time was 60 s, deposition potential was −1.15 V, initial potential was −1.15, termination potential was 0.02 V, sweep rate of 0.03 Vs^–1, and the peak positions of Cu, Pb, Cd, and Zn were −0.17, −0.41, −0.58, and −1.0 V, respectively (Han et al., 2018). The accuracy and reliability of the method have been verified in certified reference materials (CASS-6 and NASS-6) (Han et al., 2018).

Determination of Total Dissolved Fe

Cathode stripping voltammetry (CSV) was used to determine the total dissolved Fe concentration in a 797 VA Computrace system, which imposes a detection limit of 0.84 nM (Lin et al., 2016). Detection details followed were described in Lin et al. (2016). Seawater samples were pretreated, as shown in Supplementary Figure S1. First, concentrated nitric acid was added to maintain the pH value of the water sample to less than 2.0, and added H₂O₂. Next, NaOH was added to maintain the pH at 8.0 after 90 min of UV digestion. 10 mL seawater samples, 100 μL 1 M HEPPS/0.5 M NaOH (Buffer solution, pH value of the system was about 8.0), 10 μL 0.02 M DHN (Complexing ligand) and 500 μL 0.4 M KBrO₃ (Oxidant) were added successively in the voltammetric cell and then remove dissolved oxygen with high-purity nitrogen for 5 min (Lin et al., 2016). The detailed parameters of DPV were as follows: the deposition potential was −0.1 V, deposition time was 60 s, initial potential was −0.1 V, termination potential was −1.1 V, with a sweep rate of 0.024 Vs^–1 (Lin et al., 2016). The accuracy and reliability of the method have been verified in certified reference materials (CASS-5 and NASS-6) (Lin et al., 2016).

Determination of Chl a

The concentration of Chl a was determined by using a Turner Designs Trilogy fluorometer (George et al., 2015). The filter membrane was cut into pieces and extracted with a 90% acetone solution at 4°C for 24 h, then centrifuged at 4000 r speed for 10 min. The supernatant was taken for the concentration determination of Chl a (Zhang et al., 2016). The whole process was done in dark light.

Evaluation of the Trace Metal Contamination Level

In this study, both the contamination factor (C_f) and the contamination degree (C_d) were used to evaluate the surface seawater quality (Hakanson, 1980; Lü et al., 2015). C_f and C_d reflect the contamination level of a single TM and overall TMs in the medium, respectively (Wang et al., 2018).

$$C_f=\frac{C_c}{C_b}\mathit{\hspace{1em}}{C}_d=\sum _{i=1}^n{C}_f$$

where C_c represents the concentration of TM, and C_b represents the background value of corresponding TM in the seawater. The background concentrations used the grade-I seawater quality standard for China (5 μg/L Cu, 1 μg/L Pb, 1 μg/L Cd, and 20 μg/L Zn; GB 3097–1997) (Aqsiq, 1997). C_f and C_d values were interpreted as recommended by Hakanson (1980).

Results and Discussion

Species of TMs

The concentrations of TMs (Cu, Pb, Cd, and Zn) in different species in the surface seawater of Sishili Bay during the five investigated months are listed in Supplementary Table S2. The total dissolved Cu, Pb, Cd, and Zn concentrations ranged within 1.75–8.08, 0.43–2.75, 0.07–0.29, and 2.58–30.28 μg/L, respectively. The dissolved reactive Cu, Pb, Cd, and Zn concentrations ranged within 1.05–5.55, 0.15–1.59, 0.04–0.23, and 1.62–20.14 μg/L, respectively. The dissolved inert Cu, Pb, Cd, and Zn concentrations have ranges of 0.22–2.94, 0.02–1.56, 0.01–0.07, and 0.43–16.96 μg/L, respectively. The concentrations of different species of TMs followed (in decreasing order): Zn > Cu > Pb > Cd.

The concentrations of total dissolved Cu, Pb, Cd, and Zn in all samples for different months are shown in Figure 3. The statistical results identified significant differences in TM concentrations for all stations in different months. In March, the highest values of total dissolved Cu, Cd, and Zn were found at station S1, and the highest value of total dissolved Pb was found at station S12. In May, the highest values of total dissolved Cu, Pb, Cd, and Zn were found at stations S4, S6, S11, and S5, respectively. In July, the highest value of total dissolved Cu and Zn was found at station S1, and the highest values of total dissolved Pb and Cd were found at stations S10 and S3, respectively. In September, the highest values of total dissolved Cu, Pb, Cd, and Zn were found at stations S4, S6, S8, and S1, respectively. In November, the highest values of total dissolved Cu, Pb, Cd, and Zn were found at stations S6, S10, S4, and S1, respectively. In summary, the maximum values of dissolved Cu, Pb, Cd, and Zn were 8.08 (station S1 in March), 2.75 (station S6 in May), 0.29 (station S4 in November), and 30.28 μg/L (station S5 in May), respectively.

FIGURE 3

Figure 3. Concentrations of total dissolved TMs at all sampling stations in different months.

The annual mean concentrations of total dissolved Cu, Pb, Cd, and Zn in Sishili Bay were compared with those from other marine areas (Table 1). The results for all dissolved concentrations of Cu, Pb, Cd, and Zn found values of the same order of magnitude as those reported for Bohai Bay (Meng et al., 2008; Mao et al., 2009), Jinzhou Bay (Wang et al., 2012), the North Yellow Sea (Tian et al., 2009), the San Francisco Bay (Flegal et al., 1991), Boston Harbor (Li et al., 2010), and the Weser estuary (Turner et al., 1992). The concentrations of Cu in Sishili Bay were comparable with those in Bohai Bay, Jinzhou Bay, and the Weser estuary but higher than concentrations in the North Yellow Sea, the San Francisco Bay, and Boston Harbor. The concentrations of Pb in Sishili Bay were higher than in other sea areas, but lower than in Bohai Bay. The concentrations of Cd in Sishili Bay were lower than in Jinzhou Bay but higher than in Boston Harbor and San Francisco Bay. The concentrations of Zn were lower than in Bohai Bay but higher than in the North Yellow Sea, Boston Harbor, and San Francisco Bay.

TABLE 1

Table 1. Comparison of the annual mean concentrations (μg/L) of dissolved Cu, Pb, Cd, and Zn in the seawater of other regions of the world [parentheses present the range of trace metals (TMs)].

The annual mean percentages of dissolved reactive and dissolved inert concentrations of Cu, Pb, Cd, and Zn in the total dissolved concentrations are presented in Figure 4. The proportions of dissolved reactive TMs are higher, which is consistent with previous observations by Han et al. (2018). The mean percentages of the dissolved reactive concentrations of Cu, Pb, Cd, and Zn were 65.67, 59.92, 72.56, and 64.29%, respectively, following (in decreasing order): Cd > Cu > Zn > Pb. The dissolved reactive TMs (detected by ASV) were classified as free ions, inorganic complexes, and weak organic complexes (Achterberg et al., 2003). Moreover, only free ions, a number of inorganic complexes, and a small number of organic complexes are responsible for the uptake processes by the cells of organisms (Huang et al., 2003). These results indicate that the dissolved reactive TMs had high bioavailability and toxicity for marine organisms. The lowest annual mean percentages of the dissolved reactive Cu, Pb, Cd, and Zn were found at stations S1, S10, S2, and S5, respectively. Considering that the chlorophyll a level was the highest at station S1, uptake by phytoplankton could explain the low proportion of the dissolved reactive Cu (Su et al., 2015). The low proportion of the dissolved reactive Pb at station S10 may have been caused by pollutions from the sewage outfall area, influenced by tidal currents that contained a large amount of dissolved inert Pb. At station S2, higher biological activity may have been the cause for the low proportion of dissolved reactive Cd. Station S5 was an intensive scallop mariculture, and uptake from scallops could be an explanation for the low proportion of dissolved reactive Zn (Zhang et al., 2012).

FIGURE 4

Figure 4. Annual mean percentage of the dissolved reactive and inert concentrations of Cu, Pb, Cd, and Zn in surface seawater of Sishili Bay.

Spatial-Temporal Distribution Characteristics of TMs

Spatial Distribution Characteristics and Sources of TMs

The spatial distributions of TMs (annual average values) in the surface seawater of Sishili Bay are presented in Figure 5. The spatial distributions of total dissolved Cu, Cd, and Zn were similar, indicating that they might have the same or similar input sources. The concentrations decreased from nearshore to offshore and were higher in the west than in the east. The total dissolved Pb concentrations were also higher at nearshore stations than at offshore stations, but lower in the west than in the east. The spatial distribution patterns of the tested metals implied that they may have been affected by anthropogenic pollution and coastal sources. The highest concentrations of total dissolved Cu and Zn were found at station S1, near nearshore areas, where Zhifu Bay coastal industrial and agricultural activities may cause higher Cu and Zn concentrations. The highest total dissolved Cd concentration was found at station S4, near Yantai port, suggesting vessel traffic and vessel sewage as the main reasons for the high concentration of Cd (Liu et al., 2012; Han et al., 2018). Pb is a atmophile-type metal, and its atmospheric deposition is widely considered to be an important source of Pb in seawater (Stumm and Morgan, 1996; Bruland and Lohan, 2003). Therefore, the higher Pb concentration at offshore stations may have been caused by atmospheric deposition. The highest Pb concentration was found at station S6, near mariculture areas, suggesting that feed residues, chemical drug residues, and household waste from aquaculture workers may contribute to the high levels of Pb. Pb at S10 station was also relatively high, which may have been caused by pollutants from sewage outfall areas, which were carried by oceanic currents (Liu et al., 2012).

FIGURE 5

Figure 5. Spatial distribution of the concentrations of total dissolved and dissolved reactive TMs (annual average values) in the surface seawater of Sishili Bay. (A) Total dissolved Cu (μg/L), (B) dissolved reactive Cu (μg/L), (C) total dissolved Pb (μg/L), (D) dissolved reactive Pb (μg/L), (E) total dissolved Cd (μg/L), (F) dissolved reactive Cd (μg/L), (G) total dissolved Zn (μg/L), and (H) dissolved reactive Zn (μg/L).

Further study showed that the spatial distributions of dissolved reactive TMs and total dissolved TMs were similar (Figure 5). The highest concentrations of dissolved reactive Cu, Pb, Cd, and Zn were found at stations S1, S6, S4, and S1, respectively. These results indicated that the factors and sources of dissolved reactive TMs and total dissolved TMs may be similar. At station S2, the concentration of dissolved reactive Cd was low. According to the data results, the percentage of dissolved inert Cd at station S2 was highest (Figure 4), which can explain the lower dissolved reactive Cd.

Temporal Distribution Characteristics

The temporal variation of TMs (monthly average values) in Sishili Bay were significant (as presented in Figure 6). The temporal variations of total dissolved TMs and dissolved reactive TMs were similar, indicating that they might have the same or similar input sources. Total dissolved TM and dissolved reactive TM concentrations were highest in March, May, and November, and lowest in July and September. Aquaculture exerts a certain influence on the TM concentration, which adds complexity to the study of TM. The highest values of chlorophyll a were found in July, followed by September, which explains the lower concentrations of TMs in July and September (Su et al., 2015). Bioactivity decreased in March, May, and November, which may be a reason for the higher concentrations of TMs.

FIGURE 6

Figure 6. Temporal variation of different species of Cu, Pb, Cd, and Zn (μg/L, monthly average values) in the surface seawater of Sishili Bay.

Contamination Level of TMs

The total dissolved TM concentrations were assessed according to the seawater quality standards of China (Table 2). The concentrations of total dissolved Cd in the present study remained far below the grade-I seawater quality standard of China. In March, May, September, and November, the Pb concentrations in all locations exceeded the grade-I seawater quality of China. However, each TM level in the present study remained lower than the grade-II seawater quality standard of China. The concentrations of total dissolved TMs (annual mean values) of all 5 months were used to calculate C_f and C_d (Figure 7). The contamination levels of the total dissolved TMs were assessed according to C_f and C_d value standards (Table 3). The C_f values of Cu, Pb, Cd, and Zn ranged within 0.35–1.62, 0.43–2.75, 0.07–0.29, and 0.13–1.51, respectively. C_f values of Cd were all lower than 1, indicating that Cd is at a low contamination level in Sishili Bay. Pb had the highest C_f value, followed by Cu, Zn, and Cd, indicating low to moderate contamination levels. These results indicate that the major contamination pressure in Sishili Bay originates from Pb, Cu, and Zn. C_d values ranged from 1.11 to 4.70, which indicated a low contamination level of Sishili Bay. If the grade-I seawater quality standard is used as background data, contamination levels may rank differently. The actual pollution level might be higher than identified in the present study. In general, TM contamination in the seawater of Sishili Bay is light.

TABLE 2

Table 2. Rates of total dissolved TMs exceeding seawater quality standards of China among sampling locations.

FIGURE 7

Figure 7. C_f and C_d for total dissolved TMs (annual mean concentrations) in the surface seawater of Sishili Bay. (A) Value of C_f and (B) the value of C_d.

TABLE 3

Table 3. C_f and C_d standards (Hakanson, 1980; Lü et al., 2015).

Relationship of TMs With Micronutrient Metal (Fe)

Fe is ubiquitous in the natural environment, an essential nutrient for almost all organisms (Kustka et al., 2002), and key to limiting phytoplankton growth (Martin et al., 1991). To obtain more valuable experimental data, the total dissolved Fe concentration was determined and the relationship between Fe and TMs was further analyzed. The results showed that Fe concentrations were higher in Sishili Bay than in other areas (Nimmo et al., 1989; Su et al., 2016, 2015, 2017). The spatial distribution of the total dissolved Fe (annual average values) in the surface seawater of Sishili Bay is presented in Figure 8A. Unlike total dissolved Cu, Pb, Cd, and Zn, a reverse distribution pattern was found for total dissolved Fe, indicating that the source of Fe might differ from the sources of Cu, Pb, Cd, and Zn. The concentrations were lower at nearshore stations than at offshore stations. The highest concentration of total dissolved Fe was found at station S12. Station S12 was located near offshore areas, where the dry-wet deposition of atmospheric aerosols was the main external source of Fe (Johnson et al., 1994; Yuan et al., 2003). This indicates that atmospheric deposition may be the cause for the higher Fe levels. However, station S12 was close to the aquaculture zone, suggesting that sewage from the aquaculture area carried by ocean currents may be responsible for the higher Fe. The temporal variation of the total dissolved Fe (monthly average values) in Sishili Bay is presented in Figure 8B. Significant temporal variations in total dissolved Fe were found. The total dissolved Fe concentrations were highest in March and lowest in May. The variation trends of total dissolved Cu, Pb, Cd, Zn, and Fe are shown in Figure 8C. From March to May, the concentration of Fe and Cu decreased obviously, while the concentrations of Pb, Cd, and Zn increased slightly. March to May is when phytoplankton begins to grow, which suggests that during this time, Fe and Cu are more readily absorbed by phytoplankton. Then, Fe and Cu started to increase, but Pb, Cd, and Zn started to decrease and did not start to increase until July. From May to July, phytoplankton began to bloom, which may be the reason why Pb, Cd, and Zn decreased rapidly. From July to September, Cd and Zn still showed a slight decrease. From September to November, only Cu followed a slight decreasing trend. Overall, except for November, Cu presented a similar tendency than Fe.

FIGURE 8

Figure 8. Spatial-temporal distribution of total dissolved Fe concentrations in surface seawater of Sishili Bay and the change trend of Cu, Pb, Cd, Zn, and Fe. (A) Spatial distribution (nmol/L, annual average values), (B) temporal variation (nmol/L, monthly average values). (C) Change trend of Cu, Pb, Cd, Zn, and Fe. Percentage values indicate the change trend of the metal concentrations in other months compared with the first months (where the first month’s concentration is equal to 100%).

Correlations With Physiochemical Factors of TMs

The values of the physiochemical parameters in Sishili Bay during the five investigated months are listed in Supplementary Table S2. Water temperature, pH, salinity, DO, conductivity, and chlorophyll a ranged within 3.5–25.2°C, 7.78–8.40, 28.89–32.4, 3.92–17.26 mg/L, 45.22–50.89 μS/cm, and 0.02–21.19 μg/L, respectively. The spatial distributions of the physiochemical parameters (annual average values) for Sishili Bay are presented in Figure 9. Significant spatial variation was found for chlorophyll a. The values decreased from nearshore to offshore stations, and were higher in the west than in the east, which was similar to the previously observed results by Shen et al. (2014). The highest values of temperature, pH, salinity, DO, conductivity, and chlorophyll a were found at stations S10, S6, S9, S11, S9, and S1, respectively. The temporal variations of physicochemical parameters (monthly average values) in Sishili Bay are presented in Figure 10. The temporal variations of temperature and chlorophyll a were similar, and were significantly positively correlated (Yu et al., 2009). Water temperature and chlorophyll a values differed significantly among the 5 months, where the highest values were found in July, which was followed by September. The salinity and pH values were ∼31 and 8.1, respectively. DO and conductivity were much higher in March than in the other 4 months.

FIGURE 9

Figure 9. Spatial distribution of physicochemical parameters (annual average values) in surface seawater of Sishili Bay. (A) Temperature (°C), (B) pH, (C) salinity, (D) dissolved oxygen (DO; mg/L), (E) conductivity (μS/cm), and (F) chlorophyll a (μg/L).

FIGURE 10

Figure 10. Temporal variation of physicochemical parameters (monthly average values) in the surface seawater of Sishili Bay. (A) Temperature (°C), (B) pH, (C) salinity, (D) DO (mg/L), (E) conductivity (μS/cm), and (F) chlorophyll a (μg/L).

The Pearson correlation test was used to determine the correlation coefficients among dissolved reactive TM concentrations and physicochemical parameters. The results are shown in Table 4 (monthly average values). Statistical analysis showed that the concentrations of Cu, Pb, Cd, and Zn were positively correlated with each other, indicating that these four TMs have certain homology and compound contamination. The concentrations of Cu, Pb, Cd, and Zn were negatively related to temperature and chlorophyll a, and positively correlated to salinity, DO, and conductivity. The concentrations of dissolved reactive TMs were significantly positively correlated with salinity, indicating that the existing species of TMs were affected by salinity. This might be because increasing salinity intensifies the adsorption competition between ions, and the electrical properties of the adsorbent will also change; this leads to the desorption of TMs and the conversion of numerous granular TMs into dissolved states (Wu, 2012). The concentrations of Cu, Pb, Cd, and Zn were negatively correlated to pH, and the correlation was weak.

TABLE 4

Table 4. Pearson correlation matrix for the monthly average concentrations of dissolved reactive Cu, Pb, Cd, and Zn and the physicochemical parameters in the surface seawater of Sishili Bay.

Conclusion

The species, spatial-temporal distributions, sources, correlations with physiochemical factors, and the contamination assessments of TMs (Cu, Pb, Cd, and Zn) were investigated in a typical mariculture area of North China. Significant spatial-temporal distributions of TMs were identified. The spatial distribution patterns of these metals implied that they may be affected by anthropogenic pollution, discharged effluent, industrial and aquaculture pollution, uptake by organisms, atmospheric deposition, and other coastal sources. The dissolved reactive TMs and total dissolved TMs have similar spatial-temporal distributions, indicating that they also have similar factors and sources. Significant differences were found in TM concentrations at all stations in different months. The mean percentages of the dissolved reactive concentrations of Cu, Pb, Cd, and Zn were 65.67, 59.92, 72.56, and 64.29%, respectively. These values indicated that the dissolved reactive TMs have high bioavailability and toxicity for marine organisms. All TMs in the surface water were below the grade-II seawater quality standard of China. The single contaminator factors of the elements follow the order: Pb > Cu > Zn > Cd. This showed that the identified contamination degree of the mariculture area was at a low pollution level.

Data Availability Statement

All datasets presented in this study are included in the article/Supplementary Material.

Author Contributions

DP and HH designed the experiments. XD performed the experiments and analyses. SZ and CW helped the data analyses. DP and XD wrote the manuscript. All authors contributed to the article and approved the submitted version.

Funding

This work was financially supported by the National Key R&D Program of China (2019YFD0901103), the Original Innovation Project of Chinese Academy of Sciences (ZDBS-LY-DQC009), and the Key Research and Development Plan of Shandong Province (2017GHY215002).

Conflict of Interest

The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.

Supplementary Material

The Supplementary Material for this article can be found online at: https://www.frontiersin.org/articles/10.3389/fmars.2020.552893/full#supplementary-material

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