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Article

The Content Level, Spatial and Temporal Distribution Characteristics, and Health-Risk Assessment of Trace Elements in Upper Lancang River (Changdu Section)

1
Basin Water Environmental Research Department, Changjiang River Scientific Research Institute, Wuhan 430010, China
2
Hubei Provincial Key Laboratory of River and Basin Water Resources and Ecoenvironental Sciences, Changjiang River Scientifific Research Institute, Wuhan 430010, China
3
Changjiang Survey, Planning, Design and Research Co., Ltd., Wuhan 430010, China
*
Authors to whom correspondence should be addressed.
Water 2022, 14(7), 1115; https://doi.org/10.3390/w14071115
Submission received: 5 March 2022 / Revised: 27 March 2022 / Accepted: 28 March 2022 / Published: 31 March 2022
(This article belongs to the Topic Emerging Contaminants in the Aquatic Environment)

Abstract

:
Evaluation of trace elements in the water of Lancang River during the wet season (October) and dry season (December) was carried out to analyze the content of trace elements in the water, spatial and seasonal variations, enrichment, and health risks of dissolved trace metal. The results showed that the content of trace elements in the main stream of the upper Lancang River met the “Environmental Quality Standard for Surface Water” (GB3838-2002) Class I water-quality standard, but the Fe content in sampling points during the wet season exceeded the limit value of water-quality standard. Compared with other rivers in Tibet, the contents of As, Fe, and Pb in the study were relatively high. While Pb, As, and Zn were the mainly enriched trace elements. The water temperature, dissolved oxygen, conductivity, As, Cr, and Cu in the main stream of the upper Lancang River with significant seasonal variations. The content of trace elements in the front of the dam was lower than that in the tail and under the dam. The trace elements in the water of the reservoir area increased with an increase in the depth, and the reservoir had a certain interception effect on the trace elements. The As content in the main stream of the Lancang River was greatly affected by the branch of Angqu with high content of As. The HQingestion and HI of As in the part of the river in the study exceeded 1, and the water-quality health risks of the Guoduo reservoir tail and urban reaches were higher than those of other reaches, which should be paid more attention.

1. Introduction

Trace elements in water have been highly enriched, difficult to degrade, and highly toxic, especially the excessive accumulation of toxic trace elements which not only threaten safety of invertebrates and fish ecosystems, but also cause serious health effects on human beings [1,2,3,4]. Some trace elements are extremely toxic even at low concentrations, such as arsenic (As) and lead (Pb) [5]. As has been classified as a Group Ⅰ carcinogen by the International Agency for Research on Cancer [6] and can cause lung, bladder, and skin cancer even at low doses when inhaled by humans [5,7]. Exposure to Pb could seriously damage the kidney, liver, central nervous system, and blood system [8], and Pb has been one of the 67 important risk factors leading to global diseases [9]. Although iron (Fe) and Mn (manganese) are critical in organisms at specific concentrations, they have toxic effects on organisms when the concentration increases [10]. Under certain conditions, As adsorbs on manganese and iron oxides and hydroxide surface is released into the water [11], thus affecting the migration and transformation behavior of As in the aquatic environment [12].
Lancang-Mekong River is an international river, the tenth-largest river in the world [13], and one of the important cradles of human civilization in Southeast Asia [14]. It is called Lancang River with a total length of 2354 km in China. With the high-speed development of the economy in recent years, in the Lancang River basin, the urbanization process has accelerated, and trace elements have been influenced by city human activities. The compounds enter the river through hydropower development, mining, and urbanization construction. Trace element pollution is caused by geochemical background in local reach [15], and severe pollution of As and Pb in parts of Lancang River [16]. Zhang et al. [17] analyzed the sediment of the Lancang River and showed that the middle and lower of Lancang River was greatly affected by human activities. Trace elements such as copper (Cu), Pb, and As mildly or moderately polluted some parts of the Lancang River. In recent years, the Guoduo reservoir hydropower station [18] in the upper Lancang River had been put into operation, and the construction of the dam changed the original hydrological regime and form of Zhaqu [17,19]. The trace elements in the water would experience different physical and geochemical processes. In addition, the economy of Changdu city showed a trend of rapid development [20]. The study area belongs to the plateau cold and arid region, and there was a shortage of water resources in the area, which could not meet the living needs of the local people. In addition, due to the complex terrain of the local area, it is difficult to carry out relevant research work. At present, there are relatively few studies on trace elements in the upper reaches of the Lancang River, and the influence of urban development and hydropower station construction on trace elements in the upper of Lancang River is unclear. Therefore, this study took the urban section of Changdu city of Lancang River and the upper Zhaqu (80 km from the upper estuary of Zhaqu River) as the research object, carried out water environment investigation, analyzed the spatial and temporal distribution characteristics of major trace elements As, Pb, Fe, Mn, chromium (Cr), Cu, and zinc (Zn) in the water body, understood their enrichment status, and evaluated their health risks. To provide a scientific basis for water ecological environment protection in the upper Lancang River. this study provided a reference for water environment evolution of rivers and the utilization of water resources in the plateau area.

2. Materials and Methods

2.1. Study Area

Lancang River originates from the northern foot of Tanggula Mountain on The Qinghai–Tibet Plateau in China. It flows out of the border through Yunnan and Nanla Estuary, and then into the South China Sea through Laos, Thailand, Cambodia, and Vietnam [17]. The Lancang River passes through the parallel vertical valley of Hengduan Mountain. It is a steep and narrow river running from north to south with an elevation drop of 4700 m. Soil erosion, landslide, and debris flow frequently occur here [13]. The length of the source of the Lancang River to Changdu is 565.5 km, which is the upper of the Lancang River, namely, Zhaqu. Zhaqu is 448 km long in Qinghai Province and 117.5 km after exiting Qinghai to Changdu. The riverbed elevation of this section is 3150–3700 m, with an average gradient of 4.0‰–4.5‰, which is the river section with the largest river decline in the whole basin [21]. Zhaqu and Angqu flows into the Lancang River after confluence in the Changdu. The soil-forming part materials of Changdu mainly include Cretaceous, Jurassic, Triassic, Tertiary, and other multi-period magmatic rocks, sedimentary rocks, and metamorphic rock weathering residues, gravity deposits, slope deposits, etc. Zhaqu mainly contains Jurassic purple red sand and mudstone mixed with limestone [22,23]. Changdu is an important part of the Southwest Sanjiang Pb–Zn–Cu–Ag metallogenic belt [24]. In the region, a large number of Pb–zinc deposits have been produced in carbonate rocks, and depositional mercury, antimony, arsenic, and lead–zinc deposits occur [25].
Changdu is located in the semi-arid monsoon climate zone, with annual average precipitation of 473 mm and annual average temperature of 7.5 °C [26]. Zhaqu water is mainly resupplied by melting water of snow and ice in spring, and by rainwater and groundwater in summer, autumn, and winter. The water amount in spring accounts for about 12% of the annual water volume. Summer accounts for about 50% of the annual water volume [21]. From December to April of the following year, due to the influence of the westerly climate, precipitation is rare and the air is dry. Precipitation mainly concentrates from May to November [27], with sufficient sunshine, strong solar radiation, large diurnal temperature difference, and small annual temperature difference [28].

2.2. Sampling

According to the geographical characteristics of the study area, 11 sampling sites were set up in this study (Table 1). Two sites were set up in urban areas after Zhaqu merges into the Lancang River. One of them was set up at the estuary of the tributary Angqu River, and two sample sites were set up under the dam of the Guoduo reservoir. Six sample sites were set up from the dam site of the Guoduo reservoir to the 20 km upstream section (Figure 1). The survey was conducted in the wet season (October) and dry season (December) in 2018. The temperature, pH, dissolved oxygen, conductivity, and turbidity of the water were monitored on-site by a portable multi-parameter water-quality analyzer (EXO2, Yellow Springs Instrument Incorporated, Yellow Springs, OH, USA) when collecting water samples. The surface water was collected from 0.5 m below the water surface. In order to better understand the water-quality changes in the Guoduo reservoir, a vertical line was drawn in the 0.5 km section in front of the Guoduo reservoir dam, and water samples were collected at 0.5, 5, 10, 20, 30, 40, and 60 m below the water surface. After the water sample was collected, 500 mL of the sample was filtered through the 0.45 μm cellulose acetate filtration membrane on the sampling day. To filtered samples were added suprapure nitric acid until the pH of the samples was less than 2, and they were then refrigerator-stored until analysis.

2.3. Data Collection and Data-Quality Assessment

The temperature, pH, dissolved oxygen, and conductivity of all samples were calibrated before testing, with the pH electrode calibrated with buffers of pH 4.01, 7.00, and 10.01. As, Fe, Mn, Pb, Cr, Cu, and Zn were analyzed by ICP-MS (NexION 300X, PerkinElmer, Waltham, MA, USA) [29,30]. Standard reagent produced by the National Research Center for Standard Materials was used to formulate the standard curve before sample analysis. Blank samples were added to each batch of samples. The detection limits of As, Fe, Mn, Pb, Cr, Cu, and Zn (µg/L) were 0.12, 0.82, 0.12, 0.09, 0.11, 0.08 and 0.67, respectively. The recoveries (%) were 91.8, 97.2, 95.5, 92.4, 93.2, 94.6 and 96.1, respectively. All the data below the detection limit were analyzed and calculated using half of the detection limit [31].

2.4. Analytical Method

(1)
Enrichment of trace elements
In order to understand the enrichment status of metal elements in the study area, enrichment factor (EF) was used for analysis. The enrichment factor was the ratio of the metal element content in the water body of the study area to the average river content in the world [32]. According to the enrichment factor, the enrichment conditions could be divided into 6 categories: when EF > 100, it was abnormal enrichment; 10 < EF < 100, indicating super enrichment; 5 < EF < 10, indicating significant enrichment; 1.5 < EF < 5, indicating slight enrichment; 0.5 < EF < 1.5, indicating that it is not enriched. If EF < 0.5, this indicates a loss [33].
(2)
Health-risk assessment model
Health-risk assessment is a method to quantitatively describe the risk of health hazards caused by human exposure to polluted environments, which could be caused by two main ways: drinking water and skin contact. The United States Department of Environmental Protection (US EPA) had recommended a health-risk assessment model [34,35].
Risk entropy (HQ) reflects the potential risk status of non-carcinogenic risk: HQ < 0.1, indicating that the pollutant would not cause adverse health effects; 0.1 < HQ < 1, indicating that further investigation is required before action is taken; HQ > 1, indicating that pollutants are likely to cause adverse health effects [35].
H Q = A D D / R f D
The risk index (HI) can be used to assess the total potential non-carcinogenic risk from multiple pathways, and HI > 1 indicates that the pollutant might have adverse effects on human health or require further study.
H I = ( H Q i r g + H Q d e r m )
(i)
Calculation of average daily dose:
A D D i n g e s t i o n = C w × I R × A B S g × E F × E D B W × A T
(ii)
Calculation of skin exposure dose to water:
A D D d e r m a l = ( C w × S A × K p × E T × E F × E D × 10 3 ) ( B W × A T )
Reference values of exposure parameters are shown in Table 2.
Values of RfDingestion, RfDdermal, ABSg, and Kp of each (class) metallic element are shown in Table 3.

3. Result and Discussion

3.1. Trace Elements in Water

The contents of trace elements in the main stream of Lancang River were as follows: Fe > Mn > Zn > As > Cu > Pb > Cr. The contents of trace elements in all the sample points meet the Class I water-quality standard of Surface Water Environmental Quality Standard (GB3838-2002), but the Fe content in some sample points exceeded the limit value of water-quality standard (300 μg/L). The average content of As was 7.28 μg/L, which was lower than that of Sengzangbo River and Shiquan River, and much higher than that of Niyang River, Lhasa River (see Table 4), and the world river average. The average Pb content was 2.65 μg/L, which was lower than the lower Lancang River, but higher than other rivers in Tibet and the world river average. The average content of Fe was 153.1 μg/L, which was lower than that of Niyang River and far higher than that of other Tibetan rivers and the world river average. The average content of Mn was 10.84 μg/L, which was lower than that of Niyang River and the world river average, but higher than that of other Tibetan rivers. The average content of Cr was 2.27 μg/L, which was higher than that in the Niyang River and lower Lancang River. The average content of Cd was 0.06 μg/L, which was lower than that of other rivers in Tibet. The average Cu content was 6.25 μg/L, which was only lower than that of Niyang River, but much higher than the lower Lancang River. The content of Zn was only lower than that of Niyang River, but much higher than that of the lower Lancang River. Except for As, the mean contents of all other metal elements in this research were lower than the rivers of Bangladesh, but the contents of As, Fe, Pb, Cu, and Zn in the water of the Lancang River were higher than the corresponding elements’ contents in water of the world river average and other rivers of Tibet, which may be attributed to the weathering products of mineral resources and rocks outcropping in the drainage basin [40].
According to the analysis in Figure 2, different trace elements were enriched in different regions. As, Pb, and Zn were heavily enriched, Fe and Cr were moderately enriched, and Mn and Cu were slightly enriched or below in the reservoir tail water. In the reservoir water, Pb and Zn were heavily enriched, As was moderately enriched, and Fe, Mn, and Cu were slightly enriched or below. Pb and Zn were heavily enriched, As was moderately enriched, and Fe, Mn, Cu, and Cr were slightly enriched or below. Pb and As were heavily enriched, As was moderately enriched, and Fe, Mn, Cu, and Cr were slightly enriched or below. In conclusion, As, Pb, and Zn were the mainly enriched trace elements in the water in the study area.

3.2. Temporal and Spatial Distribution Characteristics of Trace Elements

The water temperature of the Lancang River mainstream in the study area fluctuated little in both the wet season (4.45–6.83 °C) and dry season (0.1–1.0 °C), but the average water temperature in the wet season (5.71 °C) was significantly higher than that in the dry season (0.37 °C) (Table 5). The pH value of river water in the wet season (8.16–8.36) and dry season (8.13–8.31) fluctuated little. The pH value of river water in the wet season (8.21) and dry season (8.22) had no significant difference, but the river water was slightly alkaline on the whole, which was similar to other rivers in Tibet [15,26]. The content of dissolved oxygen in river water in the wet season (8.86–10.24 mg/L) was higher than that in the dry season (6.52–7.25 mg/L), which was mainly due to the larger water quantity, faster flow rate, and faster exchange between water and air in the wet season. The conductivity of the river water in the wet season (226–385.3 μS/cm) was lower than that in the dry season (448–743 μS/cm).
The average content of As in the main stream of Lancang River in the wet season (5.49 µg/L) was significantly lower than that in the dry season (9.06 µg/L), but the content of Fe (average 207.7 µg/L) in the wet season was significantly higher than that in the dry season (average 98.49 µg/L) (Table 5). There was no significant difference between Mn content in the wet season (mean 10.29 µg/L) and dry season (mean 11.39 µg/L), and there was no significant difference between Pb content in the wet season (mean 3.11 µg/L) and the dry season (mean 2.18 µg/L). The contents of Cr, Cu, and Zn in the wet season were all lower than those in the dry season (Figure 3), which was similar to electrical conductivity. The main reason was that glacial meltwater and rainfall merge into rivers in the wet season, which reduces the contents of trace element plasma in water bodies [15]. According to analysis of Figure 2, the content of Fe and Pb in the wet season was higher than that in the dry season, which may be related to the higher value of local geological background. The fluctuation of As, Pb, Fe, Mn, and Cr in the main stream of the Lancang River was relatively large in the wet season, but relatively small in the dry season. This was mainly due to the high sediment content in the wet season and the continuous adsorption and desorption of trace elements in the sediment [46,47], and it was also affected by the merging of surrounding rainfall and melting water of snow and ice. In general, the contents of As, Cr, and Cu in the water body of the main stream of the Lancang River in the dry season were higher than those in the wet season, mainly because the water amount in the wet season was larger and the trace elements in the water body diluted [15].
From the changes of water quality along the main stream of the upper Lancang River, it could be seen that the variation trend of Fe and Mn in the main stream of Lancang River is similar, which was mainly because Mn was the associated element of Fe. The contents of As, Pb, Fe, Mn, Cr, and Zn were the lowest at L06 (0.3 km in front of the dam), which was the closest point to the dam site and has a slow flow rate. Most of the granular As, Pb, Fe, and Mn in the water body had sunk to the bottom of the reservoir. The contents of As, Pb, Fe, Mn, Cr, and Zn in surface water were low [48,49,50]. The As increased sharply at L09, especially during the wet season, which was mainly due to the high arsenic content (As: 18.84 μg/L) flowing into the upstream branch of L09. As, Pb, Fe, Mn, Cr, and Cu all rose suddenly at L07, mainly because L07 was located about 1 km downstream of the dam site of Guoduo reservoir, and might be due to the release of trace elements in the sediment due to the relatively large influence of water disturbance under the dam from the power station [51].

3.3. Vertical Distribution of Trace Elements

The water temperature slightly decreased with the deepening of the water depth, mainly because the local sunshine was strong, and the effect of heat conduction makes the external heat gradually decrease in the water body, so that the surface temperature is high and the bottom temperature is low (Figure 4). The vertical range of As and Fe content was 1.00–4.90 µg/L and 26.90–902 µg/L, respectively. The vertical range of Mn content was 1.16–92.23 µg/L. The vertical range of Pb content was 0.05–3.99 µg/L. The vertical range of Cr content was 0.06–2.87 µg/L. The vertical range of Cu content was 0.29–3.53 µg/L. The vertical range of Zn content was 0.33–6.48 µg/L. The contents of As, Fe, Mn, Pb, Cr, Cu, and Zn all increased gradually with the increase in water depth. The contents of trace elements in the water at 40 m increased obviously, and the highest concentrations were found in the bottom water. This was mainly due to the trace elements adsorbed on the particles settling at the bottom of the reservoir with the particles, and the bottom water being close to the bottom mud, significantly affected by sediment release [48]. Cu fluctuated greatly in the vertical direction, but the change rule was not obvious and the content of Cu was higher at 30 m and 60 m, which requires further study.

3.4. Health-Risk Assessment

Water-quality health-risk assessment could quantitatively evaluate the probability of health hazards to humans caused by water environmental pollutants [42]. According to the analysis of potential risks of trace elements in the wet season (Table 6), the average HI values of trace elements were as follows: As > Pb > Cr > Mn > Cd > Cu > Zn. Except for As, the values of HQ and HI of all trace elements were less than 1, indicating that Mn, Pb, Cr, Cu, and Zn in the study posed a lower health risk. The HQingestion of As in the reservoir tail and urban water body was lower than 1, indicating that there were health risks after As was ingested in the reservoir tail and urban water through the mouth. The HQingestion of As the dam was between 0.1 and 1, indicating that the health risk of oral ingestion needs to be further investigated. The HQingestion and HQdermal values of all children were lower than those of young people, indicating that the health risk of children through oral ingestion and skin contact was higher than that of young people. The HQdermal values of all trace elements in children and young adults were much less than 0.1, indicating that trace elements in the study area basically did not pose health risks through the skin.
According to the analysis of potential health risks of trace elements in the dry season (Table 7), the average HI values of trace elements were As > Cr > Pb > Mn > Cd > Cu > Zn. Only the values of HQingestion and HI of As in the urban area were greater than 1, while the values of HQingestion and HI in other trace elements were all less than 1, but close to 1, which should be paid great attention to by coastal residents.
The health risk of trace elements in the reservoir tail in the wet season was higher than that in the dry season (Figure 5), and HI was greater than 1, as shown in Figure 5. The health risk of trace elements in the reservoir area and under the dam in the wet season was much less than that in the dry season, but the HI value of the urban area in the wet season was almost the same as that in the dry season, and the HI was more than 1. The effects of trace elements on health risks of children and young people in the wet season were not significant, especially in the reservoir area and under the dam, while in the dry season, the effects of trace elements on health risks of children were greater than for young people. From upstream to downstream, the HI value in the wet season decreased first and then increased, and the HI value at the tail of reservoir was the largest. In the dry season, the HI value showed an increasing trend, and the highest in the urban areas.
The EPA and other documents emphasize uncertainty in the risk assessment of metals. Different ages and receptors, exposure conditions, pollutant concentrations, and daily water intake lead to different water–skin contact coefficients [33]. The exposure parameters used in the study were from the US EPA and the World Health Organization (WHO) and were not necessarily applicable to China. The risks of (class A) metal elements in the main stream of Lancang River need to be further studied.

4. Conclusions

The content of trace elements in the upper Lancang River meet the quality standard of Surface Water Environment (GB3838-2002) Class I, but the content of Fe in local sampling points during the wet season exceeds the limit of water-quality standards. Seasonal variation in trace elements in the upper Lancang River was obvious. The contents of Fe and Pb in the water in the wet season were higher than those in the dry season, while the contents of As, Mn, Cr, Cu, and Zn in the wet season were lower than those in the dry season. The As content in the upper Lancang River was greatly affected by the branch Angqu confluence. The reservoir has a certain interception effect on the distribution of the trace elements in the water, the trace elements in the front of the dam were lower than those in the tail and under the dam, and the trace elements in the water in the reservoir increased with the depth. The mean value of HI of trace elements followed this order: As > Cr > Pb > Mn > Cd > Cu > Zn. The health risk of Mn, Pb, Cr, Cu, and Zn in the study area was relatively low, but the health risk of As in some reaches was a certain health risk, which needs to be taken seriously. The research results provide basic data support for the comprehensive utilization of local water resources and water ecological environmental protection. In addition, several trace elements were investigated in this study, but further study on various other potential pollutants in the upper Lancang River is need to be enable more accurate assessment.

Author Contributions

Conceptualization, Z.Z.; Data curation, M.L., L.L., L.Z. and J.Z.; Formal analysis, Z.Z., L.L., L.Z., H.J. and J.Z.; Investigation, M.L., Z.Z., L.L., L.Z., L.D. and Y.H.; Methodology, M.L.; Project administration, L.L.; Software, R.L.; Writing—original draft, M.L.; Writing—review & editing, L.L. and L.Z. All authors have read and agreed to the published version of the manuscript.

Funding

This work was financially supported by Central Public-interest Scientific Institution Basal Research Fund (Grant No. CKSF 2021485/SH) and Changjiang River Scientific Research Institute was independently responsible for the innovation team project (Grant No. CKSF2021743/HL).

Acknowledgments

We thank the reviewers for their useful comments and suggestions.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Alexakis, D.E.; Kiskira, K.; Gamvroula, D.; Emmanouil, C.; Psomopoulos, C.S. Evaluating toxic element contamination sources in groundwater bodies of two Mediterranean sites. Environ. Sci. Pollut. 2021, 28, 34400–34409. [Google Scholar] [CrossRef] [PubMed]
  2. Liu, M.; Zhao, L.; Li, Q.; Hu, Y.; Huang, H.; Zou, J.; Gao, F.; Zhang, Y.; Xu, P.; Wu, Z. Disribution characteristics, Enrichment patterns and health risk assessment of dissolved trace elements in river water in the source region of the Yangtze River. J. Water Clim. Change 2021, 12, 2288–2298. [Google Scholar] [CrossRef]
  3. Adamiec, E.; Jarosz-Krzemińska, E.; Bilkiewicz-Kubarek, A. Adverse health and environmental outcomes of cycling in heavily polluted urban environments. Sci. Rep. 2022, 12, 148. [Google Scholar] [CrossRef]
  4. Zhao, L.; Li, W.; Lin, L.; Guo, W.; Zhao, W.; Tang, X.; Gong, D.; Li, Q.; Xu, P. Field investigation on river hydrochemical characteristics and larval and juvenile fish in the source region of the yangtze river. Water 2019, 11, 1342. [Google Scholar] [CrossRef] [Green Version]
  5. Carlin, D.J.; Naujokas, M.F.; Bradham, K.D.; Cowden, J.; Suk, W.A. Arsenic and Environmental Health: State of the Science and Future Research Opportunities. Enviorn. Health Perspect. 2016, 124, 890–899. [Google Scholar] [CrossRef] [PubMed]
  6. Juhasz, A.L.; Smith, E.; Weber, J.; Rees, M.; Rofe, A.; Kuchel, T.; Sansom, L.; Naidu, R. In vivo assessment of arsenic bioavailability in rice and its significance for human health risk assessment. Environ. Health Perspect. 2006, 114, 1826–1831. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  7. Naujokas, M.F.; Anderson, B.; Ahsan, H.; Aposhian, H.V.; Suk, W. The broad scope of health effects from chronic arsenic exposure: Update on a worldwide public health problem. Environ. Health Perspect. 2013, 121, 295–302. [Google Scholar] [CrossRef]
  8. Huang, P.C.; Su, P.H.; Chen, H.Y.; Huang, H.B.; Tsai, J.L.; Huang, H.I.; Wang, S.L. Childhood blood lead levels and intellectual development after ban of leaded gasoline in Taiwan a 9-year prospective study. Environ. Int. 2012, 40, 88–96. [Google Scholar] [CrossRef]
  9. Lim, S.S.; Vos, T.; Flaxman, A.D.; Danaei, G.; Shibuya, K.; Adair-Rohani, H.; AlMazroa, M.A.; Amann, M.; Anderson, H.R.; Andrews, K.G.; et al. A comparative risk assessment of burden of disease and injury attributable to 67 risk factors and risk factor clusters in 21 regions, 1990-2010: A systematic analysis for the Global Burden of Disease Study. Lancet 2010, 380, 2224–2260. [Google Scholar] [CrossRef] [Green Version]
  10. Kavcar, P.; Sofuoglu, A.; Sofuoglu, S.C. A health risk assessment for exposure to trace metals via drinking water ingestion pathway. Int. J. Hyg. Environ. Health. 2009, 212, 216–227. [Google Scholar] [CrossRef] [Green Version]
  11. Hasan, M.F.; Nur-E-Alam, M.; Salam, M.A.; Rahman, M.H.; Paul, S.C.; Rak, A.E.; Ambade, B.; Islam, A.R.M.T. Health Risk and Water Quality Assessment of Surface Water in an Urban River of Bangladesh. Sustainability 2021, 13, 6832. [Google Scholar] [CrossRef]
  12. Liu, R.; Yang, C.; Li, S.; Sun, P.; Shen, S.; Li, Z.; Kai, L. Arsenic mobility in the arsenic-contaminated Yangzonghai Lake in China. Ecotoxicol. Environ. Saf. 2014, 107, 321–327. [Google Scholar] [CrossRef] [PubMed]
  13. Liu, T.; Wang, X.; Zhu, E.; Liu, Z.; Zhang, X.; Guo, J.; Liu, X.; He, C.; HOU, S.; Fu, P.; et al. Evolution of the Dissolved Organic Matter Composition along the Upper Mekong (Lancang) River. ACS Earth Space Chem. 2021, 5, 319–330. [Google Scholar] [CrossRef]
  14. Yi, Z.; Gao, F.U.; Daming, H.E.; Shaojuan, L.I. Comparison of spatial-temporal distribution characteristics of water temperatures between Lancang River and Mekong River. Chin. Sci. Bull. 2007, 52, 141–147. [Google Scholar]
  15. Zhao, Z.; Li, S.; Xue, L.; Liao, J.; Yang, Q. Effects of dam construction on arsenic mobility and transport in two large rivers in Tibet, China. Sci. Total Environ. 2020, 741, 140406. [Google Scholar] [CrossRef]
  16. Song, J.; Fu, K.; Su, B.; Huang, Q.; Zhang, J. Spatial distribution of heavy metal concentrations and pollution assessment in the bed loads of the Lancang River system. Acta Geogr. Sin. 2013, 68, 389–397. [Google Scholar]
  17. Zhang, J.L.; Fu, K.D.; Wang, B.; Chen, L.Q.; Son, J.Y.; Su, B. Assessment of heavy metal pollution of bed sediment in the Lancang River. Prog. Geogr. 2014, 33, 1136–1144. [Google Scholar]
  18. Cheng, S.F.; Yun-Liang, L.I.; Zhong, H. Key points of project safety monitoring of Tibet Zhaqu Guoduo Hydropower Station. Electr. Power Surv. Des. 2013, 3, 71–77. [Google Scholar]
  19. Wang, L.H.; Jiao, Y.M.; Ming, Q.Z.; He, L.L.; Zhou, H.B. Evaluation of heavy metal pollution in Bijiang Basin in Yunnan Provinc. Res. Environ. Sci. 2009, 22, 595–600. [Google Scholar]
  20. Political Research Office of the CPC Changdu Municipal Committee. New Era new Style New Changdu-Summary of Economic and social development of Changdu since the sixth Central Tibet Work Symposium. New Tibet. 2020, 9, 35–39. [Google Scholar]
  21. He, D.M. Analysis on hydrological characteristics of Lancang—Mekong River. Yunnan Geogr. Environ. Res. 1995, 7, 139–146. [Google Scholar]
  22. Xue, H.T.; Bing, R.; Qi, W.X. Influencing factors of arsenic adsorption and desorption in sediments from Angqu River. Acta Sci. Circumstantiae 2020, 40, 3269–3276. [Google Scholar]
  23. Tao, Y.; Bi, X.; Xin, Z.; Zhu, F.; Liao, M.; Li, Y. Geological and geochemical characteristics and genetic analysis of the La Norma lead-zinc-antimony polymetallic deposit in the Changdu a of Tibet. Miner. Deposits 2011, 30, 599–615. [Google Scholar]
  24. Liu, Y.; Hou, Z.; Yu, Y.; Tian, S.; Li, Y.; Yang, Z. Study on the mineralization characteristics and genesis of MVT lead-zinc deposits in the Changdu a of Tibet. Acta Petrol. Sinica. 2013, 29, 1407–1426. [Google Scholar]
  25. Chen, B.; Qu, J. New achievements of geological structure research in Sanjiang Yuan. Geol. China 1992, 1, 15–17. [Google Scholar]
  26. Huang, X.; Sillanp, M.; Bu, D.; Gjessing, E.T. Water quality in the Tibetan Plateau: Metal contents of four selected rivers. Environ. Pollut. 2008, 156, 270–277. [Google Scholar] [CrossRef]
  27. Chen, Z.; Shikui, D.; Shiliang, L.; Nannan, A.; Isange, S.; Haidi, Z.; Qi, L.; Xiaoyu, W. Preliminary study on the effect of cascade dams on organic matter sources of sediments in the middle Lancang–Mekong River. J. Soils. Sediment. 2018, 18, 297–308. [Google Scholar]
  28. Luo, X. Research on the Industry Analysis and Development Plan of the Cold Chain Logistics Market in Changdu, Tibet; University of Electronic Science and Technology of China: Chengdu, China, 2020. [Google Scholar]
  29. Zhao, L.; Gong, D.; Zhao, W.; Lin, L.; Yang, W.; Guo, W.; Tang, X.; Li, Q. Spatial-temporal distribution characteristics and health risk assessment of heavy metals in surface water of the Three Gorges Reservoir, China. Sci. Total Environ. 2020, 704, 134883. [Google Scholar] [CrossRef]
  30. Li, L.; Chao, L.; Wen, J.Y.; Liang, Y.Z.; Min, L.; Qing, Y.L.; John, C.C. Spatial variations and periodic changes in heavy metals in surface water and sediments of the Three Gorges Reservoir, China. Chemosphere 2020, 240, 124837. [Google Scholar]
  31. Yang, Z.; Xia, X.; Wen, Y.; Ji, J.; Wang, D.; Hou, Q.; Yu, T. Dissolved and particulate partitioning of trace elements and their spatial–temporal distribution in the Changjiang River. J. Geochem. Explor. 2014, 145, 114–123. [Google Scholar] [CrossRef]
  32. Gaillardet, J.; Viers, J.; Dupré, B. 7.7-Trace Elements in River Waters. Treatise Geochem. 2014, 181, 195–235. [Google Scholar]
  33. Jie, L.; Kunli, L. Elements in surface and well water from the central North China Plain: Enrichment patterns, origins, and health risk assessmen. Environ. Pollut. 2020, 258, 113725. [Google Scholar]
  34. USEPA. Risk Assessment Guidance for Superfund Volume I: Human Health Evaluation Manual (Part E, Supplemental Guidance for Dermal Risk Assessment) Final; Office of Superfund Remediation and Technology Innovation U.S. Environmental Protection Agency: Washington, DC, USA, 2004.
  35. Giri, S.; Singh, A.K. Risk assessment, statistical source identification and seasonal fluctuation of dissolved metals in the Subarnkha River, India. J. Hazard. Mater. 2014, 265, 305–314. [Google Scholar] [CrossRef]
  36. Gao, B.; Gao, L.; Gao, J.; Xu, D.; Wang, Q.; Sun, K. Simultaneous evaluations of occurrence and probabilistic human health risk associated with trace elements in typical drinking water sources from major river basins in China. Sci. Total Environ. 2019, 666, 139–146. [Google Scholar] [CrossRef]
  37. USEPA. National Recommended Water Quality Criteria-Aquatic Life Criteria Table; Office of Water Office of Science and Technology: Washington DC, USA, 2014.
  38. Wang, J.; Liu, G.; Liu, H.; Lam, P. Multivariate statistical evaluation of dissolved trace elements and a water quality assessment in the middle reaches of Huaihe River, Anhui, China. Sci. Total Environ. 2017, 583, 421–431. [Google Scholar] [CrossRef]
  39. Xiao, J.; Wang, L.; Deng, L.; Jin, Z.D. Characteristics, sources, water quality and health risk assessment of trace elements in river water and well water in the Chinese Loess Plateau. Sci. Total Environ. 2019, 650, 2004–2012. [Google Scholar] [CrossRef]
  40. China Environmental Science Press. Chinese Soil Element Background Value; China Environmental Science Press: Beijing, China, 1990. [Google Scholar]
  41. La, B.; Bu, D.; Tan, X.; Chen, J.; Zhang, Q. Concentration and risk assessment of metal elements in Niyang river. Environ. Monit. Manag. Technol. 2017, 29, 33–36. [Google Scholar]
  42. Qin, H.; Gao, B.; Huang, B.; Zhang, S.; Dong, L.; Sun, Z. Distribution Characteristics and Pollution Risk Assessment of Trace Elements in River Water of Lhasa River Basin. Nonferrous Met. 2020, 10, 79–86. [Google Scholar]
  43. Wang, M. Study on the Supergene Enrichment and Sources of Arsenic in the Senge Zangbo Drainages and Yarlung Zangbo in Tibet; The State Key Laboratory of Environmental Geochemistry, Institute of Geochemistry, Chinese Academy of Sciences: Beijing, China, 2010. [Google Scholar]
  44. Kumar, S.; Islam, A.R.M.T.; Hasanuzzaman, M.; Roquia, S.; Khan, R.; Islam, M.S.; Rahman, M.S.; Pal, S.C.; Ali, M.M.; Gustave, W.; et al. Potentially toxic elemental contamination in Wainivesi River, Fiji impacted by gold-mining activities using chemometric tools and SOM analysis. Environ. Sci. Pollut. 2022. Available online: https://www.researchgate.net/publication/358198853_Potentially_toxic_elemental_contamination_in_Wainivesi_River_Fiji_impacted_by_gold-mining_activities_using_chemometric_tools_and_SOM_analysis (accessed on 4 March 2022). [CrossRef]
  45. Kumar, S.; Islam, A.R.M.T.; Hasanuzzaman, M.; Roquia, S.; Khan, R.; Islam, M.S. Preliminary assessment of heavy metals in surface water and sediment in Nakuvadra-Rakiraki River, Fiji using indexical and chemometric approaches. J. Environ. Manag. 2021, 298, 113517. [Google Scholar] [CrossRef]
  46. Hua, Z.; Wang, Y. Advance on pollutant release from river and lake sediments under hydrodynamic actions. J. Hohai Univ. 2018, 46, 95–105. [Google Scholar]
  47. Zhu, H.W.; Wang, D.Z.; Fan, J.Y.; Zhong, B.C. Physical processes and influencing factors of contaminants release due to resuspended sediments in water environment. Sci. Sin. Chim. 2015, 45, 18–28. [Google Scholar]
  48. Hahn, J.; Opp, C.; Evgrafova, A.; Groll, M.; Zitzer, N.; Laufen, B.R. Impacts of dam draining on the mobility of heavy metals and arsenic in water and basin bottom sediments of three studied dams in Germany. Sci. Total Environ. 2018, 640–641, 1072–1081. [Google Scholar] [CrossRef] [PubMed]
  49. Palanques, A.; Grimalt, J.; Belzunces, M.; Estrada, F.; Puig, P.; Guillen, J. Massive accumulation of highly polluted sedimentary deposits by river damming. Sci. Total Environ. 2014, 497–498, 369–381. [Google Scholar] [CrossRef]
  50. Varol, M. Dissolved heavy metal concentrations of the Kralkz, Dicle and Batman dam reservoirs in the Tigris River basin, Turkey. Chemosphere 2013, 93, 954–962. [Google Scholar] [CrossRef]
  51. Zhong, H.P.; Liu, H.; Geng, L.H. Cumulative effects of Lancang River Basin cascade hydropower development on ecology and environment. J. Hydraul. Eng. 2007, S1, 577–581. [Google Scholar]
Figure 1. Sampling sites in the study area ((a): Map of China; (b): The study area.).
Figure 1. Sampling sites in the study area ((a): Map of China; (b): The study area.).
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Figure 2. Enrichment of trace elements in water in different regions.
Figure 2. Enrichment of trace elements in water in different regions.
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Figure 3. Temporal and spatial distribution of trace elements in upper Lancang River.
Figure 3. Temporal and spatial distribution of trace elements in upper Lancang River.
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Figure 4. Vertical distribution of physicochemical properties in the water column of the Guoduo reservoir.
Figure 4. Vertical distribution of physicochemical properties in the water column of the Guoduo reservoir.
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Figure 5. Health risks of trace elements in different regions in upper Lancang River.
Figure 5. Health risks of trace elements in different regions in upper Lancang River.
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Table 1. Basic information table of sampling points.
Table 1. Basic information table of sampling points.
NumberSampling SitesLongitudeLatitudeMain Stream or Tributary
L01The tail of reservoir97°05′20.30″31°38′54.17″Main stream
L0211 km in front of the dam97°06′49.13″31°35′25.11″Main stream
L039 km in front of the dam97°07′4.33″31°35′19.17″Main stream
L045 km in front of the dam97°09′07.68″31°33′14.07″Main stream
L053 km in front of the dam97°09′41.55″31°33′01.76″Main stream
L060.3 km in front of the dam97°11′18.84″31°32′03.85″Main stream
L071 km under the dam97°07′40.69″31°34′56.02″Main stream
L0850 km under the dam97°10′58.00″31°10′3.00″Main stream
Z01The estuary of Angqu97°09′09.38″31°09′00.33″Tributary
L091 km downstream of Lancang river97°10′37.7″31°07′58.4″Main stream
L1040 km downstream of Lancang river97°21′34.8″31°55′50.0″Main stream
Table 2. Statistics of disclosure parameters.
Table 2. Statistics of disclosure parameters.
SubjectCwIRABSGIEFEDSAKpETBWAT
Adults2 aSee Table 3350 b70 b18,000 bSee Table 30.58 a65 a25,550 b
Children0.64 aSee Table 3350 b6 b6600 bSee Table 31 a20 a219 b
a Gao et al. [36]; b US EPA [37].
Table 3. RfDingestion, RfDdermal, ABSg, and Kp values of trace elements.
Table 3. RfDingestion, RfDdermal, ABSg, and Kp values of trace elements.
ElementAsCuZnPbCrMn
RfDingestion0.3 a40 c300 a1.4 c3 c24 c
RfDdermal0.285 a8 c60 a0.42 c0.075 c0.96 c
ABSGI95% b57% b20% d11.7% d3.8% b6% b
Kp0.001 b0.001 b0.0006 b0.0001 b0.003 b0.001 b
RfDingestion: oral reference dose (μg/kg/day), RfDdermal: the reference dose of the dermal absorption (μg/kg/day). a Gao et al. [36]; b US EPA [37]; c Wang et al. [38]; d Xiao et al. [39].
Table 4. Trace elements in rivers.
Table 4. Trace elements in rivers.
RiverAs (μg/L)Pb (μg/L)Fe (μg/L)Mn (μg/L)Cr (μg/L)Cu (μg/L)Zn (μg/L)Literature
MeanRangeMeanRangeMeanRangeMeanRangeMeanRangeMeanRangeMeanRange
This study7.281.00–14.12.65ND-10.0153.126.90–836.310.840.94–39.372.27ND-5.996.25ND-17.189.87ND-39.81/
Niyang River, Tibet0.10/1.160.012–5.18360.0160.0–600.027.650.02–4001.750.34–3.287.110.06–34.236.340.15–187[41]
Lhasa River, Tibet2.280.65–4.27//11.83ND-111.04.05ND-21.7//3.950.12–14.004.320.51–15.80[42]
Sengzangbo River, Tibet58.402.4–252.00.090.05–0.2214.000.16–98.13.632.18–14.7//2.580.36–4.981.250.75–4.01[43]
Yarlung Tsangpo, Tibet10.801.97–83.20.060.03–0.318.300.46–82.282.370.65–19.2//1.690.77–3.300.970.41–2.10[43]
Shiquan River, Tibet68.003.10–150////////////[43]
Xiangquan River, Tibet5.994.91–7.06////////////[43]
Naqu, Tibet5.895.87–5.91////////////[43]
The downstream of Lancang river, Tibet//11.828.43–15.210070–13013.312.5–14.10.390.28–0.501.530.86–2.21.880.83–2.93[26]
Six major river basins, Bangladesh6.531.3–3212.412.9–312476215–21,800233.815.3–117027.72.1–86//53.2410–190[11]
Wainivesi River, Bangladesh,//190153–2041623570–4260455–9610455–12246.810–10718321–753[44]
Nakuvadra-Rakiraki River, Ra Province//12.45.11–21.319857.1–444358168–53113363–18122.45.2–43.746.19.02–99.7[45]
Average of the world’s rivers0.620.07966340.701.445.34[32]
Class I of surface water5010300100/1050Water-quality standards for surface water in China
Note: “/” means no detection, and “ND” means detection limit in the table.
Table 5. Field parameters and trace element concentrations in surface waters from the upper Lancang River.
Table 5. Field parameters and trace element concentrations in surface waters from the upper Lancang River.
Sampling TimeCategoryT
(°C)
pHDO
(mg/L)
EC
(µS/cm)
As
(µg/L)
Fe
(µg/L)
Mn
(µg/L)
Pb
(µg/L)
Cr
(µg/L)
Cu
(µg/L)
Zn
(µg/L)
Wet season
(October 2018)
mean5.718.219.323575.49207.710.293.110.580.868.80
min4.458.168.862261.0026.900.94NDNDNDND
max6.838.3610.2438514.06836.339.3710.005.292.3839.81
Dry season (December 2018)mean0.378.226.906049.0698.4911.392.183.9611.6410.93
min0.108.136.524887.6564.622.601.95ND9.988.20
max1.008.317.2574312.70179.319.092.605.9917.1813.03
Note: “ND” means detection limit in the table.
Table 6. Health-evaluation index of trace elements in the main stream of Lancang River during the wet season.
Table 6. Health-evaluation index of trace elements in the main stream of Lancang River during the wet season.
ElementsReservoir TailReservoir AreaUnder the DamUrban Area
HQingestionHQdermalHIHQingestionHQdermalHIHQingestionHQdermalHIHQingestionHQdermalHI
AdultChildAdultChildAdultChildAdultChildAdultChildAdultChildAdultChildAdultChildAdultChildAdultChildAdultChildAdultChild
As1.05271.09480.00580.01191.05851.10670.29170.30340.00160.00330.29330.30670.22010.22900.00120.00250.22140.23141.22551.27450.00670.01381.23231.2884
Mn0.04840.05030.00630.01300.05470.06330.00830.00860.00110.00220.00940.01090.00470.00490.00060.00130.00530.00620.01350.01410.00180.00360.01530.0177
Pb0.05610.05840.00010.00020.05620.05860.07730.08040.00010.00030.07740.08070.09010.09370.00020.00030.09020.09400.01630.01700.00000.00010.01640.0171
Cr0.05200.05410.03260.06690.08460.12100.00050.00060.00030.00070.00090.00130.00050.00060.00030.00070.00090.00130.00050.00060.00030.00070.00090.0013
Cd0.00330.00340.00030.00070.00360.00410.00720.00750.00080.00150.00790.00900.00650.00670.00070.00140.00710.00810.00150.00150.00020.00030.00160.0019
Cu0.00110.00110.00000.00010.00110.00120.00070.00070.00000.00000.00070.00080.00080.00080.00000.00000.00080.00090.00000.00000.00000.00000.00000.0000
Zn0.00050.00050.00000.00000.00050.00060.00160.00160.00000.00010.00160.00170.00010.00010.00000.00000.00010.00010.00010.00010.00000.00000.00010.0001
Table 7. Health-evaluation index of trace elements in the main stream of Lancang River during the dry season.
Table 7. Health-evaluation index of trace elements in the main stream of Lancang River during the dry season.
ElementsReservoir TailReservoir AreaUnder the DamUrban Area
HQingestionHQdermalHIHQingestionHQdermalHIHQingestionHQdermalHIHQingestionHQdermalHI
AdultChildAdultChildAdultChildAdultChildAdultChildAdultChildAdultChildAdultChildAdultChildAdultChildAdultChildAdultChild
As0.79620.82810.00440.00900.80060.83710.77730.80840.00430.00880.78150.81710.92800.96510.00510.01050.93310.97561.18831.23580.00650.01341.19481.2492
Mn0.01040.01080.00140.00280.01180.01360.01160.01210.00150.00310.01310.01520.01450.01510.00190.00390.01640.01890.02130.02220.00280.00570.02410.0279
Pb0.04430.04610.00010.00020.04440.04620.04360.04540.00010.00020.04370.04550.04900.05100.00010.00020.04910.05110.04970.05170.00010.00020.04980.0518
Cr0.04640.04820.02900.05970.07540.10790.04980.05180.03120.06410.08100.11600.04630.04810.02900.05960.07530.10770.00050.00060.00030.00070.00090.0013
Cd0.00150.00150.00020.00030.00160.00190.00150.00150.00020.00030.00160.00190.00150.00150.00020.00030.00160.00190.00150.00150.00020.00030.00160.0019
Cu0.00820.00850.00020.00040.00840.00900.00820.00850.00020.00040.00840.00900.00830.00870.00020.00040.00860.00910.01000.01040.00030.00050.01030.0110
Zn0.00120.00120.00000.00000.00120.00130.00110.00110.00000.00000.00110.00120.00130.00130.00000.00000.00130.00130.00080.00090.00000.00000.00090.0009
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Liu, M.; Zhang, Z.; Lin, L.; Zhao, L.; Dong, L.; Jin, H.; Zou, J.; Li, R.; He, Y. The Content Level, Spatial and Temporal Distribution Characteristics, and Health-Risk Assessment of Trace Elements in Upper Lancang River (Changdu Section). Water 2022, 14, 1115. https://doi.org/10.3390/w14071115

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Liu M, Zhang Z, Lin L, Zhao L, Dong L, Jin H, Zou J, Li R, He Y. The Content Level, Spatial and Temporal Distribution Characteristics, and Health-Risk Assessment of Trace Elements in Upper Lancang River (Changdu Section). Water. 2022; 14(7):1115. https://doi.org/10.3390/w14071115

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Liu, Min, Zhongwei Zhang, Li Lin, Liangyuan Zhao, Lei Dong, Haiyang Jin, Jingyi Zou, Rui Li, and Yunjiao He. 2022. "The Content Level, Spatial and Temporal Distribution Characteristics, and Health-Risk Assessment of Trace Elements in Upper Lancang River (Changdu Section)" Water 14, no. 7: 1115. https://doi.org/10.3390/w14071115

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