Introduction

Ecological tidal water diversion has become a standard engineering measure and a significant focus of research in the field of ecological tidal water diversions. This is because tidal river networks typically have abundant water resources, and the dynamic nature of tides makes them suitable for hydrodynamic water diversion. However, the frequent and complex reversing tidal currents pose scientific challenges to cooperative water diversion. Since the 1990s, there has been an increasing implementation of ecological tidal water diversion aimed at improving water eco-environment and river health1. These projects aim to supply the deficient environmental factors to the water ecosystem through water diversion and other necessary measures such as pollution interception and ecological restoration2,3,4,5. Depending on the specific characteristics of the water ecosystem, ecological tidal water diversions typically targets include: (i) improving ecological carrying capacity, e.g., Emergency Water Transmission Project of Lower Tarim River and Zalong Wetland Emergency Water Supply Project; (ii) increasing water environment capacity, e.g., Pearl River Estuary Pressure and Salt Repair Emergency Water Diversion, Water Diversion from the Yangtze River to Lake Taihu project.

In the Taihu Lake Basin, which is characterized by urban river networks and lake marshes, the water quality is commonly described as low-carbon and high-nitrogen. The average carbon–nitrogen ratio is typically below the critical threshold value of 2.86, indicating a deficiency in self-net carbon–nitrogen ratio6. As a result, since the first water diversion test through Wangyu River in 2002, more cities, including Changshu town, have been implementing ecological water supplying projects along the water diversion lines7,8,9,10,11,12. In-depth diversion researches on effect evaluations and scientific optimizations are generally increasing13,14,15,16; however, it is still necessary to study on the scientific analysis approach to accurately describe and optimize the ecological tidal water diversion plans.

Hence, we propose a continuation-dynamic constitution analysis approach based on digital stable marker tracing. We applied this approach to analyze and optimize cooperative diversion in the center river network of Changshu town, using the tidal hydrodynamic forces of the Yangtze River and Wangyu River to introduce water resources and improve the water environment. Additionally, we designed an ecological tidal water diversion that considers water pollution control and ecological restoration to extend the effectiveness of cooperative diversion.

The objectives of this study are: (i) Based on digital stable marker tracing to propose the continuation-dynamic constitution analysis approach; (ii) apply continuation-dynamic constitution analysis to describe and optimize the cooperative diversion in Changshu tidal river network, China; (iii) further discuss the implementation effects and characteristics of ecological tidal water diversion in Changshu tidal river network, China.

Results

Water diversion design

Study area

It is located in the center of Changshu town, 31° 35ʹ–31° 46ʹ N, 120° 40ʹ–121° 03ʹ E, with a surface area of 60 km2 around; and the ground elevation is mostly 3–7 m, Woosung datum, with “Northwest-high, Southeast-low” topographic characteristic.

This area mainly contains 14 rivers and 7 gates, showed in Fig. 1: the 5 channels as Haiyangjing, Zhangjiaganghe, Gengjing, Changxuhe and Baimaotang; the 4 rivers entering the center town as Qinchuan, Huchenghe, Shanqiantang and Hunchenghe; the 5 rivers near the center town as Huabantang, Nanfushantang, Qingduntang, Hengjingtang and Donghuanhe; and the 7 gates include: the 5 estuary gates between the Yangtze River and Haiyangjing, Zhangjiaganghe, Gengjing, Changxuhe, Baimaotang, respectively; the 2 internal gates on Nanfushantang, Qingduntang.

Figure 1
figure 1

Map of the study area. The 2 diversion channels with gates are Haiyangjing (HYJ), Zhangjiaganghe (ZJGH); the 3 drainage channels with gates are Gengjing (GJ), Changxuhe (CXH), Baimaotang (BMT). In addition, there are 9 main rivers marked out: the 4 entering the centre town as Qinchuan (QC), Huchenghe (HuC), Shanqiantang (SQT) and Hunchenghe (HCH); the 2 gates controlled as Nanfushantang (NFST) and Qingduntang (QDT); and the other 3 as Huabantang (HBT), Hengjingtang (HJT) and Donghuanhe (DHH). The map was created using QGIS (QGIS Development Team, software version 3.16.13, https://www.qgis.org) and the satellite image was from 91weitu (91weitu Development Team, software version 19.3.4, https://www.91weitu.com).

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Water diversion

As the reversing tidal current and local human activities, the study river network exhibits low environmental capacity and weak self-purification capacity17,18,19. Therefore, Chen et al. scholars designed a prototype water diversion test to transfer water resources by tidal dynamic from the Yangtze River to the center river network on May 14th, 201420. The water transfer routes and quantity–quality observation sections are shown in Fig. 1; the measured processes on selected Sections are shown in Fig. 7.

Based on the prototype water diversion test’s suggestion that: “extend the water diversion time and increase the diversion channels”, authors designed two water diversion projects to improve the ecological water diversion effect of the tidal river network; see Table 1 and Fig. 1. Design1 aimed to extend the water diversion time and lengthened the water diversion duration from 13.5 to 36 h. Design2 aimed to increase the diversion channel and selected a new track: Wangyu River-Zhangjiaganghe-center river network to introduce clean water in 24 h.

Table 1 Prototype test and Simulation designs of water diversion.
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The gates that showed in Table 1 and Fig. 1 have operation rules as follows: (i) when the tide Level increases to the ordinary water Level of 3.2 m, open the diversion channels gates: Haiyangjing gate, Zhangjiagang gate, and keep the drainage channels gates closed; (ii) when tide Level decreases to the ordinary water Level of 3.2 m, close the diversion channels gates and open the drainage channel gates: Gengjing gate, Changxuhe gate and Baimaotang gate, to control flow discharge and keep water quantity balance of local river network; (iii) keep both the Nanfushantang gate and Qingduntang gate closed during the whole water diversion.

Results assessment

To evaluate the water diversion results of Design1 and Design2 (Details in Table 1), two assessment sections were selected: Section9 and Section5 (see Fig. 2). Section9 is located in the center of the tidal river network, which is the main water import area with complex flow conditions. Section5 is located downstream in the southeast of town, where a large proportion of the tidal river network flow dumps in.

Figure 2
figure 2

Time series of water ages on Section5 and Section9 in designed WDPs. (a) The assessment sections in designed WDP1; (b) the assessment sections in designed WDP2.

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Water age and residence time analysis

In Design1, see Fig. 2a, the peak discharge at Section9 was 11.9 m3/s, the residence time of the background water source in Huanchenghe was about 2.0 h, and the mean water age of the diversion water source from Yangtze River at Section9 was 10.80 h. In comparison, the peak discharge at Section5 was only 3.70 m3/s, and the residence time of the background water source in Baimaotang was about 4.0 h. No Yangtze River water source flowed into Section5 at the end of the simulation.

In Design2, see Fig. 2b, the peak discharge at Section5 was 8.15 m3/s, the residence time of the background water source in Baimaotang was about 9.0 h, and the mean water age of the diversion water source from Wangyu River at Section5 was only 0.11 h. Meanwhile, the peak discharge at Section9 was only 4.16 m3/s, the residence time of the background water source in Huanchenghe was also 9.0 h, and the mean water age of the diversion water source from Wangyu River at Section9 was only 0.45 h.

It can be inferred that the WDP Design1 from the Yangtze River had abundant water resources and topographic advantages that went into the center of town. Both helped lengthen the water age of water diversion source in Design1 to the tidal river network. For a clean and abundant water diversion, the long water age is significant to improve the effect of ecological water supplements. Some previous studies have also found that residence time was positively associated to the nutrients17,21, which means the inflow water resource of Design1 could significantly affect the nutrients in background water. However, with the increased flow path distance, drainage channels’ response in southern river networks to supplement is limited, as the ecological water resource has not yet arrived there in simulation. Some previous studies have also found that the clean supplement may not involve the entire water area22,23.

As for the WDP Design2 from Wangyu River, benefitting from the location of diversion channel Zhangjiaganghe close to the center of town, the water diversion source of Design2 can arrive at Section5 in 2 h and improve the water environment capacity of the drainage river networks. However, due to the limitation of ecological supplement discharge, inflow in diversion channel Zhangjiaganghe has low velocity and short water age. Since long-term trickle usually has a positive effect on reducing the nutrient concentration24,25, the long-time diversion processes in this situation may be advantaged.

Continuation-dynamic constitution analysis

Assessment Section9

Water quality-quantity continuation-dynamic components of Section9 on Huanchenghe in the center of town in water diversion Design1 are shown in Fig. 3a. In the initial 6 h, the mean water environment quality Level in the assessed section stayed in Level 3 to Level 5. During 6 to 17 h, as diversion water became the dominant source, the background water source of Haiyangjing in Level 2 accounted for 50% of inflow and improved the water quality at Section9. From 17 h, the water source of the Yangtze River in Level 1 started reaching the section continuously. And during 17 to 28 h, the water diversion channel Haiyangjing and water diversion source from the Yangtze River accounted for about 80% of inflow into Section9, which effectively increased the water environment capacity. After 28 h, the Level 1 water diversion source from the Yangtze River accounted for 100% inflow. We can infer that: (i) after 17 h of water diversion, the water environment capacity in the tidal river network effectively increased. Moreover, the water quality at Section9 achieved the target Grade IV after about 28 h; (ii) water supplement in this situation was compelling that the diversion water source of Yangtze River accounted for 33.1% during the whole diversion on average.

Figure 3
figure 3

Time-variant quality-quantity processes at assessment sections in designed WDP1 and WDP2. (a) Blue color gradients represent different water-quality Level s, the letter in every blue block corresponds the inflow water constitution name. (b) Horizontal axis: as a timeline, to indicate the water diversion process from start time 0 to end time n. (c) Left vertical axis: as a percentage axis, to reflect the proportion of inflow water constitution at different times, fit with the blue blocks in different depths. (d) Right vertical axis: as a flow axis, to represent the inflow on section at different times, fit with the black curve.

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The results of water diversion Design2 of Section9 of Huanchenghe in the center of town are shown in Fig. 3b. In the first 12 h, the contribution of the background water source of Huanchenghe in Level 4 was steadily above 90%; then, the inflow water source increased continuously. After 16 h, flow proportions from Wangyu River, Zhangjiaganghe and background water source of Huanchenghe became stable at about 10%, 10% and 15%, respectively; meanwhile, inflow from backbone rivers in Level 3 and branch rivers in Level 5 accounted for 65%. However, the discharge of backbones roughly reduced by 15% eventually, the same as the increased contribution of branches. The above analysis suggests that: (i) since the topographic effect that “Northwest-high, Southeast-low” of the center of town, there were a large proportion of discharges from major town river networks draining into Section9; (ii) the water quality was mostly influenced by the tributaries so that in the final 8 h, the environment quality of this area deteriorated mildly; (iii) water supplement in this situation was minimal that the diversion water source of Wangyu River only accounted for 4.13% during the whole diversion in average.

Assessment Section5

The water quality-quantity continuation-dynamic components of Section5 on the drainage channel Baimaotang in water diversion Design1 are shown in Fig. 3c. Inflow water constitutions at Section5 remained stable in the first 5 h. The contribution of background water sources of Haiyangjing and Zhangjiaganghe in Level 2 became stable at about 15% of discharges. The background water source in Baimaotang and the inflow water source from backbone Rivers accounted for 50%, and 20%, respectively, and both of their water qualities were in Level 3. Inflow water sources from tributaries had the worst water quality as Level 5, and their contribution accounted for 15% of discharges. No inflow water resource from the Yangtze River reached here during the whole diversion. Besides, during 12 to 28 h, the mean discharge at Section5 was only 0.54 m3/s due to the reversing action of water flow. After 28h, the proportion of discharges from the northern river networks increased, which might be affected by topographic factors. In a word: (i) in this situation, the diversion distance from the source Yangtze River was too long to supply the drainage channel Baimaotang ecologically; (ii) river networks around Baimaotang outside the south of town did not get significant ecological water supplement.

The results of water diversion Design2 at Section5 on the drainage channel Baimaotang are shown in Fig. 3d. Since the short distances of the flow path, the diversion water source of Wangyu River reached Section5 in the first 2 h and inflow water constitutions at Section5 became stable after 6 h. The contribution of background water resources and backbone rivers’ inflow water resources in Level 3 accounted for more than 50% of discharges; the better quality inflow water source in Level 1 and Level 2 accounted for about 20–25%; and the proportion of inflow tributaries in Level 5 accounted for about 15–20%. On average, the diversion water source from Wangyu River accounted for 6.75% during the whole diversion, which nearly did not help improve the environment. We infer that: (i) ecological water supplement in this situation was stable but not apparent to the drainage channel Baimaotang and surrounding river networks; (ii) the water quality of Baimaotang and surrounding river networks could improve a little after this WDP and the inflow water source wouldn’t have negative impacts on water quality of Secion5.

Optimization of the cooperative diversion

The WDP management methods are crucial in improving diversion efficiency26. According to the water diversion effect of designed WDPs and the results of continuation-dynamic constitution analysis, we optimize the cooperative diversion.

On the one hand, the river networks outside the south of town mainly undertake the outflow from the center of town because of the “Northwest-high, Southeast-low” topography characteristics. On the other hand, to avoid the water-Level jacking and reversing of the flow of several central reaches, which are caused by two diversion sources, we optimize the diversion scheme. Firstly, supply the ecological water mainly from the Yangtze River to the tidal river network; secondly, when the flow in center river network becomes stable, introduce water resources from the Wangyu River to consolidate the effect of environmental water supplement for the river network outside the south of town.

Discussion

To keep the enduring effect of cooperative diversion, we designed a comprehensive diversion scheme, including measures as: pollution interception, cooperative water diversion and ecological restoration, to discuss the impact of ecological tidal water diversion application (Table 2).

Based on the simulation of the Ecological Water Diversion Project scheme in Table 2, we calculated the water environment capacity of the tidal river network in different stages, and the results were showed in Fig. 4. In the first stage, due to the effect of pollution interception, ecological restoration and especially the abundant and clean water diversion from the Yangtze River and Haiyangjing channel, the rest environment capacity of the central river network had increased from − 1760.38 to 497.61 t/a. This huge improvement of the rest of WEC is the sum of main rivers’ WEC in the center of town (see Fig. 4). The significant impact of the Yangtze River water diversion on study river network could be confirmed by the previous water diversion tests20,27. During the second stage, many rivers’ water qualities were continuously improved except Huanchenghe, which was affected by drainage flow from the center of town. In the third stage, the addition of a water source from Wangyu River through the Zhangjiaganghe gate significantly increased the water environment capacity of River Shanqiantang, a channel directly connected with Zhangjiaganghe, from 13.31 t/a to the maximum value of 50.87 t/a. At the end of the simulation, the total water environmental capacity of NH3-N reached 588.81 t/a, and the water quality of the main channels in the center of town met the target. The Ecological Water Diversion Project proved to be effective in maintaining the enduring effect of cooperative diversion.

Table 2  Gantt Chart for Changshu Ecological Water Diversion Project timelines.
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Figure 4
figure 4

Water environment capacity of channels in central river network.

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Taking the River Qinchuan located in the central business district of Changshu, see Fig. 5, as an instance. The structure of this river, with a closed gate upstream connected to Beifushantang, passing through the center of town from north to south, and downstream connected to Zhangjiaganghe, resulted in limited water inflow. Previous studies suggested that the closed gate could reduce the river’s self-purification capacity due to slow flow velocity13. In the simulation, various measures were implemented, including: a. Pollution interceptions of rivers include Rivers Qinchuan, Huchenghe and Nanfushantang; b. ecological restoration as an urban scenic river; c. ecological water diversion through Haiyangjing; d. ecological water diversion through Zhangjiaganghe. Effects of these mentioned measures were operated in single and combined, and the water environmental capacity of River Qinchuan in different simulating stages was shown in Fig. 5.

Figure 5
figure 5

Water environment capacity of River QC in different stages. a. Pollution interceptions of rivers include Rivers Qinchuan (QC), Huchenghe (HuC) and Nanfushantang (NFST); b. ecological restoration as urban scenic river; c. ecological water diversion through Haiyangjing (HYJ); d. ecological water diversion through Zhangjiaganghe (ZJGH).

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The combined effect of all measures proved to be the most effective, with positive capacities at the end of Day7, while the capacities in measures “a+c” and “a+d” were still negative. It highlighted the element-complementary effect of measures in the Ecological Water Diversion Project. Moreover, the concentration of NH3-N in pollution interception measure “a” significantly reduced, and the water environment capacity in measure “a+b” preliminarily became positive. Both can prove the importance of pollution interception and ecological restoration in improving the self-purification ability of river channels28. Similarly, there has also been proposed that 75% of the international river pollution interception research was devoted to the restoration of river ecology, and about 35% was trying to restore the lost riparian vegetation and wetland community29.

Comparing the simulation results of different measures in Fig. 5, it was found that the Ecological Water Diversion Project had a better improvement and restoration effect than the sum of four single measures, see Formula (1). It reflected the comprehensive effect of the Ecological Water Diversion Project, i.e., the coupling of project elements and their synergistic impact, where “1 + 1 > 2”.

$$\left|a+b+c+d\right|-\left|a+c\right|-\left|a+d\right|-\left|a+b\right|+\left|a\right|\times 2=12.1>0.$$
(1)

Methods

The methodologies schematic diagram of this study is shown in Fig. 6. Firstly, a coupled hydrodynamic-water quality model was constructed to simulate the hydrodynamic distribution and the water quality variation along the river during water diversion processes. Secondly, the model was calibrated by the monitored data of estuary-tidal Level s and monitored water-quality data from June to August 2014, and validated by the observed data of the prototype water diversion test. Thirdly, the optimization of designed water diversion projects, see Table 1 and Fig. 1, was simulated by hydrodynamic-aquatic model and analyzed by continuation-dynamic constitution analysis. Lastly, the optimized result of the designed water diversion as a cooperative diversion project was implemented into an Ecological Water Diversion Project, which effects were discussed in water environment capacity.

Figure 6
figure 6

The flow chart of methodologies used in this study.

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Digital stable marker tracing

Principle of inflow water constitution

Let X be the set of all inflow water components, Y be the set of Conservative Substance, such that F: X → Y is a bijective mapping.

Conservative Substance refers to the mass that only has a physical effect, for example, transport, dilution and mixing, no chemical reaction or material loss while moving with the flow. That means they meet the mass conservation law, and their substance attenuation coefficient is zero.

Suppose Ci,j(0,0) is the concentration of Conservative Substance j (\(j \in Y\)) contained in the inflow water component i (\(i \in X\)), at the initial spatial and temporal coordinates, then get Formula (2):

$$C_{i,j} (0,0) = \left\{ {\begin{array}{*{20}c} 1 & {X(i) \to Y(j),} \\ 0 & {Otherwise.} \\ \end{array} } \right.$$
(2)

where Ci,j(0,0) is non-dimensional.

Digital stable marker tracing labels

Particle tracking is helpful in understanding the process of water movement30,31. In our simulation, the particle tracking was realized by Digital Tracing Labels:

Firstly, establish the bijective mapping with Conservative Substance and all inflow water constitutions of inflow rivers of the assessment sections. Secondly, label every inflow water constitution by Conservative Substance in the model. Then, simulate the time-variant concentration of each Conservative Substance according to the percentages of all water sources that flow into one section simultaneously. At last, the partition of each inflow water component can be quantified at the assessment sections.

Continuation-dynamic constitution analysis

Water age and residence time

In order to explore the hydraulic characteristic of flows with different concentrations, we calculated the residence time of background water source32,33,34,35 and the mean Water age of diversion water source on assessment section33,36,37, according to the theory of Water Age and Residence Time38,39.

Residence time of background water source means the required time for background water source particle that first leaving the assessment section during water diversion.

Age of diversion source water on assessment sections means the required time for water particle that transporting from the source to assessment section. Formula (3) showed the Mean age concentration of particle ai per Principle of inflow water constitution.

$${a}_{i}=\frac{1}{n}\sum_{t=1}^{n}{\tau }_{i}{C}_{i,j}\left(t,{x}_{0}\right),$$
(3)

where τi denotes the age of diversion water source particle i on the assessment section; Ci,j(t,x0) denotes the concentration of Conservative Substance j contained in the inflow water component i, at the temporal coordinate t and the assessment-section spatial coordinate x0. n denotes the maximum diversion time.

Continuation-dynamic constitution figure

The continuation-dynamic constitution figure shows the variation of every inflow water constitution in different water-quality concentration Level s on the assessment sections during the diversion.

Hydrodynamic: water quality model

Hydrodynamic model

The one-dimensional-unsteady hydrodynamic model describes the water flow state of a river or estuary based on the vertically-integrated mass and momentum conservation equation, showed as Formula (4) and (5), respectively, that is, the one-dimensional-unsteady Saint–Venant equation. The equations can be written as follows40.

$$\frac{\partial A}{{\partial t}} + \frac{\partial Q}{{\partial x}} = q$$
(4)
$$\frac{\partial Q}{{\partial t}} + \frac{{\partial \, \left( {\alpha \frac{{Q^{2} }}{A}} \right)}}{\partial x} + gA\frac{{\partial {\text{ h}}}}{\partial x} + \frac{{{\text{g}}Q\left| Q \right|}}{{ARC^{2} }} = 0$$
(5)

where A is the area of cross sections (m2), x and t denote the spatial and temporal coordinates, respectively; Q and q denote the discharge (m3/s) and lateral inflow (m3/s), respectively; α is the momentum correction factor, h is the mean water depth of cross section (m), R is the hydraulic radius, C is the Chezy coefficient, and g is the gravitational acceleration.

Water quality model

The water quality model is a one-dimensional advection dispersion model, and describes the water quality variation in channels based on 1-D convection–diffusion equation, see Formula (6). In order to assess the status of water quality during the diversion, the representative index NH3-N was used to reflect the influence of human beings in the center of the town24,41.

$$\frac{\partial AI}{{\partial t}} + \frac{\partial QI}{{\partial x}} - \frac{\partial }{\partial x}\left( {AD\frac{\partial I}{{\partial x}}} \right) = - AKI + I_{2} q$$
(6)

where I, D and K denote the NH3-N concentration (mg/L), diffusion coefficient (m2/s) and linear attenuation coefficient (d−1) of a water quality state variable, respectively; I2 is concentration of point source or confluence (mg/L).

Model parameters

The monitored data of estuary-tidal Level s and water qualities from June to August 2014 were used for parameter calibration, and the observed data of the prototype water diversion test20 were used for validation. The results are as follows:

(i) The monitored discharge on Sections of water diversion channels was used as the upper boundary; (ii) the corresponding monitored estuary-tidal Level on exports of drainage channels was adopted as the lower boundary; (iii) the closed boundary was set as the ordinary water Level 3.2 m; (iv) the range of river channel roughness coefficients n were 0.025–0.032; (v) the range of NH3-N daily attenuation coefficients K were 0.08/d–0.2/d.

The model performance is shown in Fig. 7. The relative errors between measurements and simulations were 15% for discharge and 20% for NH3-N concentration. Excellent model performance ensured further application for studying the designed diversion projects simulation.

Figure 7
figure 7

Results of hydrodynamic-water quality model on Section. The results of advection dispersion simulation were marked as curves and the measured processes on selected Sections were marked in points. R denotes the relative error between the simulated and measured data.

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Ecological Water Diversion Project

Pollution interception

Controlling pollutant loads of point sources is an essential part in water environment management, especially in urban areas. Based on the water-quality situation and requirement and characteristic of research area water environment that: urban domestic sewage as a significant pollutant has more than half NH3-N load in total, while urban and farmland runoff as main non-point pollutant sources have very large majorities of COD and NH3-N, respectively; we set the Sewage Interception Rate as 96% for the urban domestic sewage by improving the receiving and collecting rate of domestic sewage, as 85% for the industrial enterprise pollution by improving the standard of industrial enterprise pollution discharge, and as 75% for the farmland runoff by increasing the ecological buffer zone that cut off the non-point pollution transport path.

Cooperative water diversion

Cooperative water diversion means supplying water factor to strengthen the hydraulic connection, further enhance the self-purification capacity and ecological corridors to restore the aquatic ecosystems42. We optimized the cooperative water diversion based on Table 1.

Ecological restoration

As the results of local aquatic investigations and hydrostatic tests of aquatic plants, we selected the common plant species that: submerged plants like goldfish algae and foxtail algae to treat TN and retrain the release of P in sediments43; emerged plants like reed and lotus to adsorb N, P and NH3-N44. And considering the characteristics of different types of rivers, we selected suitable aquatic plant species to build three-dimensional plant communities45 as following: (i) Urban scenic rivers, with slow flow velocity, commercial and residential lands along, are to set ecological floating beds. (ii) Industrial buffer rivers, with relatively slow flow velocity, industrial and domestic lands along, are to build riparian vegetation buffer zone. (iii) Navigation protective rivers, with the functions of navigation, flood control, drainage etc., industrial and agricultural lands along, are to treat bank slope in vertical sections.

Project scheme

Considering the cooperative diversion optimization and measures above, we propose an Ecological Water Diversion Project scheme, see Table 2. Our simulation period selected the first 7 days of significant linear decrease in water quality concentration. Previous studies confirmed that the removal rates of NH4+-N, TN by related aquatic plants are all above 62.3% in the first 7 days46,47.