- Open Access
N2O emission and its influencing factors in subtropical streams, China
Ecological Processes volume 10, Article number: 54 (2021)
Rivers and streams are one of the primary sources of nitrous oxide (N2O) which is an important greenhouse gas with great global warming potential. Yet, over the past century, human activities have dramatically increased reactive nitrogen loadings into and consequently led to increased N2O emission from the river ecosystems. Here, we carried out a study in two subtropical rivers, i.e., Jinshui River and Qi River with slight and intense human disturbance in their respective catchments in China. The study intended to explore spatial variability and seasonality in N2O emissions, and the relative importance of physicochemical variables, nitrification and denitrification potentials, and functional genes abundance influencing N2O emissions.
N2O concentration, N2O saturation, and N2O flux of Jinshui River peaked in high flow season. N2O concentration, N2O saturations, and N2O flux in Qi River and downstream of Jinshui River were significantly higher than that in other areas in normal and low flow seasons. N2O concentration was positively correlated with water temperature, water NO3−, and DOC, negatively correlated with water NH4+ and DOC/NO3− (the ratio of dissolved organic carbon to NO3− in water), and positively correlated with potential nitrification rate in high flow season, but not correlated with functional genes abundance. Both rivers had lower N2O saturation and flux than many freshwater systems, and their EFr-5 (N2O emission factor for river) was lower than the recommended values of IPCC.
While the two rivers were moderate sources of N2O and N2O emissions in river systems were normally elevated in the summer, areas with intense human disturbance had higher N2O concentration, N2O saturations, and N2O flux than those with slight human disturbance. Physicochemical variables were good indicators of N2O emissions in the river ecosystems.
Rivers are one of the primary sources of nitrous oxide (N2O) which is an important contributor to global climate change (Stocker et al. 2013; Hu et al. 2016; Marzadri et al. 2017). But in recent decades, increasing human activities, such as land use change (e.g., deforestation, urbanization, etc.) have released large quantities of pollutants, leading to increasing nitrogen loadings which affect nitrogen cycling in and increase N2O emission from the river ecosystems (Kim et al. 2014; Hou et al. 2015; Liu et al. 2015; Chen et al. 2019; Zheng et al. 2019). The influence of N2O emissions in the river system on the atmospheric N2O balance is becoming much more important (Seitzinger and Kroeze 1998).
N2O is a byproduct of different microorganisms’ transformations in the nitrogen cycling, including nitrification, denitrification, and dissimilatory nitrate reduction to ammonium (DNRA) (Cole and Caraco 2001). Nitrification and denitrification appear to be the dominant sources of N2O in most natural systems (Firestone and Davidson 1989; Wang et al. 2009). The microorganisms driving nitrification process contain AOA-amoA and AOB-amoA genes (Kowalchuk et al. 2000). nirS, nirK, and nosZ are the key genes in the denitrification process (Braker et al. 2000; Wyman et al. 2013). N2O emission in the environment is generally associated with these gene encoding enzymes and bacteria in the nitrogen cycling (Nie et al. 2015; Nie et al. 2016; Ma et al. 2017; Cocco et al. 2018; Black et al. 2019). These genes are often used to study the relationship between N2O emission and microorganisms (Cocco et al. 2018).
Aquatic N2O production is complex and sensitive to environmental variables (Wang et al. 2009), which arises from the complexity of the nitrogen cycling, the difficulty of decoupling hydrologic and biogeochemical processes, and increasing human disturbance in the river ecosystems (Liu et al. 2015). Increasing human disturbance, such as conversion of natural land use (e.g., forests and wetlands) to human land use (e.g., cropland and urban areas), releases large quantities of pollutants, including nitrogen, and has widespread effects on biodiversity and ecological function of rivers (Müller et al. 1998; Liu et al. 2015). The increase of inorganic nitrogen concentration can promote nitrification and denitrification, leading to increase in N2O production (Weathers 1984; Herbert 1999; McMahon and Dennehy 1999; Naqvi et al. 2000; Cole and Caraco 2001). Other environmental factors, such as temperature, DO, C/NO3−, can affect the nitrogen cycle processes and subsequently N2O release (Kelso et al. 1997; Liikanen and Martikainen 2003; Baulch et al. 2012; Rosamond et al. 2012; Deng et al. 2015; Quick et al. 2019). Land use could also indirectly affect sediment denitrification and N2O emission in headwater streams by influencing the river water quality or sediment characteristics (Inwood et al. 2007). But the relative contributions of different environmental factors and biogeochemical processes to N2O emissions are widely debated (Bollmann and Conrad 1998; Soued et al. 2015; Gardner et al. 2016; Voigt et al. 2017), and few studies have addressed the indirect effects of catchment human disturbance on river N2O emission. IPCC proposed a method to estimate N2O emission flux from rivers by using emission factor (EF5-r). The recommended value of EF5-r was revised to 0.0025 in 2006 (IPCC 2006). However, due to the difference of N2O generation mechanism in different geographical regions, the universal applicability of EF5-r is widely disputed (Wang et al. 2012).
Here, we investigated environmental factors, dissolved N2O concentration, N2O saturation, N2O flux, and N2O emission factor in different hydrological regimes (i.e., high, normal, and low flow seasons) in two subtropical rivers with different human disturbance intensities in their respective catchments in China. Our objects are to (1) assess spatial variability and seasonality in dissolved N2O concentration, N2O saturation, N2O flux, and N2O emission factor and (2) assess relationships between physicochemical factors, functional genes abundance, nitrification rates, denitrification rates, and N2O concentration.
Materials and methods
Our study areas were located in Jinshui River and Qi River in China (Fig. 1). Jinshui River is a mountainous river, a secondary tributary of the Yangtze River and a primary tributary of the Han River. The catchment area of Jinshui River is 731 km2. Mean annual temperature is 11.8 °C. Annual precipitation ranges from 950 to 1200 mm (Zhang et al. 2010; Wang et al. 2015). Rainfall is highly variable, with July to October being high flow season, November and April to June is normal flow season, and December to March is low flow season (Wang et al. 2015). Elevation ranges from 363 to 2884 m in the catchment (Fig. 1).
Qi River is a plain river, a tertiary tributary of the Yangtze River and a secondary tributary of Han River. The basin area of Qi River is 1501 km2. The average annual temperature is about 15.1 °C, and the annual precipitation ranges from 860 to 935 mm. June to August is high flow season, March to May and September to November is normal flow season, and December to February is low flow season (Xiong 2018). Elevation ranges from 161 to 2018 m in the catchment (Fig. 1).
The highest temperatures occur in high flow season, followed by normal and low flow seasons in the Jinshui River and Qi River. For Jinshui River, the catchment can be divided into three zones representing varying human disturbance intensities (i.e., slightly, moderately and intensively disturbed areas) from upstream to downstream based upon population density, area of cropland, and disturbance history (Zhang et al. 2010, 2013; Wang et al. 2015). Upstream of Jinshui River is in the Foping National Nature Reserve of the Qinling Mountains, which is mostly uninhabited with extensive forest cover (Zhang et al. 2010, 2013). Cultivated lands and small towns are primarily located along the downstream and midstream of Jinshui River catchment. There are no industries in Jinshui River catchment. However, there are cultivation of edible fungi, fruit trees and traditional Chinese medicine herbs, power stations, and pharmaceutical factories in Qi River catchment (Zhao et al. 2020). In general, human disturbance in Qi River catchment has been more intensive than that in Jinshui River catchment, and the area of small towns and cultivated lands are larger in Qi River catchment than those in Jinshui River (Table S1, land use attribute table of Jinshui River and Qi River catchments; Zhao et al. 2020).
We sampled sediment, overlying water, and air samples at nine locations from upstream to downstream in Jinshui River (Zhang et al. 2013; Wang et al. 2015) (Fig. 1). Sites J1, J2, and J3 were located downstream, sites J4, J5, and J6 were located midstream, and sites J7, J8, and J9 were located in the upstream. Similarly, we sampled samples at nine locations from upstream to downstream in Qi River (Fig. 1). Sites Q1, Q2, and Q3 were located downstream, sites Q4, Q5, and Q6 were located midstream, and sites Q7, Q8, and Q9 were located upstream.
According to the hydrological regime, samples were collected in high flow season (August 2018), normal flow season (November 2018), and low flow season (March 2019) in both rivers. We sampled sediment using sterile sampling bags, and each sediment sample was mixed with three parallel samples. Overlying water (0–10 cm) was collected with polyethylene plastic bottles, filtered the samples through filter membranes (0.45 μm), and stored them at 4 °C for the determination of physicochemical factors, nitrification and denitrification rates. Overlying water (0–10 cm) was collected with 60 mL serum bottle (Thermo Fisher) for the determination of dissolved N2O concentration, and to prevent microbial activity, these samples were poisoned with 500 μL of a saturated aqueous mercury chloride (HgCl2) solution.
The surface sediment samples (0–5 cm) were collected with sterilized shovel and stored the sediment in sterile TWIRL’EM® EPR-3050 sample bags (Labplas, Quebec). Sediment samples for molecular analyses were stored in liquid nitrogen immediately, and samples for nitrogen transformation rate and physicochemical factors detections were stored in 4 °C. We sampled air samples with 12 mL gas-tight vials (Labco Exetainers) for air N2O detections above 0.5 m the water surface. Wind speed at 2 m above water surface was measured by hand-held anemometer (Kestrel 2500, USA).
Measurement of water and sediment physicochemical variables
Water temperature was measured with a YSI Professional ProPlus probe in the field. NO3− and NH4+ concentrations of water (w-NO3− and w-NH4+) and sediments (s-NO3− and s-NH4+) were measured with an automatic continuous flow analyzer (AMS westco, Smartchem 200, Italy) in the lab. NO3− and NH4+ concentrations of sediments were extracted from fresh soil with KCl (2.0 mol/L) in the lab. Dissolved organic carbon (DOC) concentration of water and sediment organic carbon (SOC) were measured with a TOC analyzer (Elementar, Vario TOC, Germany) in the lab.
Detection of dissolved N2O concentration, N2O saturation, N2O flux, and N2O emission factor
Static headspace gas chromatography was used to determine dissolved N2O concentration in water samples (Walter et al. 2005). During the water sample pretreatment, a needle was inserted into the rubber stopper of the serum bottle under the condition of sealing the serum bottle in the lab. The 30 mL of the water sample was replaced with N2 (purity > 99.999%). After the sample bottle was placed on the shaker for 4 h at room temperature to release the dissolved N2O from the water, 5 ml of gas was extracted from the top of the sample bottle with a syringe and injected into a vacuum tube. The headspace N2O sample was determined by gas chromatography (Agilent, 7890A, USA; column temperature: 60 °C; chromatographic column: hayesp Q 80-mesh packed column, 8FT; pre-column flow: 21 ml/min; separation column: constant pressure, 33.5 psi; detector ECD: 300 °C; tail blowing 5 ml/min). Finally, the dissolved N2O concentration in water was calculated according to the headspace N2O concentration (Johnson et al. 1990; Eq. 1).
where CN2O is the dissolved N2O concentration (nmol/L), Cg is the headspace N2O concentration (nmol/L), β is the Bunsen coefficient (Liu et al. 2011b), 22.4 is the molar volume of N2O, R is the gas constant 0.082, and Tk is in K. Vg is the volume of the gas phase, Vl is the volume of the liquid phase.
The N2O saturation was the ratio of the dissolved N2O concentration to the equilibrium N2O concentration (Ceq) (Eq. 2). The equilibrium N2O concentration was calculated by Henry formula (Yang et al. 2013; Liu et al. 2011b; Eq. 3).
where Ceq is the equilibrium concentration of N2O in water at the given water temperature (nmol/L), and CA is the atmospheric N2O concentration of the sampling sites (nmol/L).
where ∆ N2O is the N2O net increase and is the difference between the dissolved N2O concentration to the equilibrium N2O concentration (Eq. 5). k denotes gas exchange rate (Cole and Caraco 1998; Crusius and Wanninkhof 2003; Eqs. 6 and 7).
where U10 denotes wind speed at 10 m above water surface (m/s), and U10 was calculated by wind speed at 2 m above water surface (U2) (Yang et al. 2015; Eq. 8; Table S2). Sc denotes viscosity coefficient of N2O (Wanninkhof 2014; Eq. 9).
where T denotes water temperature (°C).
N2O emission factor for river (EF5-r) is ratios of dissolved N2O-N (μg N/L) to NO3−-N (μg N/L) (Eq. 10).
Linear mixed modeling was performed to examine spatial variability and seasonality in dissolved N2O concentration in water, N2O saturation in water, N2O flux and N2O emission factor using SPSS 20 (SPSS®, version 20; IBM®, Armonk, New York). Sampling sites were random effects, and sampling seasons and rivers were fixed effects. Linear mixed modeling was performed to examine the difference in N2O concentration, N2O saturation, N2O flux, and N2O emission factor among sampling areas of each river using SPSS 20. Sampling sites were random effects, and sampling areas were fixed effects.
A series of stepwise multiple regression analyses with backward selection (P< 0.05) were then applied to identify the determinants of N2O concentration using SPSS 20 (the independent variables were water and sediment physicochemical variables). Correlations between dissolved N2O concentration, nitrification genes abundance (Fig. S1, AOA-amoA, AOB-amoA), denitrification genes abundance (Fig. S2, nirK; Fig. S3, nirS; Fig. S4, nosZ), denitrification rates (Fig. S5), and nitrification rates (Fig. S6) were analyzed with the Pearson correlation analyses using Origin 9.0.
The Structural Equation Modeling (SEM) was performed to further elucidate the direct and indirect effects of key explanatory variables on N2O concentration. First, a conceptual path model was developed according to existing literature and basic ecological principles (Liu et al. 2015; Feng et al. 2018). Second, promising explanatory variables were selected to include in path analysis mainly based on the results of Pearson correlation (Table S3) and stepwise multiple regression analyses. The abundance of nitrification genes (AOB-amoA and AOA-amoA) and three denitrification genes (nirK, nirS, and nosZ) were found to be highly positively correlated with each other (Table S4). Afterwards, a principal component analysis (PCA) was conducted to reduce the number of variables using SPSS 20.0 (SPSS, Chicago, IL, USA). The principal component 1 (PC1) extracted from two nitrification gene explained 54.71% of the total variance and was thus considered as the representative of the overall variation in nitrification genes. The principal component 1 (PC1) extracted from three denitrification genes explained 70% of the total variance and was thus considered as the representative of the overall variation in denitrification genes (Feng et al. 2018). amoA and denitrification genes were introduced as new variables into the SEM. Third, path coefficients, R2, direct and indirect effects, and model fit parameters were calculated by AMOS 20.0. The low χ2 (chi-squared test), P value > 0.05, a comparative fit index (CFI) value > 0.95, Tucker-Lewis index (TLI) value > 0.90, and root square error of approximation (RMSEA) < 0.05 indicated that the final path model had an acceptable fit with the data (Schermelleh-Engel et al. 2003; Fan et al. 2016). Statistical analyses were conducted at a 0.05 significant level.
For Jinshui River, water temperature, s-NO3−, w-NH4+, s-NH4+, DOC, and SOC in high flow season were higher than those in other seasons (Tables 1 and 2). DOC/NO3− (the ratio of dissolved organic carbon to NO3− in water) and SOC/NO3− (the ratio of sediment organic carbon to sediment NO3−) in low flow season were higher than those in other seasons (P < 0.05). There was no significant seasonal difference in w-NO3− (P > 0.05). Temperature in downstream was the highest in all seasons (P < 0.05). DOC in upstream was the highest in high flow season (P < 0.05). DOC in downstream was the highest in normal flow and low flow seasons (P < 0.05). w-NO3− in downstream was the lowest in low flow season (P < 0.05). s-NO3− and SOC in midstream were the lowest in high flow season (P < 0.05). And DOC/NO3− in downstream was the highest in low flow season (P < 0.05).
For Qi River, water temperature, w-NO3−, s-NO3−, w-NH4+, s-NH4+ and SOC in high flow season were higher than those in other seasons (P < 0.05). DOC and DOC/NO3− in low flow season were higher than those in other seasons (P < 0.05). There was no significant seasonal difference in SOC/NO3− (P > 0.05). Temperature in downstream was highest in high and normal flow seasons (P < 0.05). w-NO3− in downstream was the lowest in low flow season (P < 0.05). s-NO3− in upstream was the lowest in high flow season (P < 0.05). DOC in downstream was the lowest in normal and low flow seasons (P < 0.05). And SOC/NO3− in upstream was the lowest in low flow season (P < 0.05).
Comparatively, water temperature in Qi River was higher than that in Jinshui River in normal flow season (P < 0.05). w-NO3− concentration in Qi River was higher than that in Jinshui River in high flow season (P < 0.05). DOC in Qi River was higher than that in Jinshui River in normal and low flow seasons (P < 0.05).
Dissolved N2O concentration
N2O concentrations in Qi River were higher, 1.51 and 1.37 times of that in Jinshui River in normal and low flow seasons (Fig. 2, P < 0.01 and P < 0.05), respectively. For Jinshui River, there was no significant seasonal difference in N2O concentration (P > 0.05). N2O concentration in normal flow season in downstream was higher (P < 0.05), and 1.12 and 1.12 times of that in midstream and upstream, respectively. There was no difference in N2O concentration between sampling sites in high and low flow seasons (P > 0.05). For Qi River, there was no significant seasonal difference in N2O concentration (P > 0.05). N2O concentration of normal flow season in midstream was higher, 1.23 times of that in downstream (P < 0.05).
N2O saturation in Qi River was higher, 1.69 times of that in Jinshui River in normal flow season (Fig. 3, P < 0.01 and P < 0.05). For Jinshui River, N2O saturation in high flow season was higher (P < 0.01), 1.61 and 1.45 times of that in normal and low flow seasons, respectively. The N2O saturation in downstream was the highest for all three seasons (P < 0.05). For Qi River, there was no significant seasonal difference in N2O saturation in Qi River (P > 0.05). N2O saturation of normal flow season in midstream was higher, 1.24 times of that in upstream (P < 0.05).
N2O flux of Qi River was 13.28 and 4.79 times of that in Jinshui River in normal and low flow seasons, respectively (Fig. 4, P < 0.01 and P < 0.05). For Jinshui River, the N2O flux in high flow season was higher (P < 0.01), 7.95 and 1.77 times of that in normal and low flow seasons, respectively. N2O flux of downstream was higher than midstream and upstream in normal and low flow seasons (P < 0.05). N2O flux in few downstream sampling sites was less than zero. For Qi River, there was no significant seasonal difference in N2O flux (P > 0.05). The N2O flux in upstream was higher, 1.63 times of that in downstream in high flow season (P < 0.05).
N2O emission factor
N2O emission factor in Jinshui River varied from 0.042–0.054%, 0.047–0.072%, and 0.047–0.089%, and in Qi River varied from 0.034–0.049%, 0.057–0.083%, and 0.054–0.113% in high, normal, and low flow seasons, respectively (Table 3). There was no significant difference in N2O emission factor between the two rivers (P > 0.05). For Jinshui River, N2O emission factor in low flow season was higher than that in high flow season (P < 0.05). N2O emission factor in upstream was lower than that in downstream and midstream in low flow season (P < 0.05). For Qi River, N2O emission factor in low flow season was higher than that in high and normal flow season (P < 0.05). There was no significant difference among sampling sites in all seasons (P > 0.05).
Relationship between N2O concentration, physicochemical variables, nitrification rate, denitrification rate, and functional genes abundance
Stepwise multiple regression revealed that w-NO3−, DOC, w-NH4+, and DOC/NO3− explained a relatively large portion of the variances in N2O concentration at annual level for both rivers (Table 4, P < 0.05). w-NO3− explained a relatively large portion of the variances in N2O concentration in high flow season (Table 4, P < 0.05). Water temperature explained a relatively large portion of the variances in N2O concentration in normal flow season (Table 4, P < 0.01). For Jinshui River, DOC/NO3− explained a relatively large portion of the variances in N2O concentration at annual level (Table 4, P < 0.05). For Qi River, w-NH4+ explained a relatively large portion of the variances in N2O concentration at annual level (Table 4, P < 0.05).
Pearson’s correlation analyses showed that there was no significant correlation between functional genes abundance and N2O concentration (Table S5, P > 0.05). There was significantly positive correlation between N2O concentration and nitrification rate in normal flow season (Table S5, r = 0.52, P < 0.05).
SEM result (R2 = 0.431, P = 0.977, χ2 = 0.467, CFI = 1.00, TLI = 1.151, RMSEA = 0.000) showed water temperature, w-NO3−, w-NH4+, DOC, and DOC/NO3− could affect N2O concentration both directly and indirectly (Fig. 5, Table S6, P < 0.05).
Seasonal and spatial variabilities of N2O emission
N2O emission (N2O concentration, N2O saturation, and N2O flux) showed significant seasonality in present study. Similar to other studies (Hasegawa et al. 2000; Harrison and Matson 2003; Garnier et al. 2009; Beaulieu et al. 2010; Rosamond et al. 2012; Burgos et al. 2015), N2O concentration, N2O saturation and flux of Jinshui River were peak in high flow season (summer) (Figs. 2 and 4). The higher NO3− and organic carbon in high flow season were important factors and tended to enhance microbial processes including those producing N2O, such as nitrification and denitrification (Starry et al. 2005; Wang et al. 2018; Liu et al. 2019). Temperature is the key driver of the temporal dynamics of N2O emission (Wang et al. 2018), and higher temperature in high flow season affects the decomposition rate of organic matter through its effect on microbial activity and consequently regulates N2O production rate in the present study (Wang et al. 2018). This finding confirms that N2O emissions in subtropical river systems are normally elevated in the summer (Musenze et al. 2014, 2015; Allen et al. 2011).
Significant spatial differences in N2O emission were also observed in present study, N2O concentration, N2O saturation, and N2O flux were higher in areas with intensive human disturbance (Figs. 2, 3, and 4). As previously noted, significant variability in water physicochemical variables was observed in the sampling areas, and these variables could be considered here as possible factors influencing the spatial differences in N2O emission. The effects of human disturbance on river N2O emission were more likely driven through changes of water physicochemical variables (Liu et al. 2015). Water characteristics were significantly affected by human disturbance (Sponseller et al. 2001; Huang et al. 2012). Disturbance gradient followed an elevational gradient in the present study, and the elevational gradient also had driven higher temperatures in the lower-elevation intensely disturbed areas. Higher temperature enhanced the N2O production processes (Rosamond et al. 2012; Burgos et al. 2015). The increase of agricultural and urban land use could lead to the decline of river water quality including increased reactive nitrogen and degrading organics in the terrestrial biosphere (Sponseller et al. 2001; Huang et al. 2012; Kim et al. 2014; Hou et al. 2015), leading to higher denitrification rate (Jung et al. 2014; Harrison et al. 2011; Morse et al. 2012). Therefore, the Qi River and downstream of Jinshui River with higher water temperature, DOC and NO3 −, had promoted the occurrence of nitrification and denitrification which enhanced N2O concentration.
Influencing factors of dissolved N2O concentration
N2O concentration has been shown to be associated with many physicochemical variables. Higher temperature can increase microbial enzyme activity in denitrification and nitrification processes (Chen et al. 2011; Zheng et al. 2016), which was demonstrated by the positive correlation between N2O concentration and water temperature in present study (Table 4). On the other hand, expression and activity of key enzymes in denitrification and nitrification processes are strongly dependent on the carbon substrate (Philippot et al. 2013; Sigleo 2019). Higher organic carbon content leads to proliferation of heterotrophic bacteria, larges consumption of dissolved oxygen (Wang et al. 2015), and the anaerobic environment is more suitable for denitrification (Chapin et al. 2011; Hou et al. 2013; Ma et al. 2014). Also, many nitrification microorganisms can use organic carbon as carbon source (Hallam et al. 2006), and these may explain the positive correlation between N2O concentration and DOC (Table 4).
Previous studies found that DOC/NO3− was significantly negatively correlated with nitrification (Schade et al. 2016; Zhao et al. 2020) and reported higher sediment denitrification rates under optimal DOC/NO3− range (0.35–3.5) (Hansen et al. 2016). DOC/NO3− was beyond this range in present study, and higher DOC/NO3− might have inhibited N2O production from denitrification and nitrification. Denitrification is positively correlated with NO3− concentration (Jung et al. 2014; Liu et al. 2019), so higher NO3− concentration may promote N2O production. In the present study, N2O concentration was positively correlated with w-NO3− concentrations (Table 4), but the relationship was not always significant (Fig. 5; Reay et al. 2003). These results indicated uncertainty of the correlation between NO3− and N2O emission, which suggests complexity of N2O production in rivers (Liu et al. 2011a). Also, heterotrophic microorganisms consume NH4+ with rapid propagation, providing an anaerobic environment for denitrification; therefore, N2O concentration from denitrification might increase as w-NH4+ decreased (Liu et al. 2015).
The correlation between functional genes abundance and N2O concentration was weak, but N2O concentration was positively correlated with potential nitrification rate in high flow season (Table S5). Several studies have shown that nitrification rate can be greater than denitrification rate in rivers (Holmes et al. 1996; Webster et al. 2003; Arango and Tank 2008). Nitrification produces twice as much N2O per unit N converted as compared to denitrification (Mosier et al. 1998). Therefore, our results did not exclude the possibility of N2O production through denitrification but identifies nitrification as the major N2O source in sediments (Koike and Terauchi 1996; Bauza et al. 2002). Direct measurement of functional genes abundance could not be an indicator of their activities, and more research on substantial post-transcriptional, protein assembly, and/or environmental factors to determine what ultimately controls activity is much needed (Ikeda et al. 2009; Liu et al. 2010; Smith et al. 2015).
Overall, the influencing factors of N2O concentration varied in different seasons and rivers in the present study (Table 4; Harrison et al. 2005; Liu et al. 2015; Yang and Lei 2018). There were more influencing factors at the annual level than the monthly level, due to large variation of physicochemical variables at the annual level. Spatially, the dominant control factor was DOC/NO3− for Jinshui River, and the dominant control factor for Qi River was NH4+ (Table 4), implying difference in controlling factors on river N2O concentration with different human activity intensities in the uplands.
N2O emission factor, N2O saturations, and N2O flux
IPCC recommended value of N2O emission factor for river (EF5-r) was 0.0025 (IPCC 2006). Similar to other studies (Clough et al. 2006; Yang et al. 2015), our measured EF5-r values ranged from 0.00034 to 0.00113 in the present study (Table 3). According to the IPCC definition, the amount of N2O released estimated by IPCC release coefficient may be overestimated because dissolved N2O concentration in river includes part of N2O dissolved in water to reach equilibrium, which is not a source of atmospheric N2O (Wang et al. 2012). A discrete measurement of EF5-r is extremely difficult, and its values were different in different rivers (Table 3). New measurement and estimation techniques are needed to minimize errors of N2O flux by applying single model (Clough et al. 2006).
Interestingly, seasonal difference of N2O saturation and N2O flux was significant in Jinshui River (Figs. 3 and 4), but not in Qi River. Spatial variations of N2O saturation and N2O flux of Qi River were inconsistent (Figs. 3 and 4). This may be due to larger direct discharge of sewage in Qi River, and N2O in the water body far exceeds the amount of N2O formed in the process of nitrogen migration and transformation, which makes the seasonal difference of N2O emission smaller. Our study showed N2O saturations and flux in Jinshui River and Qi River were similar to most freshwater systems in China (Yan et al. 2004; Zhao et al. 2009; Wang et al. 2012; Xu et al. 2016) and lower than those in other countries (García-Ruiz et al. 1999; McMahon and Dennehy 1999; Dong et al. 2004; Rosamond et al. 2011). N2O saturations of most samples in Jinshui River and Qi River were greater than 100% (Fig. 3), which indicated that both rivers were sources of atmospheric N2O (Yang et al. 2013). Overall, the two rivers had high N2O fluxes in most of their areas, and they were moderate sources of the atmospheric N2O.
We investigated N2O concentration, N2O saturation, N2O flux, and N2O emission factor of two subtropical rivers, China. Our results revealed that: (1) N2O concentration, N2O saturation, and N2O flux of Jinshui River peaked in high flow season, and areas with intensive human disturbance had higher N2O concentration, N2O saturation, and N2O flux in normal and low flow seasons. (2) Our present study rivers had lower N2O saturation and flux than many freshwater systems, and they were moderate sources of N2O. (3) Physicochemical variables including temperature, NO3−, NH4+, DOC, SOC, DOC/NO3− and SOC/NO3− were good indicators of N2O emissions in the river ecosystems.
Availability of data and materials
N2O emission factor for river
- w-NO3 − :
NO3− concentration of water
- w-NH4 + :
NH4+ concentration of water
Dissolved organic carbon concentration of water
- DOC/NO3 − :
The ratio of dissolved organic carbon to NO3− in water
- s-NO3 − :
NO3− concentration of sediment
- s-NH4 + :
NH4+ concentration of sediment
Sediment organic carbon concentration
- SOC/NO3 − :
The ratio of sediment organic carbon to NO3− in sediment
The Structural Equation Modeling
The principal component 1
Comparative fit index
Root square error of approximation
Allen D, Dalal RC, Rennenberg H, Schmidt S (2011) Seasonal variation in nitrous oxide and methane emissions from subtropical estuary and coastal mangrove sediments, Australia. Plant Biol 13(1):126–133. https://doi.org/10.1111/j.1438-8677.2010.00331.x
Arango C, Tank JL (2008) Land use influences the spatiotemporal controls on nitrification and denitrification in headwater streams. J North Am Benthological Soc 27(1):90–107. https://doi.org/10.1899/07-024.1
Baulch HM, Dillon PJ, Maranger R, Venkiteswaran JJ, Wilson HF, Schiff SL (2012) Night and day: short-term variation in nitrogen chemistry and nitrous oxide emissions from streams. Freshw Biol 57(3):509–525. https://doi.org/10.1111/j.1365-2427.2011.02720.x
Bauza JF, Morell JM, Corredor JE (2002) Biogeochemistry of nitrous oxide production in the red mangrove (Rhizophora mangle) forest sediments. Estuar Coast Shelf Sci 55(5):697–704. https://doi.org/10.1006/ecss.2001.0913
Beaulieu JJ, Shuster WD, Rebholz JA (2010) Nitrous oxide emissions from alarge, impounded river: the Ohio River. Environ Sci Technol 44(19):7527–7533 https://doi.org/10.1021/es1016735
Black A, Wakelin S, Hamonts K, Gerard E, Condron L (2019) Impacts of long term copper exposure on abundance of nitrogen cycling genes and denitrification activity in pasture soils. Appl Soil Ecol 138:253–261. https://doi.org/10.1016/j.apsoil.2019.03.009
Bollmann A, Conrad R (1998) Influence of O2 availability on NO and N2O release by nitrification and denitrification in soils. Glob Chang Biol 4(4):387–396. https://doi.org/10.1046/j.1365-2486.1998.00161.x
Braker G, Zhou JZ, Wu LY, Devol AH, Tiedjen JM (2000) Nitrite reductase genes (nirK and nirS) as functional markers to investigate diversity of denitrifying bacteria in Pacific Northwest marine sediment communities. Appl Environ Microbiol 66(5):2096–2104. https://doi.org/10.1128/AEM.66.5.2096-2104.2000
Burgos M, Sierra A, Ortega T, Forja JM (2015) Anthropogenic effects on greenhouse gas (CH4 and N2O) emissions in the Guadalete River Estuary (SW Spain). Sci Total Environ 503–504:179–189
Chapin FS, Matson PA, Vitousek PM (2011) Principles of terrestrial ecosystem ecology, 2nd edn. Springer, New York
Chen LM, Liu ST, Chen Q, Zhu GB, Wu X, Wang JW, Li XF, Hou LJ, Ni JR (2019) Anammox response to natural and anthropogenic impact over the Yangtze River. Sci Total Environ 665:171–180. https://doi.org/10.1016/j.scitotenv.2019.02.096
Chen NW, Wu JZ, Hong HS (2011) Preliminary results concerning summer-time denitrification in the Jiulong River Estuary. Environ Sci 32:3229–3234
Clough TJ, Bertram JE, Sherlock RR, Leonard RL, Nowicki BL (2006) Comparison of measuredand EF5-rderived N2O fluxes from a spring-fed rive. Glob Chang Biol 12(3):477–488. https://doi.org/10.1111/j.1365-2486.2005.01092.x
Cocco E, Bertora C, Squartini A, Delle Vedove G, Berti A, Grignani C, Lazzaro B, Morari F (2018) How shallow water table conditions affect N2O emissions and associated microbial abundances under different nitrogen fertilisations. Agric Ecosyst Environ 261:1–11. https://doi.org/10.1016/j.agee.2018.03.018
Cole JJ, Caraco NF (1998) Atmospheric exchange of carbon dioxide in a low-wind oligotrophic lake measured by the addition of SF6. Limnol Oceanogr 43(4):647–656. https://doi.org/10.4319/lo.1998.43.4.0647
Cole JJ, Caraco NF (2001) Emissions of nitrous oxide (N2O) from a tidal, freshwater river, the Hudson River, New York. Environ Sci Technol 35(6):991–996. https://doi.org/10.1021/es0015848
Crusius J, Wanninkhof R (2003) Gas transfer velocities measured at low wind speed over a lake. Limnol Oceanogr 48(3):1010–1017. https://doi.org/10.4319/lo.2003.48.3.1010
Deng FY, Hou LJ, Liu M, Zheng YL, Yin GY, Li XF, Lin XB, Chen F, Gao J, Jiang XF (2015) Dissimilatory nitrate reduction processes and associated contribution to nitrogen removal in sediments of the Yangtze Estuary. J Geophys Res Biogeosci 120(8):1521–1531. https://doi.org/10.1002/2015JG003007
Dong LF, Nedwell DB, Colbeck I, Finch J (2004) Nitrous oxide emission from some English and Welsh rivers and estuaries. Water Air Soil Pollut Focus 4:127–134. https://doi.org/10.1007/s11267-004-3022-4
Fan Y, Chen J, Shirkey G, John R, Wu R, Park H, Shao C (2016) Applications of structural equation modeling (SEM) in ecological research: an updated review. Ecol Process 5:19. https://doi.org/10.1186/s13717-016-0063-3
Feng J, Xu X, Wu JJ, Zhang Q, Zhang DD, Li QX, Long CY, Chen Q, Chen JW, Cheng XL (2018) Inhibited enzyme activities in soil macroaggregates contribute to enhanced soil carbon sequestration under afforestation in central China. Sci Total Environ 640–641:653–661
Firestone MK, Davidson EA (1989) Microbiological basis of NO and N2O production and consumption in soil. In: Andreae MO, Schimel DS (eds) Exchange of trace gases between terrestrial ecosystems and the atmosphere. Wiley, New York, pp 7–21
García-Ruiz R, Pattinson SN, Whitton BA (1999) Nitrous oxide production in the river Swale-Ouse, North-East England. Water Res 33(5):1231–1237. https://doi.org/10.1016/S0043-1354(98)00324-8
Gardner JR, Fisher TR, Jordan TE, Knee KL (2016) Balancing watershed nitrogen budgets: accounting for biogenic gases in streams. Biogeochemistry 127(2-3):231–253. https://doi.org/10.1007/s10533-015-0177-1
Garnier J, Billen G, Vilain G, Martinez A, Silvestre M, Mounier E, Toche F (2009) Nitrous oxide (N2O) in the Seine river and basin: observations and budgets. Agric Ecosyst Environ 133(3-4):223–233. https://doi.org/10.1016/j.agee.2009.04.024
Hallam SJ, Mincer TJ, Schleper C, Preston CM, Roberts K, Richardson PM, DeLong EF (2006) Pathways of carbon assimilation and ammonia oxidation suggested by environmental genomic analyses of marine Crenarchaeota. PLoS Biol 4(4):e95. https://doi.org/10.1371/journal.pbio.0040095
Hansen AT, Dolph CL, Finlay JC (2016) Do wetlands enhance downstream denitrification in agricultural landscapes? Ecosphere 7(10):e01516. https://doi.org/10.1002/ecs2.1516
Harrison J, Matson P (2003) Patterns and controls of nitrous oxide emissions from waters draining a subtropical agricultural valley. Glob Biogeochem Cycles 17(3):1081
Harrison JA, Matson PA, Fendorf SE (2005) Effects of a diel oxygen cycle on nitrogen transformations and greenhouse gas emissions in a eutrophied subtropical stream. Aquat Sci 67(3):308–315
Harrison MD, Groffman PM, Mayer PM, Kaushal SS, Newcomer TA (2011) Denitrification in alluvial wetlands in an urban landscape. J Environ Qual 40(2):634–646
Hasegawa K, Hanaki K, Matsuo T, Hidaka S (2000) Nitrous oxide from the agricultural water system contaminated with high nitrogen. Chemosphere Global Change Sci 2(3-4):335–345. https://doi.org/10.1016/S1465-9972(00)00009-X
Herbert RA (1999) Nitrogen cycling in coastal marine ecosystems. FEMS Microbiol Rev 23(5):563–590. https://doi.org/10.1111/j.1574-6976.1999.tb00414.x
Holmes RM, Jones JB Jr, Fisher SG, Grimm NB (1996) Denitrification in a nitrogen limited stream ecosystem. Biogeochemistry 33(2):125–146. https://doi.org/10.1007/BF02181035
Hou LJ, Zheng YL, Liu M, Gong J, Zhang XL, Yin GY, You L (2013) Anaerobic ammonium oxidation (anammox) bacterial diversity, abundance, and activity in marsh sediments of the Yangtze Estuary. J Geophys Res-Biogeosci 118(3):1237–1246
Hou LJ, Zheng YL, Liu M, Li XF, Lin XB, Yin GY, Gao J, Deng FY, Chen F, Jiang XF (2015) Anaerobic ammonium oxidation and its contribution to nitrogen removal in China’s coastal wetlands. Sci Rep 5(1):15621. https://doi.org/10.1038/srep15621
Hu M, Chen D, Dahlgren RA (2016) Modeling nitrous oxide emission from rivers: a global assessment. Glob Chang Biol 22(11):3566–3582. https://doi.org/10.1111/gcb.13351
Huang BQ, Liu Q, Li RF, Cao WH, Zhong JF (2012) Impacts of land use and land cover change on river. J Anhui Agric Sci 40:11073–11076
Ikeda E, Andou S, Iwama U, Kato C, Horikoshi K, Tamegai H (2009) Physiological roles of two dissimilatory nitrate reductases in the deep-sea denitrifier Pseudomonas sp. strain MT-1. Biosci Biotechnol Biochem 73(4):896–900. https://doi.org/10.1271/bbb.80833
Inwood SE, Tank JL, Bernot MJ (2007) Factors controlling sediment denitrification in midwestern streams of varying landuse. Microb Ecol 53(2):247–258. https://doi.org/10.1007/s00248-006-9104-2
IPCC (2006) IPCC Guidelines for National Greenhouse Gas Inventories, Prepared by the National Greenhouse Gas Inventories Programme. In: Eggleston HA, Buendia L, Miwa K (eds) Institute for Global Environmental Strategies. IPCC/IGES, Hayama, Kanagawa, Japan
Johnson KM, Hughes JE, Donaghay PL, Sieburth JM (1990) Bottle-calibration static head space method for the determination of methane dissolved in seawater. Anal Chem 62(21):2408–2412. https://doi.org/10.1021/ac00220a030
Jung SP, Kim YJ, Kang H (2014) Denitrification rates and their controlling factors in streams of the Han River Basin with different land-use patterns. Pedosphere 24(4):516–528. https://doi.org/10.1016/S1002-0160(14)60038-2
Kelso BHL, Smith RV, Laughlin RJ, Lennox SD (1997) Dissimilatory nitrate reduction in anaerobic sediments leading to river nitrite accumulation. Appl Environ Microbiol 63:4679–4685
Kim IN, Lee K, Gruber N, Karl DM, Bullister JL, Yang S, Kim TW (2014) Increasing anthropogenic nitrogen in the North Pacific Ocean. Science 346(6213):1102–1106. https://doi.org/10.1126/science.1258396
Koike I, Terauchi K (1996) Fine scale distribution of nitrous oxide in marine sediments. Mar Chem 52(3-4):185–193. https://doi.org/10.1016/0304-4203(95)00079-8
Kowalchuk GA, Stienstra AW, Heilig GHJ, Stephen JR, Woldendorp JW (2000) Molecular analysis of ammonia-oxidising bacteria in soil of successional grasslands of the Drentsche A (the Netherlands). FEMS Microbiol Ecol 31(3):207–215. https://doi.org/10.1111/j.1574-6941.2000.tb00685.x
Liikanen A, Martikainen P (2003) Effect of ammonium and oxygen on the methane and nitrous oxide fluxes across sediment-water interface in a eutrophic lake. Chemosphere 52(8):1287–1293. https://doi.org/10.1016/S0045-6535(03)00224-8
Liu B, Mørkved PT, Frostegård Å, Bakken LR (2010) Denitrification gene pools, transcription and kinetics of NO, N2O and N2 production as affected by soil pH. FEMS Microbiol Ecol 72(3):407–417. https://doi.org/10.1111/j.1574-6941.2010.00856.x
Liu C, Hou LJ, Liu M, Zheng YL, Yin GY, Ping H, Dong HP, Gao J, Gao DZ, Chang KK, Zhang ZX (2019) Coupling of denitrification and anaerobic ammonium oxidation with nitrification in sediments of the Yangtze Estuary: Importance and controlling factors. Estuar Coast Shelf Sci 220:64–72. https://doi.org/10.1016/j.ecss.2019.02.043
Liu WZ, Yao L, Wang Z, Xiong ZQ, Liu GH (2015) Human land uses enhance sediment denitrification and N2O production in Yangtze lakes primarily by influencing lake water quality. Biogeosciences 12(20):6059–6070. https://doi.org/10.5194/bg-12-6059-2015
Liu XL, Liu CQ, Li SL, Wang FS, Wang BL, Wang ZL (2011b) Spatiotemporal variations of nitrous oxide (N2O) emissions from two reservoirs in SW China. Atmos Environ 45(31):5458–5468. https://doi.org/10.1016/j.atmosenv.2011.06.074
Liu Y, Zhu R, Ma D, Xu H, Luo Y, Huang T, Sun L (2011a) Temporal and spatial variations of nitrous oxide fluxes from the littoral zones of three alga-rich lakes in coastal Antarctica. Atmos Environ 45(7):1464–1475. https://doi.org/10.1016/j.atmosenv.2010.12.017
Ma P, Li XY, Wang HX, Wang JN, Yan WJ (2014) Denitrification and its role in cycling and removal of nitrogen in River. J Agro-Environ Sci 33:623–633
Ma ST, Shan J, Yan XY (2017) N2O emissions dominated by fungi in an intensively managed vegetable field converted from wheat-rice rotation. Appl Soil Ecol 116:23–29. https://doi.org/10.1016/j.apsoil.2017.03.021
Marzadri A, Dee MM, Tonina D, Bellin A, Tank JL (2017) Role of surface and subsurface processes in scaling N2O emissions along riverine networks. Proc Natl Acad Sci 114(17):4330–4335. https://doi.org/10.1073/pnas.1617454114
McMahon PB, Dennehy KF (1999) N2O emission from a nitrogen enriched river. Environ Sci Technol 33(1):21–25. https://doi.org/10.1021/es980645n
Morse JL, Ardón M, Bernhardt ES (2012) Using environmental variables and soil processes to forecast denitrification potential and nitrous oxide fluxes in coastal plain wetlands across different land uses. J Geophys Res-Biogeosci 117:G02023
Mosier A, Kroeze C, Nevison C, Oenema O, Seitzinger S, Cleemput OV (1998) Closing the global N2O budget: nitrous oxide emissions through the agricultural nitrogen cycle. Nutr Cycl Agroecosyst 52(2/3):225–248. https://doi.org/10.1023/A:1009740530221
Müller B, Lotter AF, Sturm M, Ammann A (1998) Influence of catchment quality and altitude on the water and sediment composition of 68 small lakes in central Europe. Aquat Sci 60:316–337
Musenze RS, Werner U, Grinham A, Udy J, Yuan Z (2014) Methane and nitrous oxide emissions from a subtropical estuary (the Brisbane River estuary, Australia). Sci Total Environ 472:719–729. https://doi.org/10.1016/j.scitotenv.2013.11.085
Musenze RS, Werner U, Grinham A, Udy J, Yuan Z (2015) Methane and nitrous oxide emissions from a subtropical coastal embayment (Moreton Bay, Australia). J Environ Sci 29:82–96. https://doi.org/10.1016/j.jes.2014.06.049
Naqvi SWA, Jayakumar DA, Narvekar PV, Naik H, Sarma VVSS, D'Souza W, Joseph S, George MD (2000) Increased marine production of N2O due to intensifying anoxia on the Indian continental shelf. Nature 408(6810):346–349. https://doi.org/10.1038/35042551
Nie YX, Li L, Wang MC, Tahvanainen T, Hashidoko Y (2015) Nitrous oxide emission potentials of Burkholderia species isolated from the leaves of a boreal peat moss Sphagnum fuscum. Biosci Biotechnol Biochem 79(12):2086–2095. https://doi.org/10.1080/09168451.2015.1061420
Nie YXLL, Isoda R, Wang MC, Hatano R, Hashidoko Y (2016) Physiological and genotypic characteristics of nitrous oxide (N2O)-emitting Pseudomonas species isolated from dent corn Andisol farmland in Hokkaido, Japan. Microbes Environ 31:93–103
Philippot L, Spor A, Hénault C, Bru D, Bizouard F, Jones CM, Sarr A, Maron PA (2013) Loss in microbial diversity affects nitrogen cycling in soil. ISME J 7(8):1609–1619
Quick AM, Reeder WJ, Farrell TB, Tonina D, Benner SG (2019) Nitrous oxide from streams and rivers: a review of primary biogeochemical pathways and environmental variables. Earth-Sci Rev 191:224–262. https://doi.org/10.1016/j.earscirev.2019.02.021
Reay DS, Smith KA, Edwards AC (2003) Nitrous oxide emission from agricultural drainage waters. Glob Chang Biol 9(2):195–203. https://doi.org/10.1046/j.1365-2486.2003.00584.x
Rosamond MS, Thuss SJ, Schiff SL (2012) Dependence of riverine nitrous oxide emissions on dissolved oxygen levels. Nat Geosci 5(10):715–718. https://doi.org/10.1038/ngeo1556
Rosamond MS, Thuss SJ, Schiff SL, Elgood RJ (2011) Coupled cycles of dissolved oxygen and nitrous oxide in rivers along a trophic gradient in southern Ontario, Canada. J Environ Qual 40(1):256–270. https://doi.org/10.2134/jeq2010.0009
Schade JD, Bailio J, McDowell WH (2016) Greenhouse gas flux from headwater streams in New Hampshire, USA: patterns and drivers. Limnol Oceanogr 61(S1):S165–S174. https://doi.org/10.1002/lno.10337
Schermelleh-Engel K, Moosbrugger H, Müller H (2003) Evaluating the fit of structural equation models: tests of significance and descriptive goodness-of-fit measures. Method Psychol Res 8:23–74
Seitzinger SP, Kroeze C (1998) Global distribution of nitrous oxide production and N inputs in freshwater and coastal marine ecosystems. Glob Biogeochem Cycles 12(1):93–113. https://doi.org/10.1029/97GB03657
Sigleo AC (2019) Denitrification rates across a temperate North Pacific Estuary, Yaquina Bay, Oregon. Estuar Coasts 42(3):655–664
Smith CJ, Dong LF, Wilson J, Stott A, Osborn AM, Nedwell DB (2015) Seasonal variation in denitrification and dissimilatory nitrate reduction to ammonia process rates and corresponding key functional genes along an estuarine nitrate gradient. Front Microbiol 6:542
Soued C, del Giorgio PA, Maranger R (2015) Nitrous oxide sinks and emissions in boreal aquatic networks in Québec. Nat Geosci 9:1–7
Sponseller RA, Benfield EF, Valett HM (2001) Relationships between land use, spatial scale and stream macroinvertebrate communities. Freshw Biol 46(10):1409–1424. https://doi.org/10.1046/j.1365-2427.2001.00758.x
Starry OS, Valett HM, Schreiber ME (2005) Nitrification rates in a headwater stream: influences of seasonal variation in C and N supply. J North Am Benthol Soc 24(4):753–768. https://doi.org/10.1899/05-015.1
Stocker TF, Qin D, Plattner GK, Tignor M, Allen SK, Boschung J, Nauels A, Xia Y, Bex V, Midgley PM (2013) Climate Change 2013: The Physical Science Basis. Contribution of Working Group I to the Fifth Assessment Report of the Intergovernmental Panel on Climate Change. Cambridge University Press, Cambridge, United Kingdom and New York
Voigt C, Marushchak ME, Lamprecht RE, Jackowicz-Korczyński M, Lindgren A, Mastepanov M, Granlund L, Christensen TR, Tahvanainene T, Martikainena PJ, Biasi C (2017) Increased nitrous oxide emissions from Arctic peatlands after permafrost thaw. Proc Natl Acad Sci 114(24):6238–6243. https://doi.org/10.1073/pnas.1702902114
Walter S, Peeken I, Lochte K, Webb A, Bange HW (2005) Nitrous oxide measurements during EIFEX, the European iron fertilization experiment in the subpolar South Atlantic Ocean. Geophys Res Lett 32(23):L23613. https://doi.org/10.1029/2005GL024619
Wang J, Yuan J, Tan X, Li SY, Zhang QF (2015) Stable isotope composition of particulate organic matters and dissolved nitrate in the Jinshui river, upper Han river basin. Acta Ecol Sin 35:7338–7346
Wang JN, Yan WJ, Chen NW, Wang B, Yang LB (2012) Variations of river N2O saturations and emission factors in relation to nitrogen levels in China. J Agro-Environ Sci 31:1576–1585
Wang SL, Liu CQ, Yeager KM, Wan GJ, Li J, Tao FX (2009) The spatial distribution and emission of nitrous oxide (N2O) in a large eutrophic lake in eastern China: anthropogenic effects. Sci Total Environ 407(10):3330–3337. https://doi.org/10.1016/j.scitotenv.2008.10.037
Wang XM, Hu MJ, Ren HC, Li JB, Tong C, Musenze RS (2018) Seasonal variations of nitrous oxide fluxes and soil denitrification rates in subtropical freshwater and brackish tidal marshes of the Min River estuary. Sci Total Environ 616-617:1404–1413. https://doi.org/10.1016/j.scitotenv.2017.10.175
Wanninkhof R (1992) Relationship between wind-speed and gas-exchange over the ocean. J Geophys Res Oceans 97(C5):7373–7382. https://doi.org/10.1029/92JC00188
Wanninkhof R (2014) Relationship between wind speed and gas exchange over the ocean revisited. Limnol Oceanogr-Meth 12(6):351–362. https://doi.org/10.4319/lom.2014.12.351
Weathers PJ (1984) N2O evolution by green algae. Appl Environ Microbiol 48(6):1251–1253. https://doi.org/10.1128/AEM.48.6.1251-1253.1984
Webster JR, Mulholland PJ, Tank JL, Valett HM, Dodds WK, Peterson BJ, BowdenWB DCN, Findlay S, Gregory SV, Grimm NB, Hamilton SK, Johnson SL, Martí E, Mcdowell WH, Meyer JL, Morrall DD, Thomas SA, Wollheim WM (2003) Factors affecting ammonium uptake in streams: an inter-biome perspective. Freshw Biol 48(8):1329–1352. https://doi.org/10.1046/j.1365-2427.2003.01094.x
Wyman M, Hodgson S, Bird C (2013) Denitrifying alphaproteo bacteria from the Arabian sea that express nosZ, the gene encoding nitrous oxide reductase, in oxic and suboxic waters. Appl Environ Microbiol 79(8):2670–2681. https://doi.org/10.1128/AEM.03705-12
Xiong ZQ (2018) Vegetation characteristics and soil denitrification of reservoir shorelines and riparian wetlands in the Han River, China. Wuhan Botanical Garden, Chinese Academy of Science, Wuhan
Xu HX, Jiang XY, Yao XL, Lu Z (2016) Characteristics of nitrous oxide (N2O) emissions and the related factors in Lake Poyang. J Lake Sci 28:972–981
Yan WJ, Laursen AE, Wang F, Sun P, Seitzinger SP (2004) Measurement of denitrification in the Changjiang River. Environ Chem 1(2):95–98. https://doi.org/10.1071/EN04031
Yang LB, Lei K (2018) Effects of land use on the concentration and emission of nitrous oxide in nitrogen-enriched rivers. Environ Pollut 238:379–388
Yang LB, Lei K, Meng W (2015) Denitrification in water of Daliao River estuary in summer and the effect of environmental factors. Environ Sci 36:905–913
Yang LB, Wang F, Yan WJ (2013) N2O flux across sediments-water interface and its contribution to dissolved N2O in the Chao Lake tributaries, China. J Agro-Environ Sci 32(4):771–777
Zhang KR, Dang HS, Tan SD, Wang ZX, Zhang QF (2010) Vegetation community and soil characteristics of abandoned agricultural land and pine plantation in the Qinling Mountains, China. For Ecol Manag 259(10):2036–2047. https://doi.org/10.1016/j.foreco.2010.02.014
Zhang KR, Zhang YL, Tian H, Chemg XL, Dang HS, Zhang QF (2013) Sustainability of social–ecological systems under conservation projects: lessons from a biodiversity hotspot in western China. Biol Conserv 158:205–213. https://doi.org/10.1016/j.biocon.2012.08.021
Zhao BJ, Wang X, Zhang J, Tan X, He R, Zhou Q, Shi H, Zhang QF (2020) Influence factors of potential nitrification rates and functional genes abundance in the Jinshui River and the Qihe River of the Han River basin. Environ Sci 41:5419–5427
Zhao J, Zhang GL, Wu Y, Zhang J (2009) Distribution and emission of nitrous oxide from the Changjiang River. Acta Sci Circumst 29:1995–2002
Zheng LZ, Cardenas MB, Wang LC (2016) Temperature effects on nitrogen cycling and nitrate removal-production efficiency in bed form-induced hyprorheic zones. J Geophys Res Biogeosci 121(4):1086–1103. https://doi.org/10.1002/2015JG003162
Zheng YL, Hou LJ, Liu M, Yin GY (2019) Dynamics and environmental importance of anaerobic ammonium oxidation (anammox) bacteria in urban river networks. Environ Pollut 254(Pt A):112998. https://doi.org/10.1016/j.envpol.2019.112998
The authors sincerely appreciate Li XS, Wang Y, and Zhang J of Key Laboratory of Aquatic Botany and Watershed Ecology for their assistance with sampling in the field.
National Natural Science Foundation of China (Nos. 32030069, 31720103905).
Ethics approval and consent to participate
Consent for publication
The authors declare that they have no competing interests.
Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.
amoA genes abundance in the Jinshui River and Qi River. Vertical bar denote SE of triplicate samples (Zhao et al. 2020). The genes primers were shown in Table S7. Fig. S2. nirK gene abundance in the Jinshui River and Qi River. Vertical bar denote SE of triplicate samples (The data have not yet been published). The measured method was the same as amoA genes. The gene primer was shown in Table S7. Fig. S3. nirS genes abundance in the Jinshui River and Qi River. Vertical bar denote SE of triplicate samples (The data have not yet been published). The measured method was the same as amoA genes. The gene primer was shown in Table S7. Fig. S4. nosZ genes abundance in the Jinshui River and Qi River. Vertical bar denote SE of triplicate samples (The data have not yet been published). The measured method was the same as amoA genes. The gene primer was shown in Table S7. Fig. S5. Potential nitrification rates in the Jinshui River and Qi River. Vertical bar denote SE of triplicate samples (Zhao et al. 2020). Fig. S6. Potential nitrification rates in the Jinshui River and Qi River. Vertical bar denote SE of triplicate samples (The data have not yet been published). Table S1. The land use attribute table of the Jinshui River and Qi River. Table S2. Wind speed (m/s) at 2 m above water surface of Jinshui River and Qi River. Table S3. Pearson’s correlation analyses between N2O concentration and physicochemical variables. * represent P < 0.05, **represent P< 0.01. Table S4. Pearson’s correlation analyses between nitrogen transformation genes abundance (n = 54). Table S5. Pearson’s correlation analyses between N2O concentration, functional genes abundance, nitrification and denitrfication rates (n = 54). * represent P < 0.05. Table S6. Total, direct, and indirect effects of explanatory variables on N2O concentration. Table S7. The primers and primer sequences of functional genes qPCR.
About this article
Cite this article
Zhao, B., Zhang, Q. N2O emission and its influencing factors in subtropical streams, China. Ecol Process 10, 54 (2021). https://doi.org/10.1186/s13717-021-00307-3
- N2O concentration
- N2O saturation
- N2O flux
- N2O emission factor