CN116306361A - Rural river nitrogen interception capability assessment method for plain river network area - Google Patents
Rural river nitrogen interception capability assessment method for plain river network area Download PDFInfo
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Abstract
The invention relates to a method for evaluating rural River nitrogen interception capability of a plain River network area, aiming at the problem of unclear rural River nitrogen interception capability of the plain River network area, developing a River nitrogen circulation model (River-N) which covers aquatic plants and bio-geochemical circulation, coupling an existing River network three-dimensional hydrodynamic model (EFDC) and a River network nitrogen circulation model (NDP), simulating the input, output and migration conversion processes of three forms of nitrogen (granular nitrogen, ammonia nitrogen and nitrate nitrogen) of a rural River, ascertaining a source and sink balance rule of nitrogen, and quantitatively evaluating the rural River nitrogen interception capability of the plain River network area. The invention combines the simulation technologies of river network hydrodynamic force, bio-geochemical circulation, water and nitrogen loss in the polder region and the like, fully considers the unique rule of slow river flow and wide distribution of aquatic plants in rural river in the plain river network region, breaks through the problem of accurate estimation of the interception of the rural river nitrogen in the plain river network region, and can provide technical support for the pollution control and management of the rural river nitrogen in the plain river network region.
Description
Technical Field
The invention belongs to the technical field of water environment health evaluation, and particularly relates to a method for evaluating plain rural river nitrogen interception capability by combining a multi-scale model.
Background
The plain river network area is widely distributed in the downstream of rivers in all parts of the world, such as the Yangtze river, the Mei-Gong river, the majority of the Netherlands, and the like, and has the characteristics of flat topography, longitudinal and transverse river, high development of river network, wide polder area, great influence by human activities, and the like. The method is influenced by human agricultural production and life, the problem of nitrogen pollution in plain river network areas is very remarkable, the water environment quality of the areas is seriously influenced, and even water eutrophication and cyanobacteria bloom are caused; there is currently a great deal of research devoted to searching for patterns of regional water nitrogen abatement where rural rivers are considered "capillaries" of plain river network areas with significant nitrogen interception potential. However, the activity intensity of human beings around rural rivers in plain river network areas is high, nitrogen sources are numerous (farmland drainage in the levee area, water exchange in surrounding fishponds, and surrounding river convergence and the like), migration and transformation processes are complex, so that the difficulty of finely evaluating the nitrogen interception capability is high, and the difficulty to be solved in nitrogen pollution prevention and control practice is urgent.
The hydrodynamic-water quality model (MIKE 11, EFDC and the like) can systematically simulate the migration and transformation rules of river nitrogen, and is an important method for evaluating the river nitrogen interception capability at present; however, the method lacks consideration of the components of the macrophytes, and cannot realize the bio-geochemical circulation of nitrogen with different forms under the action of the macrophytes, so that the method is not suitable for rural rivers in plain river network areas where the macrophytes are dense, and development of a new technical method is needed.
Disclosure of Invention
The invention aims to fill the blank of the prior art, develop a River nitrogen circulation model (River-N) covering the circulation of aquatic plants and bio-geochemistry, couple the existing River network three-dimensional hydrodynamic model (EFDC) and the polder area nitrogen circulation model (NDP), and finely simulate the processes of nitrogen source and sink, absorption and detention and the like to form the nitrogen interception capability assessment method applicable to rural rivers in plain River network areas.
In order to achieve the above purpose, the invention adopts the following technical scheme:
the method for evaluating the rural river nitrogen interception capability of the plain river network area is characterized by comprising the following steps of:
simulating water volume exchange of rural rivers and peripheral rivers in plain river network areas based on a three-dimensional hydrodynamic model (EFDC), namely water body input and output of the rural rivers and the peripheral rivers in the plain river network areas;
simulating the water body and nitrogen exchange flux of rural rivers and polder areas in plain river network areas based on a polder area nitrogen circulation model (NDP), namely the influence of the processes of water pumping irrigation, flood drainage, culvert water diversion and the like in the polder areas on the river nitrogen circulation process; the nitrogen comprises granular nitrogen, ammonia nitrogen and nitrate nitrogen;
establishing a River nitrogen circulation model (River-N) covering aquatic plants and bio-geochemical circulation, a control equation of the River nitrogen circulation model comprising an aquatic plant elimination process;
and determining boundary conditions (main river channel afflux, foreign region and river material exchange and the like) of the river according to simulation results of the three-dimensional hydrodynamic model and the foreign region nitrogen circulation model, inputting the boundary conditions into the river nitrogen circulation model, simulating daily dynamic changes of nitrogen in rural rivers in plain river network regions, and evaluating rural river nitrogen interception capability in plain river network regions.
The method of the invention is based on a three-dimensional hydrodynamic model, and the specific process of simulating the water exchange between rural rivers and peripheral rivers in plain river network areas comprises the following steps:
collecting meteorological hydrologic monitoring data, wherein the meteorological data comprise daily data such as solar radiation, rainfall and the like, and the hydrologic data comprise daily data such as river water level and the like;
carding complex river network water systems in plain river network areas, and designing generalized modes of river grids and sections, namely determining the size and the shape of grid units, and taking the grid units as minimum basic calculation units in a three-dimensional hydrodynamic model;
the type and input mode of the boundary condition of the model are defined, the collected time series monitoring data are input, and the spatial resolution and time step size suitable for the model are tested and screened;
and (3) designing a simulation scene of typical meteorological hydrologic conditions, simulating the water flow direction of the grid unit, and accounting the water quantity exchange between the river and the peripheral river network.
The water quantity exchange and nitrogen exchange flux of the rural river and the polder region of the plain river network region based on the NDP polder region nitrogen circulation model comprises the following steps:
depending on a nitrogen circulation model (NDP) of the polder region, designing a parameterized characterization method for manually regulating and controlling a hydrologic process of the polder region, and simulating and describing uniqueness of the hydrologic-nitrogen circulation process of the polder region, wherein the uniqueness comprises nitrogen migration and conversion of 'tetrawater' (atmospheric water, surface water, soil water and underground water) nitrogen under hydrologic drive, gate pumping and drainage and nitrogen interception of a ditch and pond;
and quantitatively evaluating the exchange flux of water and nitrogen between the polder area and the river, wherein the exchange flux comprises the water pumping irrigation quantity, the flood drainage quantity and the culvert water diversion quantity of the polder area, and simultaneously determining the nitrogen exchange quantity brought by the water exchange.
The levee region refers to a relatively closed artificial water collecting unit formed by the embankment and reclamation of a plains easy waterlogging region at the downstream of a river basin, namely a broken river basin of a plains river network region, which is widely distributed in the coastal regions of the Yangtze river, the Mei-Gong river, the Rhine river, the Polynaite river, the Mitsubishi river and other global large rivers, wherein the distribution of the plain river network region of the Taihu river basin is particularly wide; the nitrogen comprises three forms of nitrogen (granular nitrogen, ammonia nitrogen and nitrate nitrogen), the total nitrogen is the total concentration of the three forms of nitrogen, and the concentration unit adopts mg/L.
Because the characteristic that the large-scale aquatic plants are widely distributed in the rural River in plain identifies the key process affecting the interception of the River nitrogen, the invention focuses on the interception of the River nitrogen by the large-scale aquatic plants, designs a River nitrogen circulation model (River-N) which covers the water plants and the bio-geochemical circulation, quantitatively simulates the multiscale processes such as River hydrodynamic force, water-soil and water-air interface nitrogen exchange, nitrogen bio-geochemical process, growth and death of the large-scale aquatic plants and the like, and covers the key process of the interception of the River nitrogen; the water-soil-water-gas interface nitrogen exchange comprises the processes of upward water covering release of nitrogen caused by concentration difference of bottom mud and interstitial water, re-suspension of granular nitrogen caused by water disturbance, natural sedimentation of the granular nitrogen and the like; the nitrogen bio-geochemical process comprises the processes of conversion between nitrogen in different forms such as nitrification, denitrification and the like, nitrogen absorption of aquatic plants and the like. The river nitrogen circulation model of the present invention increases generalization of influence of aquatic plants on river nitrogen circulation compared with a mainstream model of a river (MIKE 21, etc.), and includes: the aquatic plant growing and extinguishing process and the like, and improves the applicability of the model in widely distributing large-scale aquatic plant rivers.
The model (River-N) describes mainly the migration and conversion of three forms of nitrogen; wherein the nitrate nitrogen source mainly comprises nitrification and atmospheric sedimentation of the water body. The ammonia nitrogen source mainly comprises atmospheric sedimentation, substrate release, plant spoilage and mineralization; the particulate nitrogen source mainly comprises atmospheric sedimentation, plant spoilage, assimilation and particulate nitrogen re-suspension in the substrate.
The interception capability of the rural river in the plain river network area on nitrogen refers to the detention flux of the river on nitrogen, and the detention capability comprises natural sedimentation, denitrification, aquatic plant absorption and the like.
As a preferred embodiment of the scheme, the control equation describing the aquatic plant elimination process is as follows:
BSH T ＝BSH T-ΔT +((1-K STR )k SHOOTGrow f Uptake f PLT -K SHOOTDec f SHOOTDecT )BSH T
BRO T ＝BRO T-ΔT +K STR K SHOOTGrow f Uptake f PLT BSH T -K ROOTDec f ROOTDecT BRO T
wherein T represents time, deltaT represents time step, BSH T Representing the biomass of the overground parts of aquatic plants, K STR Represents the proportion of the aquatic plant transferred to the root system on the ground, k SHOOTGrow Indicating the maximum growth rate of the overground parts of the aquatic plants under the optimal condition, f Uptake Represents the nitrogen limitation of absorption by aquatic plants, f PLT Indicating the temperature limit of aquatic plant growth, K SHOOTDec Indicating the maximum growth rate of the overground parts of the aquatic plants under the optimal condition, f SHOOTDecT Temperature limitation indicating decay of aerial parts of aquatic plants, BRO T KH, which represents biomass of underground parts of aquatic plants Uptake Represents the half-saturation constant, K, of nitrogen absorption by aquatic plants ROOTDec Represents the metabolic rate of the root system at the reference temperature, f ROOTDecT Temperature limit, NH, indicative of root rot of aquatic plants T Represents the ammonia nitrogen concentration of surface water, NO T Represents the nitrate nitrogen concentration, theta PL Indicating the effect of temperature on the growth of the aquatic plants,
represents the surface water temperature, T PL1 、T PL2 Represents the optimal lower limit and upper limit of the temperature, theta, suitable for the growth of aquatic plants SHOOTDec Indicating the effect of temperature on the metabolic rate of the aerial parts of the aquatic plants,/->
Represents the daily average water temperature, theta ROOTDec The effect of temperature on the metabolic rate of the root system of the aquatic plant is shown.
As a preferable implementation mode of the scheme, the horizontal direction coordinate reference of the three-dimensional hydrodynamic model is rectangular coordinate or orthogonal curve coordinate, staggered grid dispersion is adopted in space, and the time integration adopts a second-order precision finite difference method to combine an internal and external mode splitting technology, namely an internal module of shear stress or oblique pressure and an external mold of free surface gravitational wave or positive pressure are adopted for quick separation calculation; the outer module adopts a semi-implicit calculation method, allows a larger time step, can adopt a self-adaptive time step mode, and the inner module adopts a vertical diffusion implicit format, and the amphibious beach area adopts a dry-wet grid technology.
The weather monitoring data refer to indexes such as daily rainfall, daily average air temperature, daily highest air temperature, daily lowest air temperature, daily average humidity and the like, the hydrologic monitoring data refer to water levels, and the water quality monitoring data refer to indexes such as total nitrogen, granular nitrogen, ammonia nitrogen, nitrate nitrogen and the like.
As a preferable implementation mode of the scheme, the method further comprises the steps of performing model verification based on measured meteorological, hydrological and water quality monitoring data, calibrating model parameters and improving model simulation accuracy.
Furthermore, the model verification is to identify key parameters of the model by adopting a global sensitivity analysis method MOAT (Morris one at a time), construct an intelligent optimization mode (genetic algorithm combined with super Latin square sampling) of the model parameters, obtain an optimal parameter set of the model, and improve the simulation precision of the model.
Further, based on measured meteorological, hydrological and water quality monitoring data, comparing simulation values and measured values of indexes such as total nitrogen, granular nitrogen, ammonia nitrogen and nitrate nitrogen, and quantitatively evaluating simulation effects of the model by adopting Nash-Sutcliffe efficiency efficiency coefficient; the weather monitoring data refer to indexes such as daily rainfall, daily average air temperature, daily highest air temperature, daily lowest air temperature, daily average humidity and the like, the hydrologic monitoring data refer to water levels, and the water quality monitoring data refer to indexes such as total nitrogen, granular nitrogen, ammonia nitrogen, nitrate nitrogen and the like.
As a preferred embodiment of the scheme, the rural river nitrogen interception capability of the plain river network area is evaluated based on the detention flux of nitrogen from the river.
Further, the detention flux of the river to nitrogen comprises quantized process fluxes of natural sedimentation, denitrification, anaerobic ammoxidation and aquatic plant absorption of granular nitrogen.
The invention combines the simulation technologies of River network hydrodynamic force, bio-geochemical circulation, water and nitrogen loss in a polder region and the like, and combines the existing River network three-dimensional hydrodynamic model (EFDC) and polder region nitrogen circulation model (NDP) by developing a River nitrogen circulation model (River-N) covering aquatic plants and bio-geochemical circulation, simulates the input, output and migration conversion processes of three forms of nitrogen (granular nitrogen, ammonia nitrogen and nitrate nitrogen) in a rural River, confirms the source and sink balance rule of nitrogen, and quantitatively evaluates the rural River nitrogen interception capability in a plain River network region. The mechanism method of the invention provides key technical support for rural river nitrogen pollution control and management and control widely distributed in the middle and downstream plain river network area.
The beneficial effects of the invention are as follows: (1) The quantitative means of the river nitrogen source collection law in the rural areas of the accounting plain are provided, and technical support is provided for identifying the river key nitrogen sources; (2) The method for quantifying the river nitrogen interception law in the plain rural areas is beneficial to accurately identifying the main control factors for river nitrogen interception; (3) The method provides the future change prediction of the nitrogen interception capability of the rural river in plain, can predict the change of the nitrogen interception capability under different engineering scheme conditions, and supports the scheme optimization of nitrogen pollution prevention and control.
Drawings
Figure 1 shows a flow chart of the method of the invention.
Figure 2 shows Jiang Guhe position and surrounding land utilization.
Fig. 3 shows the water volume exchange (dredging and no dredging conditions) of Jiang Guhe simulated by a three-dimensional hydrodynamic model of the river network (EFDC) with the peripheral river.
Fig. 4 shows the simulated change in concentration of Jiang Guhe granular nitrogen, ammonia nitrogen and nitrate nitrogen (with and without dredging) for the River nitrogen circulation model (River-N).
Figure 5 shows the nitrogen source sink profile of Jiang Guhe without dredging (2020-2021).
Figure 6 shows the Jiang Guhe total nitrogen concentration variation (with and without dredging) simulated by the River nitrogen cycle model (River-N).
Figure 7 shows the nitrogen source sink profile of Jiang Guhe under dredging conditions (2020-2021).
Detailed Description
The technical scheme of the invention is further described below with reference to the accompanying drawings and the detailed description.
Example 1
Example 1 the method of the present invention will be further described by taking Jiang Guhe (i.e., li-yang, shuzhen, jiangsu) as an example of the verification of nitrogen interception ability.
In the embodiment, a River meteorological-hydrologic-water quality monitoring (2020-2021) is carried out based on a constructed River nitrogen circulation model (River-N), the input/output and migration conversion process of three forms of nitrogen in a River are simulated, the migration conversion, input and output of nitrogen are calculated, and the River nitrogen interception capability is evaluated. The method comprises four steps of implementing nitrogen dynamic simulation on rural rivers in plain river network areas:
(1) Jiang Guhe Meteorological, hydrological and Water quality monitoring
Jiang Guhe is located in the southeast China in the typical plain river network area, i.e. the west of the Taihu river basin, has a total length of about 1130m, an average river width of about 24m and an average water depth of about 1.5m, and is a typical rural small river (FIG. 2). In this embodiment, the data used to build the assessment model mainly includes weather, water quality and water level data from 2020 to 2021. The meteorological data is from measured data in the area of the peak-to-peak resident near Jiang Guhe, including barometric pressure, precipitation, and air temperature. The water quality data is derived from water quality monitoring of Jiang Guhe, peripheral rivers and polder area fish ponds, and the monitoring indexes comprise Total Nitrogen (TN) and ammonia Nitrogen (NH) 4 + ) And nitro Nitrogen (NO) x ) Particulate Nitrogen (PN). The monitoring frequency is 1-2 months/time, and the monitoring frequency is used for model verification.
(2) Jiang Guhe and peripheral river network water exchange accounting
Considering that the terrain of the Jiang river is flat, the water system is complex, and a grid with higher spatial resolution is required to finely simulate the motion state of the Jiang river flow between grids and the processes of groove returning and rising. The reaction unit of the hydrodynamic process adopts square grids to grid the Jiang Guhe calculation domain, and the grid size is 10m.
And adopting a river network three-dimensional hydrodynamic model (EFDC) to simulate Jiang Guhe hydrodynamic conditions, and further accounting Jiang Guhe for water exchange with the peripheral river network. The Jiang Guhe and measured water level, precipitation and other data of the peripheral river are input into the EFDC model, the simulation step length is daily, simulation results are processed, and the daily input and output water quantity of Jiang Guhe and the peripheral river 2020-2021 are determined (figure 3).
(3) Jiang Guhe nitrogen source sink balance process simulation
Jiang Guhe nitrogen source sink balance is commonly influenced by human activities in surrounding polder regions of rivers and water body exchange in peripheral rivers. Therefore, the River nitrogen circulation model (River-N) is used for coupling the River network three-dimensional hydrodynamic model (EFDC) with the polder region nitrogen circulation model (NDP), and the Jiang Guhe nitrogen source sink balance process is simulated. The NDP model is a model constructed in an article published earlier by the applicant, see "Towards the development of a modeling framework to track nitrogen export from lowlandartificial watersheds (polders)".
River nitrogen cycle model (River-N) describes the migratory conversion of three forms of nitrogen; wherein the nitrate nitrogen source mainly comprises nitrification and atmospheric sedimentation of the water body. The ammonia nitrogen source mainly comprises atmospheric sedimentation, substrate release, plant spoilage and mineralization; the granular nitrogen source mainly comprises atmospheric sedimentation, plant putrefaction, assimilation and granular nitrogen resuspension in the substrate; in addition, denitrification processes, anaerobic ammoxidation processes, plant absorption consume nitrate nitrogen and ammonia nitrogen. The control equation includes:
(1) total nitrogen;
ΔTN T ＝ΔPN T +ΔNH T +ΔNO T
(2) aquatic plant growth, namely, the design of the application introduces a control equation describing the aquatic plant growth and elimination process;
BSH T ＝BSH T-ΔT +((1-K STR )k SHOOTGrow f Uptake f PLT -K SHOOTDec f SHOOTDecT )BSH T
BRO T ＝BRO T-ΔT +K STR K SHOOTGrow f Uptake f PLT BSH T -K ROOTDec f ROOTDecT BRO T
(3) particulate nitrogen;
(4) ammonia nitrogen;
(5) nitronitrogen;
wherein T represents time, deltaT represents model run time step length, TN T Indicating the total nitrogen concentration, PN of the water body T Represents the granular nitrogen concentration of the water body and NO T Represents the nitrate nitrogen concentration and NH of the water body T Represents the ammonia nitrogen concentration of the water body,
represents the concentration of granular nitrogen re-suspension +.>
Represents ammonia nitrogen assimilation concentration,/->
Indicating the nitrogen assimilation concentration->
Represents the nitrogen concentration of the plant spoilage particles,/->
Represents the atmospheric sedimentation particulate nitrogen concentration, +.>
Representing the concentration of the granular nitrogen deposited in the water body; />
Indicates the concentration of ammonia nitrogen by nitrification and->
Represents the ammonia nitrogen absorption concentration of plants, namely->
The concentration of ammonia nitrogen in the nitrogen assimilation effect,
represents the concentration of anaerobic ammonia oxidation ammonia nitrogen, +.>
Indicating denitrification nitrate nitrogen concentration,/->
Represents the ammonia nitrogen concentration of atmospheric sedimentation,/->
Representing the concentration of plant spoilage ammonia nitrogen; />
Represents the atmospheric sedimentation nitrate nitrogen concentration, +.>
Indicating the nitrogen absorption concentration of plants,/->
Indicating the anaerobic ammonium nitrate nitrogen concentration.
The River nitrogen circulation model (River-N) is driven by the output results of the EFDC model and the NDP model to simulate the nitrogen concentration of the water body under the joint influence of Jiang Guhe and peripheral River water quantity-nitrogen exchange and water quantity-nitrogen exchange in a foreign region. The obtained nitrogen concentration is input into a River nitrogen circulation model (River-N), the transformation and migration of nitrogen in different bioelectrochemical processes are described, the flux of each process is calculated, and finally Jiang Guhe nitrogen source and sink balance simulation is realized.
Inputting the water level, water quality and meteorological data actually measured in Jiang Guhe and the polder region into a River nitrogen circulation model (River-N), wherein the simulation step length is daily, then determining more sensitive 10 parameters in the River nitrogen circulation model (River-N) by adopting a parameter global sensitivity analysis method MOAT (Morris one at a time), endowing the 10 parameters with a reasonable parameter interval, and adopting a genetic algorithm and combining a super Latin sampling experiment to improve the simulation precision of the mechanism model to be optimal.
(4) Jiang Guhe Nitrogen interception capability assessment
The amount of daily exchanged water between Jiang Guhe and the peripheral river 2020-2021 was determined in step (2) of this example (fig. 3), the nitrogen flux of each bioelectrochemical process established in step (3) of this example was statistically determined Jiang Guhe for nitrogen source, sink and hold up flux, and the interception capacity of nitrogen by Jiang Guhe was analyzed (fig. 5).
Example 2
Example 2 the method of the present invention is further illustrated by taking as an example the evaluation of the impact of bottom mud dredging on nitrogen interception capacity of Jiang Guhe (Li-Yang City, jiangsu).
The method is based on a constructed River nitrogen circulation model (River-N), simulates the influence process of sediment dredging on nitrogen migration and conversion, and evaluates the influence of sediment dredging on nitrogen interception capability. The implementation is divided into four steps:
(1) Modeling of Jiang Jia river bottom mud dredging
The dredging engineering of bottom mud of 3 months in 2020 is taken as an example, and the effect of improving or weakening the nitrogen source, sink, absorption and retention capacity of a river under the dredging condition is evaluated by using the model method of the invention.
The Tai lake basin is a typical plain river network area of the Yangtze river basin. Under the influence of activities of human agriculture production and living, a large amount of nitrogen is transported into the river, so that the rural river becomes a key link of regional nitrogen circulation. Because of the dense population and dense river network, the nitrogen sources are complex and widely distributed, and mainly have sources such as farmland discharge in the polder area, fish pond discharge, peripheral river sink, atmospheric sedimentation and the like. The emission and the transfer of nitrogen not only cause the water quality of the river water body to deteriorate, but also cause eutrophication, the waterweed grows up to the river, the river channel is blocked, and the Jiang Guhe river channel is a waterweed cluster (figure 2). 3 months in 2020, jiang Guhe was subjected to one sediment dredging.
The bottom mud dredging has an important influence on river nitrogen circulation, and is mainly characterized by reducing aquatic organisms, destroying habitat of river water organisms and reducing nitrogen circulation rate in sediment, so that the geobiochemical process of nitrogen is changed, and further, the change of the nitrogen concentration of water body is influenced. However, the effect of dredging on the river course is difficult to quantitatively evaluate, and the mechanism model method can evaluate the effect of dredging on the river course, and the effect of small-sized rural rivers in the nitrogen source, sink, absorption and detention processes under the dredging condition is analyzed through the model, so that management decisions are guided, and further, the maximum absorption of nutrient load is realized. The river nitrogen circulation model calculates the change of each process flux by changing the parameters of the related bio-geochemical process, thereby realizing the simulation of the dredging effect of the sediment. The verification of the sediment dredging simulation is achieved by water quality monitoring once during the 3 days of the dredging period.
(2) Evaluation of influence of dredging of river sediment on nitrogen interception capability
In order to know in detail the effect of dredging on the concentration of river N, the frequency of water quality monitoring during the dredging period and two months after dredging (21 days to 25 days of 3 months in 2020) was once every 3 days for reflecting the effect of dredging on the river nitrogen circulation. In the above embodiment, the River nitrogen circulation model (River-N) of the present invention and the coupling thereof with the existing River network three-dimensional hydrodynamic model (EFDC) and the model for the nitrogen circulation in the levee region (NDP) have been described in detail, and the model method used in this embodiment is the same as that of the previous embodiment, but in consideration of the influence of dredging engineering on the River hydrodynamic force, macrophytes and water quality, this embodiment optimizes the release rate of nitrogen in the sediment, the absorption rate of nitrogen in the sediment, the resuspension rate, the sedimentation rate, the denitrification rate and the absorption capacity of macrophytes on nitrogen in the evaluation model, and the optimization method is also completed by using genetic algorithm in combination with the pull Ding Chao cubic sampling experiment.
Under dredging conditions, the simulation result (figure 3) of the three-dimensional hydrodynamic model of the river network shows that: after dredging, the exchange of the water volume with the peripheral river is remarkably increased in 6-10 months Jiang Guhe, and in 4 months 2020 just after dredging, the exchange of the water volume with the peripheral river is frequent in Jiang Guhe, and the exchange of the water volume is more than that of the non-dredging condition as a whole. Considering that the dredging takes away Jiang Guhe sediment and macrophytes, the river smoothness is enhanced, and the exchange of the river water with the periphery is naturally increased.
Under dredging conditions, river nitrogen circulation model (River-N) adopts Jiang Guhe 2020 water quality actual measurement data to correct, and 2021 water quality actual measurement data is used to verify model simulation effect. By analysis of the simulation results of fig. 6, the model exhibits better simulation ability and can better capture the variation characteristics of total nitrogen as a whole. The model can better capture the fluctuation change characteristics of the pollutant concentration. The fitting degree of the total nitrogen in the verification period is satisfactory (R 2 =0.58), which is higher than 0.51 in the correction period, can better capture the trend of the change in the contaminant concentration; the PBIAS (-33.17%) of TN in the validation period is smaller than that in the correction period (-34.39%). Therefore, the constructed rural river nitrogen circulation model has a good simulation level and can be applied to water quality simulation of Jiang Guhe. The observed value of total nitrogen at 25 days of 6.6 of 2021 reached 13.16mg/L, which was an outlier, and therefore this outlier was not considered in calculating the fitness.
Under dredging conditions, the accuracy of a River nitrogen circulation model (River-N) meets the requirements, and the effect of the rural small River under the dredging conditions in the nitrogen source, sink, absorption and detention processes can be known in detail through model statistical analysis under the dredging conditions. Through model statistical analysis, it was shown (fig. 7) that peripheral river inflow, polder region drainage and substrate release are the main nitrogen sources of Jiang Guhe, with 3 amounting to 92.2%, 51.9%,28.5% and 11.8%, respectively; in the composition structure of nitrogen sink, the main nitrogen sink is denitrification, peripheral river water body discharge and water diversion irrigation in the polder region, and the total of 3 nitrogen sinks is 87.9%, and the total of the 3 nitrogen sinks respectively accounts for 47.3%,29.5% and 11.1%. Under the influence of dredging, in nitrogen sources, the flux of the 2021 substrate release and the granular nitrogen re-suspension are respectively 29.48% and 87.93% less than 2020, in nitrogen sinks, the flux of the 2021 granular nitrogen sedimentation is 15.34% less than 2020, and the 2021 denitrification flux is 23% more than 2020. These differences may reflect that dredging enhances substrate release, particulate nitrogen re-suspension and sedimentation, and impairs denitrification.
Comparing the simulation results of this example with the model simulation results of example 1 under the condition of no dredging, it was found that the influence of dredging on the river water quality of the scale was mainly expressed in summer and autumn (7-11 months) (fig. 4). The total nitrogen concentration is generally greater under dredging conditions than under non-dredging conditions, especially at 7-8 months, during the dredging period and during the recovery period of aquatic vegetation. In the long-term dredging, the difference in 2 situations is very small from 11 months in 2020 to 5 months in 2021; as the water level rises, for 6-10 months 2021, the concentration in the dredging scenario is significantly greater than that in the non-dredging scenario; the water level is reduced in 11-12 months, the difference of water exchange amount is reduced, and the concentration under dredging is slightly smaller than that under non-dredging. Peak differences occur between 7 and 10 months, probably due to the fact that at this stage the peripheral river concentration is greater than Jiang Guhe, and after dredging, up to 51.9% of the water amount gushes Jiang Guhe (fig. 3) for 7 to 10 months compared with other months, plus the N concentration of the peripheral river is higher than Jiang Guhe, so that more contaminants enter the river and the contaminant concentration increases. Meanwhile, the influence of dredging on the concentration of pollutants is mainly reflected in the improvement of the ammonia nitrogen release rate of the sediment, the resuspension and sedimentation rate of granular nitrogen are improved, the plant absorption capacity is reduced, and denitrification is inhibited. During the dredging period, the ammonia nitrogen release rate is 3 times that before dredging, and the particulate nitrogen re-suspension rate and sedimentation rate are 233.3 times and 21.9 times that before dredging respectively, which may be related to the strong disturbance of the water-soil interface caused by dredging. Denitrification, nitrification and assimilation are inhibited, which may be related to dredging spoiling of the flora in the water environment on the one hand and to the removal of aquatic plants on the other hand; dredging has little effect on anaerobic ammonia oxidation. Overall, dredging increases the release of endogenous nitrogen, making the water-soil interface a source more pronounced. In the recovery period of aquatic plants (5 months to 8 months in 2020), the ammonia nitrogen release rate, the granular nitrogen re-suspension rate and the sedimentation rate obviously fall back, along with the recovery of aquatic vegetation, the plant absorption effect, denitrification, nitrification and assimilation effect are obviously improved, the influence of dredging is slowly weakened, the release of nitrogen is reduced, the absorption of nitrogen is increased, and the characteristic that a water-soil interface becomes a sink is more obvious.
According to model statistical analysis, the dredging can reduce the pollutant concentration in the sediment, but cannot obviously and continuously reduce the nitrogen in Jiang Guhe water, the peripheral river water enters Jiang Guhe to be a main factor influencing the Jiang Guhe water pollutant concentration, the peripheral river water concentration is generally higher than Jiang Guhe, and Jiang Guhe water pollutant concentration is high due to a large amount of water exchange. More water from the peripheral river after dredging is drawn into Jiang Guhe than without dredging, so that more contaminants enter the river, and the concentration of the contaminants is increased, particularly in 7-10 months (fig. 6).
Under dredging conditions Jiang Guhe has an enhanced effect as a nitrogen source due to more water sinks in the peripheral river, but Jiang Guhe has a reduced effect on nitrogen absorption and retention due to hydrodynamic enhancement, disappearance of macrophytes and destruction of bacterial flora in the water body, so that the nitrogen interception capability of Jiang Guhe after dredging is estimated to be limited by the method of the invention, particularly in 2021, the nitrogen reduction effect caused by dredging is smaller and smaller with the passage of time.
Claims (9)
1. The method for evaluating the rural river nitrogen interception capability of the plain river network area is characterized by comprising the following steps of:
simulating water volume exchange between rural rivers and peripheral rivers in the plain river network area based on the EFDC three-dimensional hydrodynamic model;
simulating water body and nitrogen exchange flux of rural rivers and polder areas in plain river network areas based on an NDP polder area nitrogen circulation model, wherein the nitrogen comprises granular nitrogen, ammonia nitrogen and nitrate nitrogen;
establishing a River-N River nitrogen circulation model which covers the aquatic plants and the bio-geochemical circulation, wherein a control equation of the River nitrogen circulation model comprises an aquatic plant generation and elimination process;
according to simulation results of the EFDC three-dimensional hydrodynamic model and the NDP polder region nitrogen circulation model, river boundary conditions are determined, a River-N River nitrogen circulation model is input, daily dynamic changes of rural River nitrogen in the plain River network region are simulated, and rural River nitrogen interception capability of the plain River network region is evaluated.
2. The method of claim 1, wherein the control equation describing the aquatic plant decontamination process is as follows:
BSH T ＝BSH T-ΔT +((1-K STR )k SHOOTGrow f Uptake f PLT -K SHOOTDec f SHOOTDecT )BSH T
BRO T ＝BRO T-ΔT +K STR K SHOOTGrow f Uptake f PLT BSH T -K ROOTDec f ROOTDecT BRO T
wherein T represents time, deltaT represents time step, BSH T Representing the biomass of the overground parts of aquatic plants, K STR Represents the proportion of the aquatic plant transferred to the root system on the ground, k SHOOTGrow Indicating the maximum growth rate of the overground parts of the aquatic plants under the optimal condition, f Uptake Represents the nitrogen limitation of absorption by aquatic plants, f PLT Indicating the temperature limit of aquatic plant growth, K SHOOTDec Indicating the maximum growth rate of the overground parts of the aquatic plants under the optimal condition, f SHOOTDecT Temperature limitation indicating decay of aerial parts of aquatic plants, BRO T KH, which represents biomass of underground parts of aquatic plants Uptake Represents the half-saturation constant, K, of nitrogen absorption by aquatic plants ROOTDec Represents the metabolic rate of the root system at the reference temperature, f ROOTDecT Temperature limit, NH, indicative of root rot of aquatic plants T Represents the ammonia nitrogen concentration of surface water, NO T Represents the nitrate nitrogen concentration, theta PL Indicating the effect of temperature on the growth of the aquatic plants,
represents the surface water temperature, T PL1 、T PL2 Represents the optimal lower limit and upper limit of the temperature, theta, suitable for the growth of aquatic plants SHOOTDec Indicating the effect of temperature on the metabolic rate of the aerial parts of the aquatic plants,/->
Represents the daily average water temperature, theta ROOTDec The effect of temperature on the metabolic rate of the root system of the aquatic plant is shown.
3. The method of claim 1, wherein the three-dimensional hydrodynamic model utilizes a water level based grid cell to determine the direction of water flow and the three-dimensional hydrodynamic process.
4. The method of claim 1, wherein the horizontal direction coordinate reference of the three-dimensional hydrodynamic model is rectangular coordinates or orthogonal curve coordinates, staggered grid dispersion is adopted in space, a finite difference method of second order precision is adopted in time integration and combined with an internal and external mode splitting technology, a semi-implicit calculation method is adopted in an external module, an internal module adopts a vertical diffusion implicit format, and an amphibious beach area region adopts a dry and wet grid technology.
5. The method of claim 1, further comprising model checking, calibrating, and calibrating model parameters based on measured weather, hydrology, and water quality monitoring data.
6. The method of claim 5, wherein the model check is: identifying key parameters of the model by adopting a sensitivity analysis method, constructing an intelligent optimization mode of the model parameters, and obtaining an optimal parameter set of the model; and comparing the simulation values and the actual measurement values of the nitrogen indexes, and quantitatively evaluating the simulation effect of the model by adopting the Nash efficiency coefficient.
7. The method of claim 6, wherein the optimizing is accomplished using a genetic algorithm in combination with a latin hypercube sampling experiment.
8. The method of claim 1, wherein the rural river nitrogen interception capacity of the plain river network area is assessed based on the retention flux of nitrogen by the river.
9. The method of claim 8, wherein the retention flux of nitrogen by the river comprises quantified particulate nitrogen natural settling, denitrification, anaerobic ammoxidation, aquatic plant absorption process flux.
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