Home Geochemical sedimentary records of eutrophication and environmental change in Chaohu Lake, East China
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Geochemical sedimentary records of eutrophication and environmental change in Chaohu Lake, East China

  • Shuguang Lu , Li Wu EMAIL logo , Houchun Guan , Xiaosi Hu , Baodong Yang , Wenjing Luo , Ziyi Xu , Yang Zhang , Boshi Liu and Wentian Cai
Published/Copyright: July 11, 2024
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Open Geosciences
From the journal Open Geosciences Volume 16 Issue 1

Abstract

Chaohu Lake is a representative lake in China that suffers from severe eutrophication and algal blooms. Understanding the changes in the lake’s eutrophic condition over time is essential for its restoration and management under the background of global changes and regional sustainability. In this context, the compositions of carbon and nitrogen isotopes (δ 13Corg and δ 15N, respectively), total organic carbon (TOC), total nitrogen (TN), and carbon–nitrogen ratio (C/N) were analysed to depict the history of eutrophic state of Chaohu Lake, and its relationship with environmental changes. The result show that before the 1950s, the primary productivity of the lake was low. During the period from the 1950s to the 1970s, primary productivity increased substantially due to eutrophication. From the 1970s to the present, as a result of the construction of the Chaohu Floodgate Station, water replacement in the semi-closed Chaohu Lake gradually slowed and nutrients began to accumulate more rapidly. These conditions led to enhanced lake productivity and rapid eutrophication, mainly caused by intensified human activities and increased exogenous inputs. Our findings suggest that the geochemical records (δ 13Corg, δ 15N, TOC, TN, and C/N ratios) in sediment for Chaohu Lake are capable of recording important shifts in the temporal evolution of lake-water trophic state.

Keywords: lake sediment; geochemistry; stable isotope; eutrophication; Chaohu Lake

1 Introduction

Environmental issues have received increasing attention in terms of their impact on human society [1,2,3,4,5]; especially, eutrophication and harmful algal blooms have become serious water quality problems worldwide in recent years [6,7,8,9,10,11,12]. Chaohu Lake is the fifth largest freshwater lake in China, and it is an important freshwater resource and ecological wetland in the middle and lower reaches of the Yangtze River [13,14]. Its strategic location and unique ecosystem make it vital for the region’s water supply, agriculture, and as a part of the South-North Water Transfer Project. However, the eutrophication of Chaohu Lake has become increasingly serious as the cyanobacterial blooms seriously, which are closely related to the eutrophication of this lake and its environmental evolution, threatening the drinking water safety and ecosystem health [13,14]. Therefore, understanding the changes in the lake’s eutrophic condition over time is essential for its restoration and management [15].

At present, some studies have focused on the history of eutrophication in Chaohu Lake, but the specific views on this issue are quite different. For example, Wang et al. [16] observed initial signs of eutrophication in Chaohu Lake as early as the late 1950s. In contrast, research by Chen et al. [17] showed that the lake did not begin to transition to eutrophication until the end of 1970s. Zan et al. [18], however, pinpointed the onset of Chaohu Lake’s eutrophication to the 1960s, noting that it intensified significantly around the 1980s due to rapid population growth, urbanisation, and the expansion of industrial and agricultural activities. Furthermore, Chen et al. [19] indicated significant human impacts on Chaohu Lake since the 1960s, leading to increased organic matter burial and algal productivity. This discrepancy underscores the need for a comprehensive investigation into the temporal patterns and underlying causes of eutrophication in Chaohu Lake to devise effective countermeasures [20]. A long-term description depicting the historical variation of Chaohu Lake’s eutrophic state and the status of environmental disturbance is lacking for the past decades.

Using geochemistry to study environmental problems has been extensively carried out [1,2,6,7]. Following this method, the past eutrophic state would be presented clearly. Changes in total organic carbon (TOC), total nitrogen (TN), and organic carbon and nitrogen isotopes (δ 13Corg and δ 15N, respectively) in sediments can be used to determine the palaeoenvironmental evolution history at the time of sediment deposition [21,22,23,24]. Isotope fractionation occurs because of the different carbon sources utilised by various plants during photosynthesis [25,26]. The composition of δ 13Corg in lake sediments has proven to be an effective proxy for the source of organic matter in the lake, the structure of the lacustrine ecosystem, and changes in primary productivity [23,24,27,28]. Wu et al. [29] used the TOC, C/N, and δ 13C of the core taken from Cuoe Lake to reconstruct the climate changes of the central Tibetan Plateau since 10.5–1.6 ka BP, and they pointed out that high TOC, high δ 13C corresponds to warm and humid climatic conditions. Lücke et al. [30] used δ 13Corg to reconstruct the productivity changes since 14.2 ka BP of Lake Holzmaar in Germany and believed that favourable climatic conditions can improve lake palaeoproductivity, resulting in higher δ 13C of sediments. Moreover, δ 15N is an effective method for identifying the nitrogen source in lake sediments [22,24], and together with the carbon–nitrogen ratio (C/N), it is widely used to indicate the contribution of organic matter from different sources in lake sediments [31,32]. McFadden and Mullins [33] evaluated the palaeoproductivity of Ontario Lake by combining C/N, carbon, and nitrogen isotopes and concluded that high δ 15N reflects high lake productivity. However, other factors, such as nitrification/denitrification, terrestrial input, and cyanobacterial nitrogen fixation, may also affect the nitrogen isotope composition of sediments.

Therefore, sediment cores were collected from the western part of Chaohu Lake, and sedimentary geochemical indicators (δ 13Corg, δ 15N, TOC, TN, and C/N) were selected as proxies to explore the sources of organic matter and nitrogen at different depths (time periods) of the lake sediment. C/N ratios and nitrogen isotopes were then compared to analyse the eutrophication and environmental evolution of Chaohu Lake. Our study aimed to explore the temporal evolution of Chaohu Lake’s eutrophic state, and to study the interaction of environmental factors and eutrophication, so as to guide future restoration and management. The results of this study would provide a useful reference and scientific basis for the ecological protection of lakes from the perspective of global change and regional sustainable socio-economic development.

2 Materials and methods

2.1 Study area

Chaohu Lake, located in the central part of the Anhui Province and the lower reaches of the Yangtze River (Figure 1), is an important water source for Hefei and is one of the three most heavily eutrophic lakes in China [17]. The lake covers an area of 760 km2, with a length of 54.5 km from east to west, a width of 21.0 km from north to south, and an average depth of 2.69 m [34–37]. The limnology and climate information of Chaohu Lake is shown in Table 1. With the influence of strong wind-wave disturbance and high sediment input by rivers into Chaohu Lake, the suspended matter concentration of the lake water is high, causing low but sufficient transparency to support cyanobacteria growth in the lake. The basal sediments belong to the Xiashu loess of the late Pleistocene, with upper modern sediments represented from a depth of 50–100 cm to the lake floor [22]. The development of watershed agriculture and urbanisation has exacerbated eutrophication in Chaohu Lake over the last 100 years. The lake residence period increased considerably after the construction of the Chaohu Floodgate Station at the southwest exit of Chaohu City in 1962 [38]. A mass of contaminants from the catchment basin enters the lake and pollutes the lake water at an alarming rate [34,39,40]. Cyanobacterial blooms are a serious environmental problem. As a result, the government has strengthened the pollution governance of Chaohu Lake, and a total of 167 water pollution control projects have been implemented, with a total investment of approximately 1,665,561,205 US$ during the 12th Five-Year Plan.

Figure 1 Location of Chaohu Lake (a) and (b) and position of the sampling site (CH) (c).
Figure 1

Location of Chaohu Lake (a) and (b) and position of the sampling site (CH) (c).

Table 1

Limnology and climate parameters (multi-year average) of the Chaohu Lake

Water depth (m) Water level amsl (m) Water temperature (℃) Eh (mV) pH Transparency (m) Evaporation (mm) Precipitation (mm)
Maximum 3.77 9.81 29.30 235.40 9.41 2.20 1293.9 1881.40
Minimum 1.16 7.35 4.00 16.00 7.03 0.05 915.9 516.70
Mean 2.69 8.37 19.80 144.10 8.69 0.49 1013.5 980.00

2.2 Sampling and analytical methods

The western part of the lake was chosen as the sampling site (31°33′44.6″N, 117°23′39.4″E, Figure 1) based on field investigations, where a high sedimentation rate prevails. An 85 cm sedimentary core was obtained by gravity with a Beeker-type sediment sampler (Eijkelkamp, Netherlands) from a platform anchored in the middle of western Chaohu Lake with an average water depth of 3 m. The core was transferred quickly to airtight containers with PVC pipes to limit sample oxidisation and was kept under cooling in the laboratory. Pictures of the collected cores were taken, and the lithology was described. The samples were then sliced at 1 cm intervals. The whole core was mainly composed of green-gray silt, of which the depth from 0 to 25 cm was mainly green-gray fine silt, and the depth from 25 to 85 cm was green-gray medium silt with some fine silt layers.

Geochemical analysis of carbon and nitrogen in the samples was conducted at the State Key Laboratory of Lake Science and Environment, Nanjing Institute of Geography and Limnology, Chinese Academy of Sciences. Initially, the samples were dissolved in diluted 5% hydrochloric acid several times and then kept in a low-temperature water bath for at least 3 h to completely remove the remaining carbonate. Subsequently, the samples were washed with distilled water and ground into fine powders after drying at a low temperature. Subsequently, the values of TOC and TN were measured using a Leeman CE440 elemental analyser (Leeman Company) with an error of less than 0.1% using 10 mg samples. Isotopic ratios were measured using a continuous flow system that comprised an elemental analyser directly attached to a Finnigan Delta plus isotope mass spectrometer, and the accuracy was higher than 0.2‰ [41,42]. The values of δ 13Corg and δ 15N are expressed in standard delta notation relative to Vienna Pee Dee Belemnite (VPDB) and atmospheric nitrogen (AIR) standards, respectively.

2.3 Chronology

The CH lake core collected in April 2006 was located near the AC2 core (31°33′31″N, 117°24′17″E, a study conducted by East China Normal University in 2003) [43,44], which was dated using gamma spectrometry 137Cs measurements. The pretreatment method involved selecting the ground samples at a certain interval, weighing approximately 3 g of each sample, placing it into a cylindrical sample tube with a diameter of 1 cm and a height of 4 cm, and using it after 3 weeks of wax sealing γ-ray radiometer for measurement. The experimental instrument used was the GWL-120210-S high-purity Ge well-type photon detection system produced by EG & GORTEC, with an energy resolution of 1.91 kev. A fully enclosed shielded room guaranteed a low environmental background value. The maximum value of 137Cs in the AC2 sample at a depth of 13 cm was assigned to nuclear weapons tests in 1963. This result shows that the sedimentation rate of the AC2 core is 0.33 cm y−1. Tu et al. [34] used 210Pb and the water-sediment balance method to analyse the sediment deposition rate in Chaohu Lake from 1980 to 1986 and found the same average sedimentation rate of 0.33 cm year−1. The average sedimentation rate of Chaohu Lake obtained by Du et al. [45] from two cores is also recorded as 0.32 cm year−1. Using the sedimentation rate of the AC2 core as a reference, we calculated that the CH core represents sediment deposition since 1750 AD by assuming a constant sedimentation rate (Figure 2).

Figure 2 Changes in carbon and nitrogen geochemical proxies for core CH in Chaohu Lake.
Figure 2

Changes in carbon and nitrogen geochemical proxies for core CH in Chaohu Lake.

3 Results

The geochemical results are listed in Table 2, and the trends of δ 15N, δ 13Corg, TOC, TN, and C/N values with depth are shown in Figure 2, with a peak at 83 cm and δ 15N value of 4.01‰. The trend of δ 15N tends to increase gradually below 77 cm of the core. The variation of δ 15N values at 19–75 cm depth is between 3.33 and 4.78‰, with an average value of around 4‰. The δ 15N value reaches 3.14‰ at 75 cm. From bottom to top, the δ 15N values showed large variations between 1 and 19 cm, decreasing between 15 and 19 cm, increasing rapidly between 5 and 15 cm, and then decreasing again at the core top. δ 13Corg is relatively stable below 53 cm, and its value fluctuates around −22.50‰ (VPDB), with little change. The δ 13Corg value of the 1–53 cm cores generally showed a downward trend from bottom to top, and the δ 13Corg value of the 0–9 cm part decreased rapidly. The TOC value shows a relatively stable trend between 29 and 85 cm, and a peak appears at 71 cm. The TOC value of the 1–29 cm samples showed a gradual upward trend from bottom to top, increasing at three depth intervals of 1–11, 13–19, and 23–29 cm, and finally reaching a value of 0.97%. The TN was relatively stable below 27 cm, varying between 0.04 and 0.06%. The TN content increased continuously from 1 to 27 cm and reached 0.16% at 1 cm. The C/N ratio changed drastically below 69 cm. The C/N ratio is in the range of 5–10 between 29 and 69 cm and remains stable after a small sharp variation between 1 and 29 cm.

Table 2

Analytical results of carbon and nitrogen geochemical proxies for CH core

C/N TN (%) TOC (%) δ 13Corg (‰) δ 15N (‰)
Maximum 26.72 0.16 1.12 −22.22 5.63
Minimum 3.96 0.04 0.26 −24.85 2.13
Mean 8.59 0.06 0.49 −23.07 3.90

4 Discussion

4.1 Diagenesis

Changes in organic nitrogen content in Chaohu CH cores are mainly affected by two factors: the provenance and initial productivity factors of the lake and the effect of early diagenesis [26]. Early diagenesis can lower C/N and δ 13Corg values during the transfer and accumulation of organic matter [46,47]. Studies have also shown that N is preferentially mineralised during early diagenesis, and selective degradation of organic matter leads to changes in the C/N value [47,48]. The degradation of algal organic matter reduced the content of TN and followed the exponential decay mode, which further led to an increase in the C/N value [25,47]. According to our analytical data, there is an obvious increase in the C/N value between 77 and 68 cm, and the conditions for the increase in the C/N value described previously exist. However, from the comparative analysis of TOC, TN, and δ 13Corg, the reason for the increase in C/N value is mainly due to the increase in TOC content and the TN content, which did not show a significant exponential decrease. In addition, the variation in δ 13Corg is steady from 77 to 71 cm, where C/N ratios and TOC values peak. The aforementioned analysis shows that early diagenesis did not affect the TOC and TN contents and C/N values in the CH core of Chaohu Lake. The data obtained from the experiment can be used to indicate the source of organic matter and the primary productivity of the lake. It can also be used to reflect the eutrophication and environmental evolution of Chaohu Lake.

4.2 Sources of organic matter in lake sediments

There are two sources of organic matter in lake sediments: exogenous terrestrial and endogenous aquatic plants. The content of organic matter from different sources is closely related to the conditions of the material source, transportation, and preservation [49]. The exogenous organic matter in all lake sediments consisted almost entirely of terrestrial plants. Terrestrial plants are mainly divided into three major types based on different pathways of photosynthesis: C3 plants, C4 plants, and crassulacean acid metabolism plants. The ranges of δ 13Corg values of different plants are shown in Table 3 [50–53]. Endogenous organic matter in lake sediments primarily originates from the remains of dead plants and animals from lakes, together with terrestrial detritus through their deposition. Therefore, the composition and variety of δ 13Corg values of aquatic plants in lacustrine sediments are complex and wide (Table 3). Based on their different distribution locations, aquatic plants can be classified into three categories: submerged plants, emerged plants, and phytoplankton. Submerged plants have higher δ 13Corg values because they absorb more CO2 gases emitted by dissolved bicarbonate than terrestrial plants. Under normal conditions, submerged plants have δ 13Corg values of −12 to −20‰ with an average value of −15‰ [54,55]. As for emerged plants, when absorbing atmospheric CO2, they have a δ 13Corg value of −24 to −30‰, with an average value of −27‰, similar to C3 plants [50]. Of course, emerged plants have higher δ 13Corg values of −12‰ to −24‰ if they absorb more CO2 emitted from HCO 3 − [56]. The range of δ 13Corg values of phytoplankton is between −18 and 22‰ [26].

Table 3

Distribution range of δ 13Corg values of various plants

Type C3 C4 CAM Emerged plant Submerged plant Phytoplankton
Value range (‰) −37 to −24 −19 to −9 −30 to −10 −30 to −24 −20 to −12 −22 to −18

Using the C/N ratios in lake sediments, we can roughly determine whether the organic matter in the lake sediments is mainly of endogenic or exogenic origin. Terrestrial vascular plants mainly contain cellulose with a low protein content, and the opposite result has been found in diatoms [57]. Therefore, organic matter sources can be analysed according to C/N ratios. The C/N ratios of organic matter in diatoms were between three and eight, terrestrial higher plants were about 20 or higher, and soil organic matter was between 10 and 13 [58–60]. The C/N value of the organic matter in lake sediments is greater than eight, which is generally considered to be affected by the interaction between terrestrial and algal organic matter [57,61].

Based on the aforementioned analysis, it can be concluded that the endogenic organic matter developed in Chaohu Lake was the primary source of sedimentary organic matter in the CH core (Figure 3) [52,62–64]. C/N values higher than 13 in the depth interval of 77–69 cm, corresponding to the time interval of 1739–1767 AD, indicated the contribution of terrestrial organic matter to the lake. However, for most of the depositional period covered by core CH, the organic matter generated within the lake was the main source of sedimentary organic matter. Soil and water loss occurred at a certain time owing to extreme flood events and other reasons. As a result, a large amount of terrestrial organic matter entered the lake, decreasing δ 15N and δ 13Corg and increasing C/N ratios. According to the records of the Brief Chorography of Chaohu Lake [65], there were 55 flood disaster events during the 296 years of the Qing Dynasty (1636–1912 AD), with an average value of once per 5.4 years. Before 1788 AD (core depth below 63 cm), δ 13Corg values and other indicators of Chaohu Lake underwent dramatic changes, reflecting more exogenous material in the lake. Decreasing in the top ∼8 cm (1980 AD) δ 13Corg values, together with low C/N values (<10), suggests an increased contribution of algal organic matter (Figure 2).

Figure 3 Correlation between TOC and TN (a): distinctive source combination of C/N ratios and δ 13Corg values (b) in the CH core sediments of Chaohu Lake.
Figure 3

Correlation between TOC and TN (a): distinctive source combination of C/N ratios and δ 13Corg values (b) in the CH core sediments of Chaohu Lake.

4.3 Sources of nitrogen and its significance in eutrophication

The δ 15N of sediments is affected by the isotopic composition of the assimilated nitrate source, food web dynamics, biological fractionation, and isotope fractionation during sediment diagenesis. Depending on the source of the nitrogen-containing substances, the δ 15N value changes can be used to reflect the source of nitrogen. Different sources have different δ 15N contents, and the δ 15N value of soil nitrogen ranges between 2 and 4‰. The δ 15N value of the synthetic fertiliser was between −4 and 4‰, whereas the sewage δ 15N value was between 10 and 20‰. The δ 15N value of atmospheric deposition NO 3 − is between 0.2 and 0.8‰ [66].

An indicative significance of δ 15N is observed in Figure 2 and Table 2; δ 15N values of the CH core below 19 cm depth (1942 AD) show no clear changes, with an average value of 3.8‰. This indicates that the nitrogen in the sediment at the centre of Chaohu Lake was mainly due to soil erosion before the 1950s. In the 3–19 cm depth interval (1949–1998 AD), the δ 15N values of the core changed considerably, with an average value of ∼4.45‰. There are also clear changes in other data, such as the rapid increase in the values of TN and TOC and the rapid decrease in δ 13Corg values, suggesting that the sediments are strongly influenced by exogenous factors, and the nitrogen values increased by exogenous inputs such as synthetic fertilisers. Moreover, the δ 15N values decreased with a mean value of 2.13‰ from 0 to 3 cm depth (1998–2005 AD).

4.4 Sedimentary records of environmental evolution

The first stage occurs below 63 cm depth and represents periods before the late 18th century according to the deposition rate. At this stage, sediments in Chaohu Lake were strongly affected by exogenous inputs, and all geochemical index data fluctuated greatly due to extreme flood events [37]. Furthermore, both TN and δ 15N values were relatively low during this period, indicating that the primary productivity of the lake was rather low.

The second stage occurred at a depth of 25–63 cm (from the 1780s to the 1920s). At this stage, the lake was less affected by exogenous factors with low productivity, as indicated by the relatively stable proxy profiles, implying a low anthropogenic impact on the lake during this stage. These two stages include the period from the mid-late Qing Dynasty to the founding of the Republic of China when the Chaohu Lake Basin had not yet entered the stage of urbanisation and industrialisation during this period [67]. Another piece of evidence for the low effects of human disturbance is that native vegetation remains in the basin. Natural grasslands occupy most areas around the lake, with conifers and broad-leaf trees as the main components [68].

The third stage was from 17 to 25 cm (from the 1920s to the 1950s), and the values of δ 15N, TN, and TOC increased in general. Combined with the analysis of nitrogen sources, the proxy data showed that the exogenous input and primary productivity of the lake began to increase, leading to the eutrophication of the lake. δ 13Corg and C/N showed an obvious upward increasing trend, indicating eutrophication of the lake by phytoplankton blooms. The increased eutrophication in the lake is a result of anthropogenic activities. Native vegetation in the Chaohu Lake Basin was also destroyed during this period. Vegetation has changed to plantations, secondary forests, and large areas of cultivated crops [69] when the main settlement points in the basin (such as Hefei City and Chao County, etc.) underwent urbanisation and industrialisation [59].

The fourth stage occurred at a depth of 3–17 cm (from the 1950s to the end of the 20th century). This is a period of rapid development, including regional urbanisation and industrialisation, after the reform and opening-up policy of China, during which human activity has increased its impact on the lake [70]. At this stage, the values of TOC, TN, and δ 15N increased rapidly, indicating that the productivity of the lake was greatly increased and eutrophication was further aggravated. Phytoplanktons are compelled to utilise and gather 15N, increasing δ 15N values and productivity. The large increase in δ 15N values in the 3–10 cm depth interval (from the 1970s to the 1990s) could be related to the (a) denitrification process at a suboxic interface in the water column, coupled with the release of fixed N from sediments, or (b) incomplete assimilation of nitrate and concomitant preferential 14N uptake under enhanced reactive N supply by riverine delivery. At the same time, the decrease of δ 13Corg shows that the cycle of C/N ratios was shifted by the construction of the Chaohu Floodgate Station in 1962 [65]. After the completion of Chaohu Floodgate Station, the water level of Chaohu Lake is stable at approximately 8 m year-round, and the lakeshore (20% of the lake area) has lost its basking condition [71]. There has been a massive decrease in aquatic plants with high winds and waves on the lake surface. This leads to the collapse of the lakeshore, ecological degradation, and reduction of self-purification of the water body. Meanwhile, the reduction in water exchange (88.24% reduction) and prolongation of the changing water cycle led to the retention of pollutants in the lake and a reduction in the environmental capacity of the water body [71]. All of these factors have contributed to the ecological imbalance and enhanced eutrophication of Chaohu Lake. Eutrophication further hastened the growth of diatoms as the decomposition of organic matter was enhanced and produced more CO2, which accounted for the decrease in δ 13Corg values [66].

The fifth stage was from a depth of 0–3 cm (from the end of the 20th century to the present). The values of TOC and TN increased considerably, and a significant declining trend was shown by the δ 15N values, indicating that Chaohu Lake remained at the eutrophic stage. Previous studies have found that the δ 15N of sediments is significantly negative when the lake evolves into a eutrophic stage [21]. Under eutrophic conditions, different phytoplankton species that utilised 15N were observed. The degree of eutrophication of the lake has intensified with the decomposition and denitrification of organic matter in the surface sediments [21,53].

5 Conclusions

  1. The TOC in lake sediments stemmed mainly from phytoplankton living on CO2 dissolved in water, and the C/N records reflect flood events over the last 200 years in the basin.

  2. The TN content in Chaohu Lake sediments was mainly affected by soil erosion and transport from the catchment before the 1950s, and subsequently by human activities, including the use of artificial nitrogen fertiliser and input of other pollutants from the lake’s drainage basin.

  3. Chaohu Lake was relatively stable before the 1950s when it was less affected by human activities. During the period from the 1950s to the 1970s, primary productivity increased substantially due to eutrophication. From the 1970s to the present, as a result of the construction of the Chaohu Floodgate Station, water replacement in the semi-closed Chaohu Lake gradually slowed and nutrients began to accumulate more rapidly. These conditions led to enhanced lake productivity and rapid eutrophication, which were intensified by human activities and increased exogenous inputs.

  4. Future research on Chaohu Lake should focus on the impact of human activities on lake eutrophication. Eutrophication control requires an understanding of the nutrient backgrounds of lakes. The reconstruction of the lake’s quasi-natural nutrient background by lake sediment and the process of increasing nutrient levels can provide targets for the management of eutrophic lakes at different stages. It is necessary to strengthen the research on the types and accumulation history of pollutants in lake sediments. This is helpful for correctly evaluating the changes in lake pollution sources and provides a scientific basis for lake pollution control.

Acknowledgements

The authors gratefully acknowledge anonymous reviewers for their thorough reading of this manuscript and for their insightful questions and constructive suggestions, which significantly improved the quality of this article.

  1. Funding information: This research was supported by the Key Project of the 14th Five-Year Plan of Anhui (Grant No. 2022BFAFZ01365), the National Natural Science Foundation of China (Grant No. 41771221), and the National Key Innovation Training Program for College Students (Grant No. 202310370039).

  2. Author contributions: LW and HG designed the study. LW, SL, HG, XH, BY, WL, and ZX performed the fieldwork. YZ, BL, and WC carried out the laboratory analysis. LW and SL prepared the manuscript with contributions from all co-authors. The authors applied the SDC approach reflecting the declining importance of their contribution for the sequence of authors.

  3. Conflict of interest: Authors state no conflict of interest.

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Received: 2024-01-05
Revised: 2024-04-15
Accepted: 2024-04-24
Published Online: 2024-07-11

© 2024 the author(s), published by De Gruyter

This work is licensed under the Creative Commons Attribution 4.0 International License.

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  140. Spatial-temporal and trend analysis of traffic accidents in AP Vojvodina (North Serbia)
  141. Exploring environmental awareness, knowledge, and safety: A comparative study among students in Montenegro and North Macedonia
  142. Determinants influencing tourists’ willingness to visit Türkiye – Impact of earthquake hazards on Serbian visitors’ preferences
  143. Application of remote sensing in monitoring land degradation: A case study of Stanari municipality (Bosnia and Herzegovina)
  144. Optimizing agricultural land use: A GIS-based assessment of suitability in the Sana River Basin, Bosnia and Herzegovina
  145. Assessing risk-prone areas in the Kratovska Reka catchment (North Macedonia) by integrating advanced geospatial analytics and flash flood potential index
  146. Analysis of the intensity of erosive processes and state of vegetation cover in the zone of influence of the Kolubara Mining Basin
  147. GIS-based spatial modeling of landslide susceptibility using BWM-LSI: A case study – city of Smederevo (Serbia)
  148. Geospatial modeling of wildfire susceptibility on a national scale in Montenegro: A comparative evaluation of F-AHP and FR methodologies
  149. Geosite assessment as the first step for the development of canyoning activities in North Montenegro
  150. Urban geoheritage and degradation risk assessment of the Sokograd fortress (Sokobanja, Eastern Serbia)
  151. Multi-hazard modeling of erosion and landslide susceptibility at the national scale in the example of North Macedonia
  152. Understanding seismic hazard resilience in Montenegro: A qualitative analysis of community preparedness and response capabilities
  153. Forest soil CO2 emission in Quercus robur level II monitoring site
  154. Characterization of glomalin proteins in soil: A potential indicator of erosion intensity
  155. Power of Terroir: Case study of Grašac at the Fruška Gora wine region (North Serbia)
  156. Special Issue: Geospatial and Environmental Dynamics - Part I
  157. Qualitative insights into cultural heritage protection in Serbia: Addressing legal and institutional gaps for disaster risk resilience
https://doi.org/10.1515/geo-2022-0649
Keywords for this article
lake sediment; geochemistry; stable isotope; eutrophication; Chaohu Lake
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  151. Multi-hazard modeling of erosion and landslide susceptibility at the national scale in the example of North Macedonia
  152. Understanding seismic hazard resilience in Montenegro: A qualitative analysis of community preparedness and response capabilities
  153. Forest soil CO2 emission in Quercus robur level II monitoring site
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  155. Power of Terroir: Case study of Grašac at the Fruška Gora wine region (North Serbia)
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