Hydrochemical Characteristics of Groundwater and Dominant Water–Rock Interactions in the Delingha Area, Qaidam Basin, Northwest China

Groundwater is undoubtedly important for water supplies and eco-environment protection, especially for arid and semi-arid regions. Analyzing the characteristics and evolution of groundwater is significant for the rational management of groundwater resources. This study investigated the hydrogeochemical characteristics and evolutions of groundwater in the Delingha area, northeast of the Qaidam Basin, northwest China, with a total of 123 water samples, including 105 unconfined groundwater samples, 12 confined groundwater samples, and 6 surface water samples. Hydrochemical results showed that the unconfined and confined groundwater presented diversity in ion concentration. Total Dissolved Solids (TDS) of the unconfined groundwater increased from 146.5 to 8954 mg/L along the groundwater flow direction. The groundwater hydrochemical types were HCO3-Ca·Mg and HCO3·SO4-Ca·Mg in the mountain front area, SO4·HCO3-Ca·Mg and SO4·Cl-Ca·Mg types in the alluvial-lacustrine plain, and Cl·SO4-Na and Cl-Na types in the lacustrine plain. The saturation index showed that parts of the groundwater samples were supersaturated with carbonate minerals (calcite and dolomite); however, all the samples were undersaturated with evaporite minerals (halite and gypsum). Groundwater chemical evolution is mainly controlled by evaporite and carbonate mineral dissolutions, aluminosilicates weathering, and cation exchange.


Introduction
Water shortage has been a critical issue in many parts of the world, especially in arid and semi-arid areas [1][2][3][4]. Qaidam Basin, which is located in Northwest China, is a typical arid area [5]. Because of the lack of surface-water and precipitation, groundwater has been the main water resource in this area. Sustainable management of groundwater has become a critical issue for this area. Understanding the hydrochemical characteristics of the local groundwater could provide guidance for sustainable groundwater development [6].
The hydrochemistry of groundwater is generally regulated by precipitation, geological structure, rock type, residence time, and geochemical processes along the groundwater flow paths [7,8]. Recent studies for the groundwater of Qaidam area have focused on the recharge source, circulation, hydrochemical characteristics, and hydrochemical evolution of the local groundwater [4,5]. For The geologic outcrops in this study area include sediments of Sinian, Carboniferous, Permian, and Trias up to Quaternary periods. The outcrops of bedrock are mainly distributed in the mountain area. The alluvial fan and lacustrine plain were comprised of the Quaternary deposits of coarse sand, fine sand and sandy clay, with the thickness ranging from 0 to 500 m ( Figure 2). Bedrock fissure groundwater occurring in sandstone and slates of the Triassic and Permian periods is widely distributed in the north and east of this study area. The carbonate fissure karst water occurring in phyllite and limestone of the Carboniferous period is mainly distributed in the south slope of Zongwulong Mountain and mainly receives the replenishment from atmospheric precipitation and snowmelt. Clastic rock fracture groundwater mainly occurs in the hilly area and alluvial-lacustrine plain, in where the lithology is composed of glutenite, sandstone, and mudstone interbeds. Loose sediment groundwater is the main water resource of this region, with a water table depth of 4-60 m.  The main rivers in the Delingha area are the Baying river and Baishui river ( Figure 1). The Baying river is the largest river in this area, originating from the Zongwulong Mountain and running through the entire Delingha city. After passing through the Delingha city, it leaks heavily into the aquifer and supplies the groundwater. Then, part of groundwater flows eastward and eventually

Sampling and Analysis Methods
A total of 123 water samples were collected from May to October 2016 in the Delingha region. Those samples (including 6 surface-water, 105 unconfined groundwater and 12 confined groundwater samples) were collected along the general groundwater flow direction, from Zongwulong Mountain to Hurleg Lake ( Figure 1). Samples of surface-water were collected from the Baying river, and samples of groundwater were collected from wells, boreholes and springs. The depths of those wells and boreholes of the unconfined aquifer are about 30-150 m. And the depths of boreholes of the confined aquifer, which is in the southern lacustrine plain, range from 100 to 500 m.
All the water samples were stored in portable bottles and then analyzed in the Laboratory of Groundwater Sciences and Engineering of the Institute of Hydrogeology and Environmental Geology, Chinese Academy of Geological Sciences. Major cations (K + , Na + , Ca 2+ , Mg 2+ ) were measured with ICP-OES, anions (Cl − , SO 4 2− ) were carried out by spectrophotometry (DX-120IC), and HCO 3 − and TDS were measured by acid-base titration and gravimetric processes, respectively. According to the charge balance verification of all hydrochemical data, the ionic balance error was within the limit value of ±5%, indicating the accuracy of our data.

Hydrochemical Characteristics
Statistics analysis of the hydrochemical parameters of 123 water samples is shown in Table 1, containing the minimum, maximum, and mean values of the major ions and hydrochemical parameters. As shown in Table 1, the concentration of cations in all water samples follows the same order of Na + > Ca 2+ > Mg 2+ > K + . However, the order of the concentration of anions in unconfined groundwater (SO 4 2− > Cl − > HCO 3 − ) is different with that of the confined groundwater and surface water (HCO 3 − > SO 4 2− > Cl − ). This implies the different water types that will be discussed in Section 3.2 and can indicate the difference of some geochemical processes (such as evaporation or water-rock interactions) occurring in different water. TDS, which is a comprehensive hydrochemical parameter, can be used to reflect the groundwater quality [10]. As shown in Table 1, TDS values of the unconfined groundwater range from 52 to 8954 mg/L with a mean value of 1043 mg/L. And it can be concluded that a gradually increasing trend of the TDS value of unconfined groundwater along the flow direction is occurring. This is mainly due to the fact that the unconfined groundwater in the recharge area (northern mountains area) is directly recharged from precipitation and snowmelt, while the groundwater in the discharge area (southeast and southwest area) may be influenced by relatively strong evaporation or water-rock reactions, especially in Gahai Lake and Hurleg Lake. However, the confined groundwater is always fresh water with TDS < 1 g/L. This hydrochemistry difference between unconfined groundwater and Water 2020, 12, 836 5 of 16 confined groundwater indicates the difference of some hydrochemical processes (such as evaporation) occurring in those two aquifers. In addition, the surface-water's hydrochemistry feature (concentration less than that of unconfined groundwater, but greater than that of the confined groundwater) implies the great recharge and runoff conditions and slight evaporation effects in the downstream area of Baying river. These hydrochemistry distributions in different areas and different aquifers can guide the selection for water resource field.
The pH values vary from 7 to 9 with a mean value of 8, indicating weak alkaline conditions. According to the National Drinking Water Standard of China, the standard pH value of residents' drinking water is 6.5-8.5. Thus, the analysis result of pH indicates that most water in this area is within the potable range.
The spatial distribution of Na + , Ca 2+ , Mg 2+ , K + cations shows an increasing tendency along the groundwater flow direction (from the mountain area to the alluvial-lacustrine plain). Na + is the dominant cation in this area, with concentration from 3.5 mg/L to 1887 mg/L in water samples; Ca 2+ , Mg 2+ are the secondary cations in water samples; concentration of K + is the lowest, with a mean value of 6.9 mg/L.
The concentration of Cl − also shows a gradual increase from the mountain area to the alluvial-lacustrine plain. The mean concentration of Cl − is 279.1, 67.1, and 113.8 mg/L for unconfined groundwater, confined groundwater, and surface-water, respectively. All the unconfined groundwater samples and parts of confined groundwater samples have Cl − values beyond the drinking water limit of 250 mg/L. The results of the main hydrochemical parameter correlation are presented in Table 2. The strong positive correlations between TDS and mainly ions (Na + , Cl − , Mg 2+ , SO 4 2− , Ca 2+ , K + , and HCO 3 − ) suggest the important role played by those mentioned ions in the groundwater hydrochemistry. There are good corrections between Na + and Cl − (0.974), Ca 2+ and SO 4 2− (0.915), Ca 2+ and Mg 2+ (0.858), indicating that the major ions of groundwater may originate from the halite, gypsum, and carbonate dissolution.

Groundwater Hydrochemical Types
The piper diagram is an important means to comprehend the hydrochemical characteristics, hydrochemical types and hydrochemical evolution in groundwater [11,12]. Figure 3 shows that the surface water and confined groundwater are characterized by HCO 3 -Ca·Na and HCO 3 ·SO 4 -Ca·Na types. However, the type of water chemistry for unconfined groundwater is relatively complex in this study area, including HCO 3 -Ca·Mg, HCO 3 ·SO 4 -Ca·Mg, SO 4 ·HCO 3 -Ca·Mg, SO 4 ·Cl-Ca·Mg, Cl·SO 4 -Na, and Cl-Na types. The hydrochemical types of the unconfined groundwater in the mountain area (recharge area) were mainly HCO 3 -Ca·Mg and HCO 3 ·SO 4 -Ca·Mg types, those in the alluvial-lacustrine plain (runoff area) were mainly SO 4 ·HCO 3 -Ca·Mg, SO 4 ·Cl-Ca·Mg types, and those in the lacustrine plain (discharge area) were mainly Cl·SO 4 -Na and Cl-Na types ( Figure 2).
The piper diagram is an important means to comprehend the hydrochemical characteristics, hydrochemical types and hydrochemical evolution in groundwater [11,12]. Figure 3 shows that the surface water and confined groundwater are characterized by HCO3-Ca·Na and HCO3·SO4-Ca·Na types. However, the type of water chemistry for unconfined groundwater is relatively complex in this study area, including HCO3-Ca·Mg, HCO3·SO4-Ca·Mg, SO4·HCO3-Ca·Mg, SO4·Cl-Ca·Mg, Cl·SO4-Na, and Cl-Na types. The hydrochemical types of the unconfined groundwater in the mountain area (recharge area) were mainly HCO3-Ca·Mg and HCO3·SO4-Ca·Mg types, those in the alluviallacustrine plain (runoff area) were mainly SO4·HCO3-Ca·Mg, SO4·Cl-Ca·Mg types, and those in the lacustrine plain (discharge area) were mainly Cl·SO4-Na and Cl-Na types ( Figure 2). According to the analysis of groundwater types in the Delingha area, there is a clear zoning distribution along the flow path ( Figure 4). The groundwater recharge area (mountainous area) is mainly featured with HCO3-type, the runoff area (the alluvial-lacustrine plain) is mainly represented According to the analysis of groundwater types in the Delingha area, there is a clear zoning distribution along the flow path ( Figure 4). The groundwater recharge area (mountainous area) is mainly featured with HCO 3 -type, the runoff area (the alluvial-lacustrine plain) is mainly represented by SO 4 -type, and the groundwater discharge area (near the Gahai Lake and Keluke Lake) is mainly featured with Cl-type.
Water 2020, 12, x FOR PEER REVIEW 7 of 17 by SO4-type, and the groundwater discharge area (near the Gahai Lake and Keluke Lake) is mainly featured with Cl-type.

Main Hydrochemical Processes
Gibbs diagrams were constructed by the equivalence ratios of Na + /(Na + + Ca 2+ ) and Cl − /(Cl − + HCO3 − ) versus TDS. This method has been widely used to identify hydrogeochemical evolution, which involves precipitation, rock weathering, and evaporation-crystallization processes [13]. In the Gibbs diagram, the water samples are located in the lower right, with low TDS values but high values

Main Hydrochemical Processes
Gibbs diagrams were constructed by the equivalence ratios of Na + /(Na + + Ca 2+ ) and Cl − /(Cl − + HCO 3 − ) versus TDS. This method has been widely used to identify hydrogeochemical evolution, which involves precipitation, rock weathering, and evaporation-crystallization processes [13]. In the Gibbs diagram, the water samples are located in the lower right, with low TDS values but high values of Na + /(Na + + Ca 2+ ) or Cl − /(Cl − + HCO 3 − ), indicating that the chemical compositions have been influenced by atmospheric precipitation; samples fall in the center region, suggesting that the rock weathering process is dominant; and samples with high TDS values and high Na + /(Na + + Ca 2+ ) and Cl − /(Cl − + HCO 3 − ) values fall in the upper right region, indicating the influence of evaporation.
As shown in Figure 5, all the confined groundwater and surface-water samples and most of the unconfined groundwater samples lie in the rock-weathering process dominance area, indicating that the main hydrochemical process of the local water is water-rock interaction. However, a few of unconfined groundwater samples collected from the lacustrine plain with a water table depth of 3-5 m are located in the transition region between evaporation and rock-weathering, suggesting that the water in the lacustrine plain was influenced both by evaporation and water-rock interaction.

Major Ion Relations in the Groundwater
The major ion relationship was plotted to explain the hydrochemical evolution processes and the controlling mechanism of the local groundwater. The ion ratio relationship can further assist in comprehending the process of water-rock interactions in this area. Thus, according to the hydrochemistry data, ratio graphs of the major ion relationship were plotted ( Figure 6).

Major Ion Relations in the Groundwater
The major ion relationship was plotted to explain the hydrochemical evolution processes and the controlling mechanism of the local groundwater. The ion ratio relationship can further assist in comprehending the process of water-rock interactions in this area. Thus, according to the hydrochemistry data, ratio graphs of the major ion relationship were plotted ( Figure 6).
If the molar ratio of Na + /Cl − is approximate to 1, indicating that halite dissolution mainly contributes to Na + concentration in groundwater; if this ratio is greater than 1, meaning that there is silicate weathering or a cation exchange; and if this ratio is less than 1, representing an anthropogenic disturbance. As shown, Figure 6a presents the ion relationship between Na + and Cl − . A few of the groundwater samples were along the 1:1 trend line, and the other samples lay above the 1:1 trend line, suggesting that halite dissolution, silicate weathering, and cation exchange are important sources of Na + . In addition, the saturation index (SI) of halite in Section 3.5 can further prove this view of the sources of Na + and Cl − . And few groundwater sample lie under the 1:1 trend line (Figure 6a), indicating that anthropogenic disturbance is weak in this area. If the molar ratio of Na + /Cl − is approximate to 1, indicating that halite dissolution mainly contributes to Na + concentration in groundwater; if this ratio is greater than 1, meaning that there is silicate weathering or a cation exchange; and if this ratio is less than 1, representing an anthropogenic disturbance. As shown, Figure 6a presents the ion relationship between Na + and Cl − . A few of the groundwater samples were along the 1:1 trend line, and the other samples lay above the 1:1 trend line, suggesting that halite dissolution, silicate weathering, and cation exchange are important sources of Na + . In addition, the saturation index (SI) of halite in Section 3.5 can further prove this view of the sources of Na + and Cl − . And few groundwater sample lie under the 1:1 trend line ( Figure  6a), indicating that anthropogenic disturbance is weak in this area.
If the HCO3 − /Na + ratio of water samples is 1:1 and 0.82:1.18, indicating that weathering of silicate minerals (albite and plagioclase) occurs in the groundwater. The corresponding hydrochemical reactions can be seen in Table 3 (reactions of 3 and 4). As shown in Figure 6b, only a few water samples were plotted between the 1:1 line and line 0.82:1.18. Furthermore, the correlation coefficient between Na + and HCO3 − is low (Table 2). These data suggest that the dissolution of albite and plagioclase is not the main source of Na + and HCO3 − in groundwater. Meanwhile, a ratio of Na + /HCO3 − larger than 1 showed the excess of Na + , which is mainly because of the dissolution of halite and cation exchange. If the HCO 3 − /Na + ratio of water samples is 1:1 and 0.82:1.18, indicating that weathering of silicate minerals (albite and plagioclase) occurs in the groundwater. The corresponding hydrochemical reactions can be seen in Table 3 (reactions of 3 and 4). As shown in Figure 6b, only a few water samples were plotted between the 1:1 line and line 0.82:1.18. Furthermore, the correlation coefficient between Na + and HCO 3 − is low ( Table 2). These data suggest that the dissolution of albite and plagioclase is not the main source of Na + and HCO 3 − in groundwater. Meanwhile, a ratio of Na + /HCO 3 − larger than 1 showed the excess of Na + , which is mainly because of the dissolution of halite and cation exchange.  Figure 6c also showed that samples of the confined groundwater and a part of unconfined groundwater lay over the 1:1 trend, implying that there may be an inverse cation exchange Equation (2) or weathering of calcite, dolomite and anorthite. 2Na The plot of (Mg 2+ + Ca 2+ ) versus (HCO 3 − + SO 4 2− ) can also determine the mineralization processes of groundwater. If the weathering of carbonate and sulfate minerals is the primary reaction in the groundwater, water samples will be along the 1:1 trend line. The samples will tend to lie in the right area when there is cation exchange Equation (1) occurring in the groundwater; water samples will locate at the left area of the diagram when an inverse cation exchange Equation (2) is occurring in the groundwater. As shown in Figure 6d, most of the groundwater samples lie along the 1:1 trend line, implying that the occurrence of dissolutions of carbonates and gypsum minerals. In addition, most of the confined groundwater samples and a part of the unconfined groundwater samples are observed to fall above the trend line of 1:1, indicating the effects of the inverse cation exchange process. Reactions (5-7, 10, 11) in Table 3 show the main processes that can release Ca 2+ and HCO 3 − . Figure 6e is the bivariate plots of Ca 2+ and HCO 3 − . According to those reactions, the ratios between  Figure 6f, and nearly all samples lie along the 2:1 line and 1.7:0.7 line, indicating a source of dolomite and pyroxene dissolution. If HCO 3 − and K + mainly come from the weathering of K-feldspar and biotite, according to the chemical reactions (formulas 8-9, in Table 3), the HCO 3 − /K + is 1:1 (K-feldspar) and 5:2 (biotite), respectively. As shown in Figure 6g, all water samples are above the line (1:1) and line (5:2). This suggests that the HCO 3 − is superfluous and that the weathering of K-feldspar and biotite are rare in the groundwater. The HCO 3 − was mainly from the weathering of albite, plagioclase, and carbonate minerals. The chlor-alkaline index (CAI) is an important way to study the occurrence of cation exchange [17,18]. The CAI-1 and CAI-II are estimated through the following equations (units of ions with meq/L): If the chlorine-alkalinity index is less than 0, the normal cation exchange process is dominant for hydrochemistry. On the contrary, if the index is a positive value, a reverse cation exchange process takes place. Figure 6h showed that all confined groundwater and most of the unconfined groundwater of the study area had negative chlorine-alkalinity index values, suggesting that Na + or K + in the aquifer have been substituted by Ca 2+ or Mg 2+ in the groundwater Equation (1). However, some unconfined groundwater samples are with positive index values, indicating a reverse cation exchange process Equation (2).

Saturation Index and Mineral Dissolution
Groundwater hydrochemistry was governed by many processes, such as groundwater flows, recharge and discharge processes, and water-rock reactions. Along the groundwater flow direction, hydrochemistry is always affected by minerals weathering in long residence time [19]. The saturation index (SI) of a mineral can be estimated by the following equation: SI = log( K IAP K SP ) (where, K IAP is the ions activity product for a mineral equilibrium reaction, and K SP is the solubility product of the mineral). The PHREEQC software can be used to calculate the SI values of the minerals in groundwater [20]. The results of SI suggest the trend of water and mineral chemical equilibrium and water-rock interaction. If unsaturated (SI < 0), the mineral will be continuously weathered by the groundwater; if supersaturated (SI > 0), the mineral will precipitate; and if SI is close to 0, the mineral phase will remain in an equilibrium state. According to the hydrochemistry data, the saturation indices of particular minerals were calculated ( Table 4).
The Saturation Index values of calcite and dolomite of a part of samples were greater than 0, and those of the other samples were less than 0 ( Table 4), indicating that the carbonate minerals keep gradually from unsaturation to supersaturation status. In contrast, the SI of halite and gypsum for all groundwater samples was less than 0 ( Table 4), suggesting that the halite and gypsum will continuously dissolve in groundwater. The Saturation Index values of calcite and dolomite ranged from −0.73 to 1.34 and −1.73 to 3.12, with mean values of 0.18 and 0.21, respectively. Figure 7b showed that there was a bad correlation between SI and TDS. In addition, the concentrations of Ca 2+ , HCO 3 − , Mg 2+ , HCO 3 − were not correlating with SI calcite (Figure 7e) and SI dolomite (Figure 7f), which indicate that the weathering of calcite and dolomite did not continue, and only a part of the minerals will be continuously dissolving along the groundwater flow direction. On the contrary, SI halite and SI gypsum were less than 0 and positively correlated with TDS (Figure 7a,b). Moreover, Na + and Cl − , Ca 2+ , and SO 4 2− show high correlation coefficients (R 2 equal to 0.974 and 0.915, respectively, Table 2). This suggests that the halite and gypsum will be continuing dissolved in groundwater along the flow direction. At the same time, the addition of Ca 2+ from the weathering of gypsum could lead to supersaturation of calcite and dolomite, thus inhibiting the weathering of calcite and dolomite. Figure 7c,d represent the scatter plots of Na + , Cl − versus SI halite and Ca 2+ , SO 4 2− versus SI gypsum , and the correlation coefficients R 2 are 0.975, 0.99, 0.948, and 0.941, respectively. The dissolution of halite and gypsum can produce exponential increases of Na + , Cl − and Ca 2+ , SO 4 2− , suggesting that halite and gypsum are the main minerals along the flow direction.
Because the stratum of the study area is mainly the Quaternary strata containing a large amount of clay minerals, there may be dissolution of aluminosilicate minerals, especially albite, anorthite, and plagioclase. This explanation is also supported by previous studies (Table 5) [21,22].  Because the stratum of the study area is mainly the Quaternary strata containing a large amount of clay minerals, there may be dissolution of aluminosilicate minerals, especially albite, anorthite, and plagioclase. This explanation is also supported by previous studies (Table 5) [21,22]. In addition, mineral stability diagrams were another important way to assess the degree of the fluid-rock equilibrium [23]. Figure 8 shows the Ca-, Na-, K-, and Mg-aluminosilicates stability diagrams of 43 water samples in this area. The software PHREEQC was applied to calculate the activities of ions, such as Ca 2+ , Mg 2+ , Na + , K + , and H 4 SiO 4 . The stability field diagrams of Ca-, Mg-, and Na-aluminosilicates (Figure 8a-c) showed that most of the unconfined groundwater samples lay in the stability region of kaolinite, while a few unconfined and all confined groundwater samples lay in the stability region of montmorillonite. Meanwhile, a number of water samples were located in the boundary between the stability fields of kaolinite and montmorillonite. And only one unconfined groundwater sample lay in the stability field of Gibbsite. Those results of Figure 8a-c showed that kaolinite and montmorillonite were in equilibrium. On the K + -H + -SiO 2 system plot (Figure 8d), all water samples fall in the stability field of illite, suggesting that illite is stable. To sum up, kaolinite, montmorillonite, and illite will be in equilibrium with the groundwater in this study area. Figure 8a-d showed that no water samples lay in the Amesite, Anorthite, Albite, or K-feldspar stability field. Some previous researches indicated that water samples keeping in equilibrium with kaolinite reflected good drainage conditions [24]. Table 6 shows the 14 C age of the local groundwater within the age of 5000-7000 years, indicating that the groundwater has relatively fast-updating capacity and that the groundwater runoff condition is good.
In addition, mineral stability diagrams were another important way to assess the degree of the fluid-rock equilibrium [23]. Figure 8 shows the Ca-, Na-, K-, and Mg-aluminosilicates stability diagrams of 43 water samples in this area. The software PHREEQC was applied to calculate the activities of ions, such as Ca 2+ , Mg 2+ , Na + , K + , and H4SiO4. The stability field diagrams of Ca-, Mg-, and Na-aluminosilicates (Figure 8a-c) showed that most of the unconfined groundwater samples lay in the stability region of kaolinite, while a few unconfined and all confined groundwater samples lay in the stability region of montmorillonite. Meanwhile, a number of water samples were located in the boundary between the stability fields of kaolinite and montmorillonite. And only one unconfined groundwater sample lay in the stability field of Gibbsite. Those results of Figure 8a-c showed that kaolinite and montmorillonite were in equilibrium. On the K + -H + -SiO2 system plot (Figure 8d), all water samples fall in the stability field of illite, suggesting that illite is stable. To sum up, kaolinite, montmorillonite, and illite will be in equilibrium with the groundwater in this study area. Figure 8ad showed that no water samples lay in the Amesite, Anorthite, Albite, or K-feldspar stability field. Some previous researches indicated that water samples keeping in equilibrium with kaolinite reflected good drainage conditions [24]. Table 6 shows the 14 C age of the local groundwater within the age of 5000-7000 years, indicating that the groundwater has relatively fast-updating capacity and that the groundwater runoff condition is good.   The four main feldspars stability diagrams and HCO 3 − versus Na + , Ca 2+ , Mg 2+ , K + bivariate plots indicated that there was weathering of aluminosilicate minerals, such as albite, plagioclase, anorthite, pyroxene, and amphibole in the study area (reactions of 3-7 in Table 3).

Implication for the Groundwater Resource Management
According to the result of TDS distribution along the groundwater flow direction (Figure 4), the groundwater quality in different areas and different aquifers can be concluded. As shown in Table 1, it can be learned that the confined groundwater is fresh water, even in the downstream area. However, as shown in Figure 4, along the flow direction, the unconfined groundwater was divided into three zones: fresh groundwater zone (TDS < 1 g/L), slightly salty groundwater zone (1 g/L < TDS < 3 g/L) and salty groundwater zone (TDS > 3 g/L). This can provide information for the local groundwater development. All the confined groundwater in this study area can be pumped for drinking water; however, only the fresh unconfined groundwater zone can be selected as the water resource field.
The result of the groundwater hydrochemical types (Figures 2 and 4) indicates that the HCO 3 − type groundwater, which means high quality water, is mainly located in the northern area. The HCO 3 − type groundwater can be supplied for a domestic water source. The SO 4 2− type groundwater can be supplied for agricultural and industrial consumption. Thus, this study can support the reasonable utilization and management of differentiated water. In addition, the result of the hydrochemistry difference between unconfined and confined groundwater implies the weak connection between those two aquifers in the lacustrine plain area. This can provide information for the elaborate hydrogeological modeling study of the groundwater resource assessment. Furthermore, the results of the hydrochemistry evolution indicate that the hydrochemical composition of groundwater is derived from dissolutions of evaporite minerals (halite and gypsum) and carbonate minerals (such as calcite and dolomite), aluminosilicate weathering and cation exchange. This result of mineral sources of groundwater can provide basic data for the refined groundwater pollution research.

Conclusions
A comprehensive analysis of hydrochemical data of 123 water samples in the Delingla area were conducted to provide a basis for understanding the major ions origins, distribution, and associated hydrogeochemical evolutions along the flow path and supporting the the local groundwater resource management.
The results showed that groundwater hydrochemistry has obvious zoning distribution in this area. TDS of groundwater is gradually increasing from the mountain area to the lacustrine plain. Furthermore, groundwater is characterized by HCO 3 -Ca·Mg and HCO 3 ·SO 4 -Ca·Mg types in the mountain area (recharge area), SO 4 ·HCO 3 -Ca·Mg and SO 4 ·Cl-Ca·Mg types in the alluvial-lacustrine plain (runoff area), and Cl·SO 4 -Na and Cl-Na types in the lacustrine plain (discharge area). The ions ratio relations, mineral saturation index, and mineral stability diagrams suggest that the dominating hydrochemical processes were dissolutions of evaporite minerals (halite and gypsum) and carbonate minerals (such as calcite and dolomite), aluminosilicates weathering, and cation exchange. The results of this study can provide references for further understanding of the groundwater geochemical evolution processes in this area and other similar areas. In addition, the hydrochemistry characteristics and groundwater evolution can guide the selection of water resource fields and provide information for the elaborate assessment and protection of groundwater resources.