Temporal and Spatial Characteristics of CO 2 Flux in Plateau Urban Wetlands and Their Inﬂuencing Factors Based on Eddy Covariance Technique

: Urban wetlands, an important part of the urban ecosystem, play an important role in regional carbon cycles and the carbon balance. To analyze the CO 2 source and sink effects of plateau urban wetlands, based on the data measured by an eddy covariance instrument, the temporal and spatial characteristics of CO 2 ﬂux and their inﬂuencing factors in the urban wetland of Xining City in the Qinghai Province of China during a warm season (July to September 2020) were studied. The results show that: (1) On the daily scale, the CO 2 ﬂux exhibited an obvious “U”-type variation, characterized by strong uptake in the daytime and weak emission at night, with an average daily ﬂux of − 0.05 mg · m − 2 · s − 1 . The CO 2 uptake peak of the wetland took place at 13:00 ( − 0.62 mg · m − 2 · s − 1 ), and the emission peak occurred at 23:30 (0.34 mg · m − 2 · s − 1 ); (2) on the monthly scale, the CO 2 ﬂux of the wetland in the study period showed a net uptake each month. The ﬂux increased month by month, and the maximum value occurred in September ( − 142.82 g · m − 2 · month − 1 ); (3) from a spatial point of view, the river area showed a weak CO 2 uptake ( − 0.07 ± 0.03 mg · m − 2 · s − 1 ), while the artiﬁcial wetland area showed a strong CO 2 uptake ( − 0.14 ± 0.03 mg · m − 2 · s − 1 ). The former was signiﬁcantly lower than the latter ( p < 0.01); (4) the regression analysis results show that the CO 2 ﬂux was signiﬁcantly correlated with PAR, VPD, T soil , and SWC ( p < 0.01). The relationships between the ﬂux and PAR, T soil , and SWC were rectangular hyperbola (y = 0.2304 − 2 × 10 − 3 x/(0.9037 + 0.0022x), R 2 = 0.64), exponential (y = 0.046exp(0.091x), R 2 = 0.88), and quadratic (y = − 0.0041x 2 + 0.1784x − 1.6946, R 2 = 0.83), respectively. Under the joint action of various environmental factors, the urban wetland ecosystem in plateau displayed a strong carbon sink function in warm seasons. This study can establish a data scaffold for the accurate estimation of carbon budget of this type of ecosystem.


Introduction
Wetland ecosystems are an important part of terrestrial ecosystems. Although they only account for 1% of the Earth's surface area, the carbon (up to 225 × 10 9 t) stored in wetland ecosystems accounts for 11% of the total land carbon; thus, the wetland ecosystem plays a great role in the global carbon cycle [1]. Compared to natural wetlands, urban wetlands are strongly disturbed and managed intensively by humans, which affects the source and sink effects of urban wetland greenhouse gases in terms of wetland hydrology, soil and vegetation [2][3][4][5][6]. Urban and regional carbon management (URCM) research plans have become a part of the global carbon project (GCP) [7]. In recent years, extensive studies have focused on the hydrological relationships between urban wetlands, and it is believed that their connectivity will change the redox states and C:N stoichiometric characteristics of wetlands, thus, promoting the emission of greenhouse gases [8,9]. Studies on the contents of urban wetlands have focused on the influence of species, density, phenology and the human management of wetland plants on sources and sinks of greenhouse gases [10][11][12]. In addition, the molecular biology in regard to the source and sink effects of greenhouse gases in urban wetlands is also being studied [13,14]. Therefore, urban wetlands have become a common subject of research in relation to greenhouse gas sources and sinks.
Currently, research methods of CO 2 flux in wetland ecosystems include inventory estimations, chamber, remote sensing inversion, the eddy covariance method, etc. [15][16][17]. In the eddy covariance method, the CO 2 exchange rate between the wetland ecosystem and atmospheric interface in the region is calculated by measuring the covariance between the CO 2 mixing ratio and vertical wind velocity fluctuation in the atmosphere [18]. The eddy covariance method has been widely accepted because of its continuity, high precision, and lack of interference in the monitoring environment in the monitoring of ecosystem fluxes. Compared to the traditional monitoring methods, such as the static chamber method, the monitoring range of the eddy covariance method is larger. Thereby, in the last decade, this method has been widely applied in studies on CO 2 fluxes in ecosystems [19][20][21].
Research on the CO 2 sources and sinks of urban wetland ecosystems has been carried out extensively, and fruitful objectives have been achieved, but regional imbalances in studies have been encountered. Recent research has focused on urban rivers and lake wetlands in low-altitude regions [22][23][24], and few studies have assessed plateau urban wetlands, especially the Qinghai-Tibet Plateau urban wetland, which is highly sensitive to climate change and human activities. The Qinghai-Tibet Plateau is a region of China with abundant wetlands. Although the area of wetlands in China is reducing by about 1% annually, the wetland area in the Qinghai-Tibet Plateau has increased, and the area of artificial wetlands has increased faster than those of other types of wetlands [25][26][27]. Therefore, considering the fact of global climate change, research on the CO 2 sources and sinks of urban wetlands in the Qinghai-Tibet Plateau is of great significance to the carbon turnover, carbon cycle and regional carbon emissions reduction in regional wetland ecosystems. Taking the Huangshui National Wetland Park in Xining, Qinghai Province of China, in the northeast of the Qinghai-Tibet Plateau as the research object, this work reports the temporal and spatial variation characteristics of CO 2 flux in the warm season (July to September 2020) in the study area on the basis of data measured by the eddy covariance instrument method and data quality assessments. Additionally, the response of CO 2 flux of the plateau urban wetland ecosystem to external environmental factors was investigated. Based on the data and theoretical findings reported in this work, the CO 2 budget of a plateau urban wetland ecosystem can be accurately evaluated.

Description of the Area
The flux tower (36 • 39 14 , 101 • 41 7 ) was located in the Huangshui National Wetland Park, Xining City, Qinghai Province, China. The altitude of this park is about 2290 m. The park has a plateau semi-arid climate with an annual temperature of 5.7 • C, annual precipitation of 360-400 mm, annual evaporation of 1363.6 mm, strong solar radiation, long sunshine time and large temperature difference between day and night [28]. The park has a total area of 5.09 km 2 , and is the largest wetland ecosystem in Xining City. The vegetation covers a large area, dominated by perennial trees which mainly include Populus cathayana Rehd, Salix babylonica and Pinus tabuliformis Carr.
In order to better understand the spatial ranges represented by the observed value of the eddy covariance instrument, in this study, the source area range of the observation tower was calculated using the footprint model (Kljun model) [29], which is relatively new and has been validated. The region surrounded by the 90% horizontal isoline represents the region with a contribution rate of 90% to the value observed. This region is named as the 90% contribution source area. The range of the 90% contribution source area calculated in this paper varied from 125 to 491 m. The range of source areas in the northwest direction (270 • to 320 • ), principally the Huangshui River and artificial wetland water area, exceeds the average value. Additionally, the range of source areas in the southeast direction (120 • to 150 • ), primarily the artificial wetland vegetation area, also exceeds the average value. In contrast, the ranges of source areas in the east and west directions are slightly smaller than average. Therefore, the average range of the 90% contribution source area (246 m) was taken as the radius of the circular study area with the center of the observation point ( Figure 1). itation of 360-400 mm, annual evaporation of 1363.6 mm, strong solar radiation, long sunshine time and large temperature difference between day and night [28]. The park has a total area of 5.09 km 2 , and is the largest wetland ecosystem in Xining City. The vegetation covers a large area, dominated by perennial trees which mainly include Populus cathayana Rehd, Salix babylonica and Pinus tabuliformis Carr.
In order to better understand the spatial ranges represented by the observed value of the eddy covariance instrument, in this study, the source area range of the observation tower was calculated using the footprint model (Kljun model) [29], which is relatively new and has been validated. The region surrounded by the 90% horizontal isoline represents the region with a contribution rate of 90% to the value observed. This region is named as the 90% contribution source area. The range of the 90% contribution source area calculated in this paper varied from 125 to 491 m. The range of source areas in the northwest direction (270° to 320°), principally the Huangshui River and artificial wetland water area, exceeds the average value. Additionally, the range of source areas in the southeast direction (120° to 150°), primarily the artificial wetland vegetation area, also exceeds the average value. In contrast, the ranges of source areas in the east and west directions are slightly smaller than average. Therefore, the average range of the 90% contribution source area (246 m) was taken as the radius of the circular study area with the center of the observation point ( Figure 1).

Instrument Setting and Field Observation
The eddy covariance system is mainly composed of an LI-7500RS-type open-circuit three-dimensional ultrasonic anemometer, CSAT3-type open-circuit CO2/H2O analyzer, and data collector, with sampling frequency of 10 Hz. The original output data of the 3D ultrasonic anemometer include horizontal wind speed, vertical wind speed, ultrasonic virtual temperature, and the diagnostic value of the instrument. The original output data of the CO2/H2O analyzer include the absolute density of CO2, absolute density of water vapor, intensity of CO2 signal, and diagnostic value of the instrument. When the eddy covariance system was operated, the CO2 flux was calculated once every 30 min and the value was stored with the original data observed. The flux results calculated on-line

Instrument Setting and Field Observation
The eddy covariance system is mainly composed of an LI-7500RS-type open-circuit three-dimensional ultrasonic anemometer, CSAT3-type open-circuit CO 2 /H 2 O analyzer, and data collector, with sampling frequency of 10 Hz. The original output data of the 3D ultrasonic anemometer include horizontal wind speed, vertical wind speed, ultrasonic virtual temperature, and the diagnostic value of the instrument. The original output data of the CO 2 /H 2 O analyzer include the absolute density of CO 2 , absolute density of water vapor, intensity of CO 2 signal, and diagnostic value of the instrument. When the eddy covariance system was operated, the CO 2 flux was calculated once every 30 min and the value was stored with the original data observed. The flux results calculated on-line should be calibrated before they are used for scientific research. To ensure the accuracy of the measured CO 2 and H 2 O fluxes, the CO 2 and H 2 O analyzers were calibrated with standard CO 2 gas (±1% 450 ppm) and a dew-point generator (LI-610) every three months. The 3D anemometer was maintained regularly, and the wind speed measured was compared with the value derived from a micro meteorological station to ensure an error of less than 5%.
Soil temperature (T soil ) at a depth of 5 cm underground and soil water content (SWC) were automatically recorded every 30 min via a data collector (Sutron9210 Xlite, USA).

Eddy Covariance Technology
The CO 2 flux is defined as the quantity of CO 2 transported per unit area in unit time [30], and can be calculated as follows: where w represents the vertical component of three-dimensional wind speed (m·s −1 ); r is the molar concentration of CO 2 measured by the instrument (µmol·m −3 ); w and r represent the deviations between instantaneous and average values of w and r, respectively. The upper lines indicate the average values in the corresponding periods.

Data Quality Control
The original 10 Hz data were processed using the Express module in the Eddypro software (LI-COR Company). The processing steps include coordinate axis rotation correction, trend correction, data synchronization, statistical test, density correction, ultrasonic virtual temperature correction, spectrum correction, attack angle correction, data quality control mark and other procedures. Finally, 30 min of flux data were obtained [31][32][33].
Due to the influence of measurement errors and weather factors, the quality of partial data was poor. Thereby, quality assessment (QA) of the 30-min flux data was required [34]: (1) The abnormal flux values calculated by the EddyPro software were excluded; (2) the flux data obtained in raining and snowing periods were excluded; (3) the poor-quality flux data represented by 2 in the "0-1-2" quality evaluation method of the EddyPro software were excluded.
For the CO 2 flux data derived at night, in addition to the above-mentioned quality control process, the quality control was enhanced as follows: (1) The negative data at night were excluded because only the respiration of vegetation and soil occurred at night; (2) based on data analysis, the empirical threshold of CO 2 flux is 23 µmol·m −2 ·s −1 , so the values beyond this threshold were excluded; (3) the instrument response to the weak convection at night was insensitive, so the intensity of air turbulence was evaluated according to the air friction velocity (u*), and the CO 2 flux data with night friction wind speeds lower than 0.2 m·s −1 were excluded; (4) the abnormally large values were excluded, according to the quadruple standard deviation of CO 2 flux value. After the quality control, 41.4% of the original flux data were excluded, and the exclusion rate was greater than that of FLUXNET (35%) [35].

Data Interpolation
(1) For the day-time, CO 2 flux data of net ecosystem excluded, the Michaaelis-Menten equation was adopted in the interpolation by fitting [36]: where NEE d stands for the CO 2 flux data (mg·m −2 ·s −1 ) measured by the day-time eddy covariance system; R eco,d stands for the dark respiration rate of ecosystem during the day (mg·m −2 ·s −1 ); PAR is the photosynthetically active radiation (µmol·m −2 ·s −1 ); α is the apparent initial light energy utilization efficiency (mg·µmol −1 ); P max stands for the maximum photosynthetic rate (mg·m −2 ·s −1 ), which is the net photosynthetic rate of the ecosystem corresponding to a maximum PAR value.
(2) For the night-time flux data excluded, the interpolation was performed on the basis of the relationship between CO 2 flux and soil temperature [37]: where R eco,n stands for the CO 2 flux data measured by the night-time eddy covariance system; a and b are the fitting coefficients; T soil is the relevant soil temperature.
(3) The temperature sensitivity coefficient of ecosystem respiration (Q 10 ) was calculated by the following equation [38]: (4) For the conventional meteorological data, when the data were excluded continuously less than four times, the linear interpolation was performed; when the data were excluded continuously more than four times, but less than eight times, the average value of the values observed at the same time in the four days before and after the missing date was taken as the required value. If the data were excluded continuously more than eight times, the average value in the relevant month was taken as the value required [39].

Split of CO 2 Flux Data
Ecosystem respiration (R eco ) is the basis to calculate the total productivity of the ecosystem (GEP). Since photosynthesis does not take place for plants at night, NEE n can be taken as the night-time ecosystem respiration (R eco,n ). A respiratory curve can be obtained by fitting models to the flux and temperature data at night, and the daytime ecosystem respiration (R eco,d ) can be obtained by calculating the value corresponding to the daytime temperature according to the respiratory curve [40]. The ecosystem respiration is defined as: Therefore, the total primary productivity GPP can be expressed as: At the ecosystem scale, the total ecosystem productivity equals the total primary productivity: GEP = GPP (7)

Data Statistical Analysis
The data were processed using Microsoft Excel 2016 software, and statistical analysis was conducted with IBM SPSS Statistics 25 software. Graphs were made with Origin 2020 software. Data completed by fitting and interpolation were used to analyze the temporal and spatial variation characteristics of CO 2 flux, while only effective data were used to analyze the influence of environmental factors on net CO 2 exchange. The half-hour and daily average fluxes were taken as the arithmetic means in corresponding periods, and the monthly and total fluxes were taken as the cumulative values in corresponding periods.

Daily Dynamic Change of CO 2 Flux
At an interval of half an hour, the monthly average mean of net ecosystem CO 2 exchange (NEE) at the same time of each month was calculated, according to the CO 2 flux data in the warm season (July to September) in 2020, and thus, the month-average daily changes in NEE in different months were obtained ( Figure 2). A positive NEE value reflects CO 2 emission, and a negative value correlates to CO 2 uptake. Figure 2 shows that the NEE in the warm season of the wetland exhibited obvious daily variation characteristics, and the daily fluctuation curve is generally in a "U" shape. Carbon uptake (−0.24 ± 0.28 mg·m −2 ·s −1 ) took place in the daytime while carbon emission occurred at night (0.17± 0.19 mg·m −2 ·s −1 ). During the study period, the daily CO 2 uptake in July, August, and September occurred at about 8:00, and the NEE gradually changed from positive to negative, indicating that the photosynthetic rate of the ecosystem was higher than that of the respiration rate and carbon emission was altered by carbon uptake. The maximum CO 2 uptake peak took place in the range of 12:00 to 14:00, and the values were −0.62, −0.56, and −0.62 mg·m −2 ·s −1 , respectively. Then, the uptake value was gradually weakened, and the carbon uptake was altered by carbon emission at about 18:30. The maximum CO 2 emission peak took place in the range of 22:00 to 23:00, and the values were 0.34, 0.28, and 0.18 mg·m −2 ·s −1 . The average daily fluctuation in July is most obvious from −0.62 to 0.34 mg·m −2 ·s −1 . Meanwhile, the fluctuations of net CO 2 emissions in the ecosystem at night were relatively small, and the values are significantly smaller than those of the net CO 2 uptake in the daytime (p < 0.01). changes in NEE in different months were obtained (Figure 2). A positive NEE value reflects CO2 emission, and a negative value correlates to CO2 uptake. Figure 2 shows that the NEE in the warm season of the wetland exhibited obvious daily variation characteristics, and the daily fluctuation curve is generally in a "U" shape. Carbon uptake (−0.24 ± 0.28 mg·m −2 ·s −1 ) took place in the daytime while carbon emission occurred at night (0.17± 0.19 mg·m −2 ·s −1 ). During the study period, the daily CO2 uptake in July, August, and September occurred at about 8:00, and the NEE gradually changed from positive to negative, indicating that the photosynthetic rate of the ecosystem was higher than that of the respiration rate and carbon emission was altered by carbon uptake. The maximum CO2 uptake peak took place in the range of 12:00 to 14:00, and the values were −0.62, −0.56, and −0.62 mg·m −2 ·s −1 , respectively. Then, the uptake value was gradually weakened, and the carbon uptake was altered by carbon emission at about 18:30. The maximum CO2 emission peak took place in the range of 22:00 to 23:00, and the values were 0.34, 0.28, and 0.18 mg·m −2 ·s −1 . The average daily fluctuation in July is most obvious from −0.62 to 0.34 mg·m −2 ·s −1 . Meanwhile, the fluctuations of net CO2 emissions in the ecosystem at night were relatively small, and the values are significantly smaller than those of the net CO2 uptake in the daytime (p < 0.01).  Table 1 shows the average and cumulative CO2 fluxes of the plateau urban wetland ecosystem in the warm season (July to September) in 2020. Carbon sink took place in each month of the warm season. Over the measurement period, though the month-average GPP flux and month-average Reco flux decreased gradually, the difference between them increased month by month. The month-average NEE fluxes in July, August and September were −0.04, −0.05, and −0.06 mg·m −2 ·s −1 , respectively. The carbon sink capacity of the wetland ecosystem increased month by month, and the monthly total CO2 uptake was −102.05, −120.53, and −142.82 g·m −2 ·month −1 , respectively.  Table 1 shows the average and cumulative CO 2 fluxes of the plateau urban wetland ecosystem in the warm season (July to September) in 2020. Carbon sink took place in each month of the warm season. Over the measurement period, though the month-average GPP flux and month-average R eco flux decreased gradually, the difference between them increased month by month. The month-average NEE fluxes in July, August and September were −0.04, −0.05, and −0.06 mg·m −2 ·s −1 , respectively. The carbon sink capacity of the wetland ecosystem increased month by month, and the monthly total CO 2 uptake was −102.05, −120.53, and −142.82 g·m −2 ·month −1 , respectively.  Figure 3a shows the net CO 2 exchange capacities of the plateau urban wetland ecosystem in all wind directions in the warm season, and the flux fluctuated between −0.32 and 0.15 mg·m −2 ·s −1 . According to the distribution characteristics of the wetland park, the research area was divided into two parts, with the 90 • and 270 • wind directions as the boundary. The north and south parts are denoted by river and artificial wetland regions. All the areas with net CO 2 emissions were located in the river area (0-30 • and 300-360 • ), and net CO 2 uptake was found in other wind directions. One-way analysis of variance results (Figure 3b) show that carbon uptake, −0.07 ± 0.03 and −0.14 ± 0.03 mg·m −2 ·s −1 , occurred in both regions during the whole study period, but the carbon uptake intensity of the artificial wetland area was significantly higher than that of the river region (p < 0.05). Figure 3a shows the net CO2 exchange capacities of the plateau urban wetland ecosystem in all wind directions in the warm season, and the flux fluctuated between −0.32 and 0.15 mg·m −2 ·s −1 . According to the distribution characteristics of the wetland park, the research area was divided into two parts, with the 90° and 270° wind directions as the boundary. The north and south parts are denoted by river and artificial wetland regions. All the areas with net CO2 emissions were located in the river area (0-30° and 300-360°), and net CO2 uptake was found in other wind directions. One-way analysis of variance results (Figure 3b) show that carbon uptake, −0.07 ± 0.03 and −0.14 ± 0.03 mg·m −2 ·s −1 , occurred in both regions during the whole study period, but the carbon uptake intensity of the artificial wetland area was significantly higher than that of the river region (p < 0.05).

Factors Affecting CO2 Flux
For a better understanding of the response of flux characteristics to environmental factors, the net CO2 exchange capacity in the warm season can be split into day-time (NEEd) and night-time (NEEn). Table 2 shows the Pearson correlation coefficients between NEE and primary environmental factors in a typical sunny day at a 0.5-h scale. During the day, NEEd was significantly negatively correlated (p < 0.01) with photosynthetically active radiation (PAR) and significantly positively correlated (p < 0.01) with the saturated vapor pressure difference (VPD) and air temperature (Tair). At night, NEEd was significantly positively correlated (p < 0.01) with soil temperature (Tsoil) and significantly negatively correlated (p < 0.01) with soil moisture content (SWC).

Factors Affecting CO 2 Flux
For a better understanding of the response of flux characteristics to environmental factors, the net CO 2 exchange capacity in the warm season can be split into day-time (NEE d ) and night-time (NEE n ). Table 2 shows the Pearson correlation coefficients between NEE and primary environmental factors in a typical sunny day at a 0.5-h scale. During the day, NEE d was significantly negatively correlated (p < 0.01) with photosynthetically active radiation (PAR) and significantly positively correlated (p < 0.01) with the saturated vapor pressure difference (VPD) and air temperature (T air ). At night, NEE d was significantly positively correlated (p < 0.01) with soil temperature (T soil ) and significantly negatively correlated (p < 0.01) with soil moisture content (SWC).

Factors Affecting Daytime CO 2 Flux
Photosynthetically active radiation directly affects the photosynthesis of plants and is a major environmental factor affecting the net CO 2 exchange of the ecosystem in the daytime [41]. In this study, the Michaelis-Menten equation was adopted to correlate NEE d and PAR (Equation (2)). Figure 4a shows that NEE d and PAR obviously exhibited a rectangular hyperbola relationship on the daily scale. With an increase in PAR, NEE d decreased significantly (p < 0.01), indicating that the carbon sink capacity of the wetland was significantly enhanced due to the strengthened photosynthetically active radiation. Meanwhile, the influence of PAR on NEE d in different months (Figure 4b) was studied (Figure 4b). The results show that the apparent quantum efficiency (α), parameter of maximum photosynthetic rate (P max ), and dark respiration rate of the ecosystem in daytime (R eco,d ) displayed season-dependent trends: in the warm season of 2020, the maximum α value of the plateau urban wetland ecosystem was registered in August, and P max and R eco,d reached their maximums in July. Approximately 64% of the changes in NEE d during the study period can be ascribed to PAR, which indicates that PAR is the key environmental factor affecting NEE d . However, NEE d cannot be predicted by PAR alone, and is also largely affected by other environmental factors (Table 2). photosynthetic rate (Pmax), and dark respiration rate of the ecosystem in daytime (Reco,d) displayed season-dependent trends: in the warm season of 2020, the maximum α value of the plateau urban wetland ecosystem was registered in August, and Pmax and Reco,d reached their maximums in July. Approximately 64% of the changes in NEEd during the study period can be ascribed to PAR, which indicates that PAR is the key environmental factor affecting NEEd. However, NEEd cannot be predicted by PAR alone, and is also largely affected by other environmental factors (Table 2). The saturated vapor pressure difference determines the canopy conductance and closure degree of plant leaf stomas; thus, affecting the photosynthetic capacities of trees [42,43]. Based on the analysis of the response processes of plateau urban wetland NEEd to PAR under different VPD conditions ( Figure 5), it was found that under three VPD conditions, pronounced rectangular hyperbola relationships between PAR and NEEd were observed. When the VPD was ≤ 1 kPa, most of the corresponding photosynthetically active radiation was weak, and the light saturation point could not be readily reached for the photosynthesis of plant leaves. At this time, Reco,d reached its maximum of 0.2717 mg·m −2 ·s −1 . The values α, Pmax, and R 2 were 0.0029 mg·μmol −1 , 1.0342 mg·m −2 ·s −1 , and 0.56. When VPD was in the range of 1 to 1.5 kPa, α decreased, while Pmax and R 2 increased. When Pmax reached the maximum value of 1.0526 mg·μmol −1 , the photosynthesis efficiency of the ecosystem also reached the maximum. When VPD was ≥ 1.5 kPa, the stomas were partially closed and Pmax decreased, so VPD tended to inhibit the photosynthesis of ecosystem. In summary, excessively high and low VPD values were not conducive to the photosynthesis of plants, and the VPD range of 1-1.5 kPa is most suitable for the photosynthesis of vegetation in plateau urban wetlands. In addition, on the one hand, Tair had an indirect impact on the stomas of plant leaves by affecting the VPD, resulting in a light saturation phenomenon and thereby changing the net photosynthetic rate dynamics [44]. On the other hand, excessively high Tair directly destructed the cellular structures of The saturated vapor pressure difference determines the canopy conductance and closure degree of plant leaf stomas; thus, affecting the photosynthetic capacities of trees [42,43]. Based on the analysis of the response processes of plateau urban wetland NEE d to PAR under different VPD conditions ( Figure 5), it was found that under three VPD conditions, pronounced rectangular hyperbola relationships between PAR and NEE d were observed. When the VPD was ≤ 1 kPa, most of the corresponding photosynthetically active radiation was weak, and the light saturation point could not be readily reached for the photosynthesis of plant leaves. At this time, R eco,d reached its maximum of 0.2717 mg·m −2 ·s −1 . The values α, P max , and R 2 were 0.0029 mg·µmol −1 , 1.0342 mg·m −2 ·s −1 , and 0.56. When VPD was in the range of 1 to 1.5 kPa, α decreased, while P max and R 2 increased. When P max reached the maximum value of 1.0526 mg·µmol −1 , the photosynthesis efficiency of the ecosystem also reached the maximum. When VPD was ≥ 1.5 kPa, the stomas were partially closed and P max decreased, so VPD tended to inhibit the photosynthesis of ecosystem. In summary, excessively high and low VPD values were not conducive to the photosynthesis of plants, and the VPD range of 1-1.5 kPa is most suitable for the photosynthesis of vegetation in plateau urban wetlands. In addition, on the one hand, T air had an indirect impact on the stomas of plant leaves by affecting the VPD, resulting in a light saturation phenomenon and thereby changing the net photosynthetic rate dynamics [44]. On the other hand, excessively high T air directly destructed the cellular structures of leaves, and passivated the enzymes for photosynthesis, thus, affecting the net photosynthetic rate [42]. Nonetheless, the regression analysis results show that T air and NEE d were linearly correlated, but the relationship was weak (R 2 = 0.09), indicating that T air was not the major factor limiting the daytime photosynthesis.
Water 2021, 13, 1176 9 of 14 leaves, and passivated the enzymes for photosynthesis, thus, affecting the net photosynthetic rate [42]. Nonetheless, the regression analysis results show that Tair and NEEd were linearly correlated, but the relationship was weak (R 2 = 0.09), indicating that Tair was not the major factor limiting the daytime photosynthesis.

Factors Influencing CO2 Flux at Night
Temperature, as one of the important driving forces of ecosystem respiration, has a significant impact on carbon exchange in night ecosystems. Especially in high-altitude regions, the temperatures change greatly between day and night and among seasons, so temperature is often a major environmental factor controlling the CO2 flux [37,45,46]. Therefore, the NEEn was correlated with soil temperature at a depth of 5 cm underground. The NEEn refers to the average CO2 flux in half an hour, corresponding to an interval of 0.5 °C. The fitting results are shown in Figure 6a. With the increase in Tsoil, the NEEn of urban wetland ecosystem in the warm season increased exponentially (R 2 = 0.88), indicating that the soil temperature could be the reason for the respiration variation of the ecosystem at night. Different from other regions, in the Qinghai-Tibet Plateau, the biogeo-

Factors Influencing CO 2 Flux at Night
Temperature, as one of the important driving forces of ecosystem respiration, has a significant impact on carbon exchange in night ecosystems. Especially in high-altitude regions, the temperatures change greatly between day and night and among seasons, so temperature is often a major environmental factor controlling the CO 2 flux [37,45,46]. Therefore, the NEE n was correlated with soil temperature at a depth of 5 cm underground. The NEE n refers to the average CO 2 flux in half an hour, corresponding to an interval of  Figure 6a. With the increase in T soil , the NEE n of urban wetland ecosystem in the warm season increased exponentially (R 2 = 0.88), indicating that the soil temperature could be the reason for the respiration variation of the ecosystem at night. Different from other regions, in the Qinghai-Tibet Plateau, the biogeochemical activities of various organisms adapt to the regional environment, and usually take place under extremely cold conditions, so slight changes in temperature will cause evident changes in their activities [47]. Q 10 is a sensitivity parameter used to depict the response of CO 2 flux to temperature variation, and it is defined as the increasing fold of CO 2 flux corresponding to 10°C of temperature rise [48]. The soil temperature at 5 cm corresponded to a Q 10 value of 2.48, within the Q 10 range of 1.28 to 4.75 for the land ecosystems in China [49]. This is lower than the value (3.45) of alpine meadow wetlands in the Qinghai-Tibet Plateau [50], yet far higher than that (1.33) of the Yellow River Estuary intertidal salt marsh wetland [51] and that (1.84) of the Shenlongjia Dajiu Lake peat wetland [52]. In conclusion, the response of the CO 2 flux of plateau urban wetland ecosystem to the change in soil temperature is relatively sensitive, which indicates that more attention should be paid in the situation of global warming.

Importance and Particularity of CO2 Fluxes of Plateau Urban Wetlands in Warm Seasons
Urban wetland plays an important role in global carbon cycle through carbon fixation and oxygen release, and has a high value of climate regulation [7,28]. As the Qinghai-Tibet Plateau is located in a high-altitude area, the climate does not change obviously among the four seasons, showing obvious cold and warm seasons [54]. Compared to the long cold season, the rainy and thermal warm season plays an important role in the carbon cycle of urban wetland ecosystem in the Qinghai-Tibet Plateau, and is the main period for the fast growing of vegetation and CO2 uptake. During the study period, the overall CO2 uptake of −365.40 g·m −2 in the study area was observed, and this value is comparable to that of the Artemisia selengensis meadow wetland in Qinghai Lake (−351.14 g·m −2 ) [47], and higher than that of the low-altitude Yellow River Delta reed wetland (−195.39 g·m −2 ) and the salt marsh wetland (−81.69 g·m −2 ) [51,55], indicating that the urban wetland ecosystem of the Qinghai-Tibet Plateau is an important carbon sink. Similar to other ecosystems, the NEE showed obvious daily changes in the warm season. The daily flux maximum of CO2 uptake in the plateau urban wetland ecosystem reached 0.62 mg·m −2 ·s −1 , comparable to that of the alpine meadow wetland in the eastern margin of the Qinghai-Tibet Plateau (0.68 mg·m −2 ·s −1 ) [50], higher than that of the Artemisia selengensis meadow wetland (0.42 mg·m −2 ·s −1 ) [47] and cold wetland of the source region of the Yellow River (0.55 mg·m −2 ·s −1 ) [46], and lower than that of the cold Maqu meadow wetland (10.20 mg·m −2 ·s −1 ) [56]. Compared to the wetland ecosystems in the plain area, the value is higher than that of the Shenlongjia Dajiu Lake peat wetland (0.30 mg·m −2 ·s −1 ) [52] and lower than that of the unflooded Nanji wetland of Poyang Lake (0.80 mg·m −2 ·s −1 ) [6]. In the warm season, solar radiation in the northeast of the Qinghai-Tibet Plateau is strong, and the temperature difference between day and night is large, so the daily CO2 flux varied between −0.62 and 0.34 mg·m −2 ·s −1 , to a larger extent. The fluctuation is larger than that of the peat swamp in the Canada estuary (−0.29-0.18 mg·m −2 ·s −1 ) [57], yet smaller than that of the reed wet-  Soil water content affects the NEE n by changing the oxygen content in the soil and redox potential of the wetland ecosystem. Ultra-high or ultra-low SWC values will limit the respiration of soil organisms [53]. During the study period, the SWC value at night of the plateau urban wetland varied in the range of 21.03-28.49%. The average CO 2 flux in half an hour was correlated to SWC values at intervals of 5% following the binomial fitting. The results are shown in Figure 6b (R 2 = 0.83). With the increase in SWC, NEE n increased. When SWC reached 21.64%, NEE n reached the maximum. Then, with the increase in SWC, NEE n decreased, indicating that the optimal soil moisture content that is favorable for the carbon emission of plateau urban wetland is around 21.64%.

Importance and Particularity of CO 2 Fluxes of Plateau Urban Wetlands in Warm Seasons
Urban wetland plays an important role in global carbon cycle through carbon fixation and oxygen release, and has a high value of climate regulation [7,28]. As the Qinghai-Tibet Plateau is located in a high-altitude area, the climate does not change obviously among the four seasons, showing obvious cold and warm seasons [54]. Compared to the long cold season, the rainy and thermal warm season plays an important role in the carbon cycle of urban wetland ecosystem in the Qinghai-Tibet Plateau, and is the main period for the fast growing of vegetation and CO 2 uptake. During the study period, the overall CO 2 uptake of −365.40 g·m −2 in the study area was observed, and this value is comparable to that of the Artemisia selengensis meadow wetland in Qinghai Lake (−351.14 g·m −2 ) [47], and higher than that of the low-altitude Yellow River Delta reed wetland (−195.39 g·m −2 ) and the salt marsh wetland (−81.69 g·m −2 ) [51,55], indicating that the urban wetland ecosystem of the Qinghai-Tibet Plateau is an important carbon sink. Similar to other ecosystems, the NEE showed obvious daily changes in the warm season. The daily flux maximum of CO 2 uptake in the plateau urban wetland ecosystem reached 0.62 mg·m −2 ·s −1 , comparable to that of the alpine meadow wetland in the eastern margin of the Qinghai-Tibet Plateau (0.68 mg·m −2 ·s −1 ) [50], higher than that of the Artemisia selengensis meadow wetland (0.42 mg·m −2 ·s −1 ) [47] and cold wetland of the source region of the Yellow River (0.55 mg·m −2 ·s −1 ) [46], and lower than that of the cold Maqu meadow wetland (10.20 mg·m −2 ·s −1 ) [56]. Compared to the wetland ecosystems in the plain area, the value is higher than that of the Shenlongjia Dajiu Lake peat wetland (0.30 mg·m −2 ·s −1 ) [52] and lower than that of the unflooded Nanji wetland of Poyang Lake (0.80 mg·m −2 ·s −1 ) [6]. In the warm season, solar radiation in the northeast of the Qinghai-Tibet Plateau is strong, and the temperature difference between day and night is large, so the daily CO 2 flux varied between −0.62 and 0.34 mg·m −2 ·s −1 , to a larger extent. The fluctuation is larger than that of the peat swamp in the Canada estuary (−0.29-0.18 mg·m −2 ·s −1 ) [57], yet smaller than that of the reed wetland in Northeast China (−1.0-0.30 mg·m −2 ·s −1 ) [58] and the Amazon marsh wetland (−0.88-0.30 mg·m −2 ·s −1 ) [59].
Plateau urban wetlands are usually constructed in the vicinity of rivers, and the close material circulation and energy flow between them will inevitably lead to dynamic changes in the source and sink functions of wetlands. Due to the particularity of plateau rivers, in the global carbon cycle, rivers not only play the role of a "pipeline" connecting land and marine ecosystems, but are also important greenhouse gas emission sources [60]. It has been reported that urban rivers, affected by humans, have higher greenhouse gas emissions. For example, eutrophication can change the structure and function of the ecosystem, thus, affecting the dynamic emission of greenhouse gases [61]. Due to the existence of rivers, some of the regions in the plateau urban wetland ecosystem exhibited net CO 2 emissions, and the CO 2 uptake intensity in the wetland region was significantly higher than that in the river region. In addition, the warming trend of the Qinghai-Tibet Plateau is becoming more and more obvious under the influence of global warming, and the warming rate in the past 40 years is twice the global average rate in the same period [62,63]. High temperatures, increased eutrophication, and their interaction can significantly affect the production, transportation, and emission of greenhouse gases [64]. Under the dual actions of global climate change and human activities, the source and sink effects of the plateau urban wetland ecosystem face many challenges, and more attention should be paid to this issue in the future.

Conclusions
With the development of warming changes in the global climate, the uncertainty related to greenhouse gas emissions from the Qinghai-Tibet Plateau wetlands, especially the urban wetlands, has increased significantly. In this study, the Huangshui National Wetland in Xining City, Qinghai-Tibet Plateau, which is sensitive to climate change and human activities, was taken as the research object. The temporal and spatial variation characteristics and influencing factors of CO 2 flux in the warm season (July to September 2020) were analyzed. The principal conclusions are presented as follows: (1) The CO 2 flux of urban wetland ecosystem in the Qinghai-Tibet Plateau exhibited obvious "U" type daily change characteristics. CO 2 uptake was observed in the daytime and emission was recorded at night, with a large daily variation range.
(2) The urban wetland ecosystem of the Qinghai-Tibet Plateau had a strong carbon sink function in the warm season, with total uptake of −365.40 g·m −2 . However, due to the net CO 2 emission in some river regions, the carbon uptake intensity of the artificial wetland region was significantly higher than that of the river region.
(3) During the day, the CO 2 flux was primarily affected by PAR and VPD, and the optimal VPD, which was most favorable for the carbon uptake of ecosystem, was in the range of 1-1.5 kPa. At night, the CO 2 flux was largely affected by T soil and SWC, and the optimal SWC, which was most favorable for the carbon emission of ecosystem, was 21.64%. This is noteworthy because the research object is located in the city, large quantities of C, N and other nutrients have been discharged into the object, and these nutrients will change the structure and function of the ecosystem through eutrophication, and thereby noticeably affect the emission dynamics of CO 2 , especially CO 2 emission from rivers. Therefore, monitoring factors related to the water environment, such as dissolved oxygen, dissolved organic carbon, and total nitrogen, should be enhanced in the future. In addition, methane emission should be assessed in future studies, so the carbon budget of the plateau urban wetland ecosystem can be evaluated with higher precision.

Data Availability Statement:
The project still on going and the data cannot be published at the current stage because there might be more analysis and comparison of the data. However, in case any researcher needs the data can either contact us via email or use Digitizer Plot for the graphs to extract the data.