A vegetation construction method and system based on root system synergistic soil fixation in an estuary intertidal zone

Abstract

The application discloses a kind of based on root system synergic soil fixation estuary intertidal zone vegetation construction method and system, method includes: collecting the hydrodynamic parameter of target area, soil salinity distribution and topographic elevation data, generate the multidimensional environmental characteristic set reflecting tidal scour intensity and site condition;Based on multidimensional environmental characteristic set, output species combination and time window matching scheme;According to matching scheme, generate the multilayer planting structure model with ladder wave dissipation function;According to multilayer planting structure model, the planting density of each species, strip width and the number of alternate units are calculated, and the estuary intertidal zone vegetation construction scheme containing space configuration and seedling demand is generated.Using the embodiment of the application, the three-dimensional anchoring capacity of root network to the soil of intertidal zone can be enhanced, and the survival rate and ecological stability of vegetation community in complex hydrodynamic environment can be improved.

Description

Technical Field

[0001] This invention belongs to the field of ecological restoration technology, specifically a method and system for constructing intertidal vegetation in estuaries based on root-based synergistic soil stabilization. Background Technology

[0002] The intertidal zone of estuaries is a critical area of ​​land-sea interaction, and its ecosystem is extremely fragile due to multiple environmental factors, including periodic tidal erosion, wave erosion, and salinity stress. Traditional vegetation establishment methods often employ single-species planting or simple block arrangements, lacking systematic adaptation to the complex hydrodynamic environment. This results in low plant survival rates, poor root soil stabilization, and difficulty in forming long-term stable vegetation communities. While existing technologies address plant salt tolerance and tidal adaptability, they often overlook the synergistic and complementary effects of different species' root systems in space, failing to fully utilize the deep anchoring capacity of deep-rooted plants and the surface cover protection function of herbaceous plants. Furthermore, the timing of planting often relies on empirical judgment, lacking comprehensive consideration of tidal cycles, soil salinity dynamics, and plant dormancy patterns, further restricting the sustainability of vegetation establishment. Summary of the Invention

[0003] The purpose of this invention is to provide a method and system for constructing intertidal vegetation in estuaries based on root-based synergistic soil stabilization, in order to overcome the shortcomings of the prior art, enhance the three-dimensional anchoring ability of the root network to the intertidal soil, and improve the survival rate and ecological stability of vegetation communities in complex hydrodynamic environments.

[0004] One embodiment of this application provides a method for constructing intertidal vegetation in estuaries based on root-based synergistic soil stabilization, the method comprising: Collect hydrodynamic parameters, soil salinity distribution and topographic elevation data of the target area to generate a multi-dimensional environmental feature set reflecting the intensity of tidal erosion and site conditions. Based on the multidimensional environmental feature set, target specifications for deep-rooted herbaceous plants and salt-tolerant woody plants with established root networks are screened out, and the optimal planting time during the plant's dormancy period is determined, outputting a matching scheme for species combinations and time windows. Based on the matching scheme, combined with topographic elevation data, a strip-shaped alternating layout with herbaceous plant belts as the wave-facing protection layer and woody plant belts as the wave-recovery layer is designed to generate a multi-layered planting structure model with stepped wave-dissipating function. Based on the multi-layered planting structure model, the planting density, strip width, and number of alternating units for each species are calculated to generate an estuarine intertidal vegetation construction scheme that includes spatial configuration and seedling requirements.

[0005] Another embodiment of this application provides a system for constructing intertidal vegetation in estuaries based on root-based synergistic soil stabilization, the system comprising: The data acquisition module is used to collect hydrodynamic parameters, soil salinity distribution and topographic elevation data of the target area, and generate a multi-dimensional environmental feature set that reflects the intensity of tidal erosion and site conditions. The determination module is used to screen out the target specifications of deep-rooted herbaceous plants and salt-tolerant woody plants with established root networks based on the multidimensional environmental feature set, determine the optimal planting time during the plant's dormancy period, and output a matching scheme between species combination and time window. The design module is used to design, based on the matching scheme and combined with topographic elevation data, a strip-shaped alternating layout with herbaceous plant belts as the wave-facing protection layer and woody plant belts as the wave-recovery layer, to generate a multi-layered planting structure model with stepped wave-dissipating function. The generation module is used to calculate the planting density, strip width and number of alternating units of each species based on the multi-layered planting structure model, and generate an estuarine intertidal vegetation construction scheme that includes spatial configuration and seedling requirements.

[0006] Another embodiment of this application provides a storage medium storing a computer program, wherein the computer program is configured to execute the method described in any of the preceding claims when running.

[0007] Another embodiment of this application provides an electronic device including a memory and a processor, wherein the memory stores a computer program and the processor is configured to run the computer program to perform the method described in any of the preceding claims.

[0008] Compared with existing technologies, the present invention provides a method for constructing intertidal vegetation in estuaries based on root-based synergistic soil stabilization, which can enhance the three-dimensional anchoring ability of the root network to the intertidal soil and improve the survival rate and ecological stability of vegetation communities in complex hydrodynamic environments. Attached Figure Description

[0009] Figure 1 A hardware structure block diagram of a computer terminal for a method of constructing intertidal vegetation in estuaries based on root-based synergistic soil stabilization, provided in an embodiment of the present invention. Figure 2 A flowchart illustrating a method for constructing intertidal vegetation in estuaries based on root-based synergistic soil stabilization, provided as an embodiment of the present invention. Figure 3 This is a schematic diagram of a estuarine intertidal vegetation construction system based on root-based synergistic soil stabilization, provided as an embodiment of the present invention. Detailed Implementation

[0010] The embodiments described below with reference to the accompanying drawings are exemplary and are only used to explain the present invention, and should not be construed as limiting the present invention.

[0011] The present invention first provides a method for constructing intertidal vegetation in estuaries based on root-based synergistic soil stabilization. This method can be applied to electronic devices, such as computer terminals, specifically ordinary computers.

[0012] The following detailed explanation uses a computer terminal as an example. Figure 1 This is a hardware structure block diagram of a computer terminal for a method of constructing intertidal vegetation in estuaries based on root-based synergistic soil stabilization, provided as an embodiment of the present invention. Figure 1 As shown, the computer device includes a processor, memory, and network interface connected via a system bus, wherein the memory may include non-volatile storage media and internal memory.

[0013] See Figure 2 The present invention provides a method for constructing intertidal vegetation in estuaries based on root-based synergistic soil stabilization, which may include the following steps: S201 collects hydrodynamic parameters, soil salinity distribution and topographic elevation data of the target area to generate a multi-dimensional environmental feature set reflecting the intensity of tidal erosion and site conditions. Specifically, hydrological monitoring sections can be set up in the target area along the direction perpendicular to the coastline. The flow velocity and direction data and tidal level change data during the tidal cycle can be continuously collected by an acoustic Doppler current profiler and a pressure-type tide gauge to generate the original set of hydrodynamic parameters. The core of this step is to acquire basic tidal dynamic data of the intertidal zone of the target estuary through standardized hydrological monitoring deployment and continuous data acquisition. After preprocessing, a structured set of raw hydrodynamic parameters is formed, providing a core basis for subsequent tidal scour intensity analysis. The specific implementation method is as follows: The establishment of hydrological monitoring sections must adhere to the principles of representativeness and full coverage. Based on the shoreline length, topographic complexity, and tidal dynamic distribution characteristics of the target area, monitoring sections should be established perpendicular to the coastline. The spacing between sections should be set at 500-1000 meters, depending on the scope of restoration. If the target area has special areas such as sharp tidal bays or abrupt topographic changes, the spacing should be increased to 300 meters to ensure that the monitoring data fully reflects the hydrodynamic differences between different areas. Each monitoring section should have one monitoring point for each of the three tidal zones: high tide, mid-tidal, and low tide. The mid-tidal zone, being the area with the strongest tidal erosion, is the core monitoring point. This point must be located in a natural tidal flat area without any artificial structures obstructing the view to avoid data distortion.

[0014] Data acquisition employed a combined acoustic Doppler current profiler and a pressure-type tide gauge. The acoustic Doppler current profiler utilized the acoustic Doppler effect to monitor the water body in 1-meter water layers from the surface to the bottom, collecting real-time data on the velocity and direction of each layer. Velocity was measured in meters per second, and direction was measured clockwise from true north (0 degrees). The pressure-type tide gauge calculated the tide level by monitoring the hydrostatic pressure of the water body. It was installed on fixed bases at each monitoring point on the seabed and continuously recorded tidal changes, with the tide level measured in meters, using the local theoretical depth datum as the zero point. The data acquisition duration needed to cover at least three complete tidal cycles. For irregular semi-diurnal tidal areas, continuous acquisition for 72 hours was sufficient. The sampling frequency was uniformly set to 10Hz to ensure the capture of abrupt changes in velocity and tidal level during high and low tides.

[0015] After data collection, the raw data were preprocessed. First, abnormal data caused by instrument interference and water flow disturbance were removed using the 3σ principle. Then, the layered velocity data were weighted and averaged to obtain the tidal average velocity at each monitoring point. At the same time, core characteristic parameters such as maximum velocity, ebb and flow duration, average tidal range, and maximum tidal range for each tidal cycle were statistically analyzed. Finally, all monitoring data were structured and organized according to monitoring section, monitoring point, and collection time. The geographical coordinates, tidal zone, and collection equipment corresponding to each data point were labeled to generate a raw hydrodynamic parameter set containing time-series data of velocity and direction, tidal level change curves, and tidal cycle characteristic parameters. All data in the parameter set were retained to three decimal places to ensure data accuracy.

[0016] Soil sampling points were set up at the monitoring section using the grid sampling method. The soil salinity value of each sampling point was measured using a portable salinity meter and conductivity meter. A spatial distribution map of soil salinity was generated by the Kriging interpolation algorithm. The core of this step is to achieve a global spatial representation of soil salinity through systematic soil sampling and precise salinity measurement, combined with spatial interpolation algorithms. This generates a spatial distribution map that intuitively reflects the characteristics of salinity distribution, providing spatial data for subsequent plant salt tolerance screening. The specific implementation method is as follows: Soil sampling points were strategically placed around each hydrological monitoring section, using a regular grid sampling method. The grid size was set at 50m × 50m, with each grid node serving as a standard sampling point. For areas with meandering shorelines and potential abrupt salinity changes at the edge of the tidal flats, the grid size was increased to 20m × 20m to ensure accurate reflection of spatial salinity variations. Surface mud and debris were removed during sampling, and soil samples were collected from a depth of 0-30cm. This soil layer is the primary distribution layer for the roots of intertidal plants in the estuary, and its salinity directly affects plant growth and development. Each sampling point underwent three repeated sampling measurements to avoid accidental errors from single sampling.

[0017] Salinity determination employed a combined calibration method using a portable salinity meter and a conductivity meter. First, soil samples were prepared into a soil extract at a soil-to-water ratio of 1:5. After thorough stirring and clarification, the salinity of the extract was directly measured using a portable salinity meter (parts per thousand). Simultaneously, the conductivity of the extract was measured using a conductivity meter (millisiemens per centimeter). The linear correlation between salinity and conductivity was used to calibrate the salinity measurement results. Values ​​with deviations exceeding ±0.2‰ were discarded. The average of three valid measurements was taken as the final soil salinity value for that sampling point, ensuring the accuracy of the results.

[0018] Kriging interpolation was used for spatial interpolation of salinity. Based on the principle of geospatial autocorrelation, this algorithm is one of the optimal interpolation methods for simulating the spatial distribution of soil properties. First, the salinity values ​​of all sampling points were analyzed by variogram. By fitting spherical, exponential, and Gaussian models, the optimal semivariogram model was determined to clarify the spatial structure characteristics and range of soil salinity. Then, based on the grid framework of the target area, the salinity values ​​of unsampled areas were interpolated and estimated. The grid resolution of the interpolated soil salinity spatial distribution map was set to 10 meters to match the resolution of the subsequent topographic data. The map presents the salinity value of each spatial location in grid form, and marks the high-value areas, low-value areas, and gradual trends of salinity, intuitively reflecting the spatial distribution pattern of soil salinity in the target area.

[0019] A drone-borne lidar was used to perform oblique photogrammetry on the target area to obtain high-precision point cloud data, which was then filtered and classified to generate a digital elevation model. The core of this step is to utilize the 3D scanning technology of UAV-borne LiDAR to acquire high-precision terrain point cloud data of the target area. After professional data processing, a digital elevation model is generated, which accurately reflects the terrain elevation, slope, and other site conditions, providing a foundation for subsequent terrain zoning and layout design. The specific implementation method is as follows: Unmanned aerial vehicle (UAV)-borne lidar oblique photogrammetry requires selecting a suitable operating environment, avoiding rainy, foggy, and windy weather. Operations should be conducted during clear periods with wind speeds below level 3 and cloud cover below 30%, ensuring uninterrupted propagation and reflection of the laser beam. Flight parameters should be standardized, with a flight altitude controlled at 100 meters, a flight path overlap rate of 80%, and a lateral overlap rate of 70%. This parameter combination ensures the integrity and continuity of point cloud data, avoiding missed data areas. The lidar point cloud acquisition density should be no less than 100 points / square meter to ensure accurate capture of the subtle undulations of the tidal flat terrain.

[0020] During the operation, the UAV-borne lidar scans the target area across the entire region by emitting laser beams, receiving the reflected echoes from the laser beams and ground objects, and combining this with GPS positioning and inertial navigation systems to acquire raw point cloud data containing three-dimensional spatial coordinates. The geographic coordinates of the point cloud data are initially based on the WGS-84 coordinate system, and will be uniformly projected and converted later. The raw point cloud data contains ground points, vegetation points, man-made structures, and other miscellaneous points, requiring preprocessing. First, coordinate correction is performed, converting all point cloud data to the Gauss-Kruger projection coordinate system, with geographic coordinate accuracy controlled within 1 meter. Then, a progressive triangular mesh filtering method is used for filtering. This method can accurately distinguish between ground points and non-ground points by constructing a triangular mesh model, gradually eliminating non-ground point clouds such as vegetation, floating mud, and man-made debris, retaining only ground point clouds that reflect the actual terrain.

[0021] The filtered ground point cloud was subjected to gridded interpolation. Inverse distance weighting was used for spatial interpolation, converting the ground point cloud data into regular raster data with a resolution of 1 meter, consistent with the resolution of the soil salinity spatial distribution map. This resulted in the generation of a digital elevation model (DEM). This model accurately reflects the site characteristics of the target area, including elevation, slope, aspect, and topographic relief. Elevation values ​​are in meters, with the local theoretical depth datum as the zero point. The model's elevation error does not exceed ±0.1 meters, meeting the accuracy requirements for intertidal topographic zoning and vegetation layout design in estuaries.

[0022] The original hydrodynamic parameter set, soil salinity spatial distribution map and digital elevation model are spatially registered and fused to calculate the tidal erosion intensity index, salinity stress level and topographic slope factor, and finally generate a multidimensional environmental feature set.

[0023] The core of this step is to achieve precise spatial matching and fusion of multi-source environmental data. By quantitatively calculating core environmental assessment factors, a multi-dimensional environmental feature set that comprehensively reflects the intensity of tidal erosion and site conditions is formed, providing complete environmental data support for subsequent species selection, planting time determination, and layout design. The specific implementation method is as follows: First, spatial registration is carried out to unify the original hydrodynamic parameter set, soil salinity spatial distribution map, and digital elevation model to the same Gauss-Kruger projection coordinate system, with the geographic coordinate accuracy controlled within 1 meter. For discrete monitoring point data in the original hydrodynamic parameter set, spatial interpolation is used to convert them into raster data with the same resolution as the soil salinity map and digital elevation model, forming a hydrodynamic raster layer. This ensures that the three types of data can achieve accurate one-to-one matching in spatial location, without spatial misalignment or offset.

[0024] After spatial registration is completed, data fusion is performed. By overlaying layers, the hydrodynamic raster layer, the soil salinity spatial distribution map layer, and the digital elevation model layer are superimposed to construct a spatial dataset containing multiple environmental elements. Each raster cell in this dataset corresponds to a unique geographic coordinate and contains the hydrodynamic parameters, soil salinity value, and topographic elevation value of that location, thus achieving integrated integration of multi-source environmental data.

[0025] Based on the fused spatial dataset, three core environmental assessment factors were quantitatively calculated. The first is the tidal erosion intensity index, which comprehensively reflects the erosion capacity of tides on mudflats. The average tidal velocity V (m / s), average tidal range H (m), and wave shear force τ (Pa) were selected as calculation factors, and a weighted summation method was used. The calculation formula is I = 0.4V + 0.3H + 0.3τ, where the weights are determined according to the contribution of each factor to tidal erosion. A larger I value indicates a stronger tidal erosion intensity in the area. The index value is retained to two decimal places. The second is the salinity stress level. Soil salinity values ​​are used to classify stress into three levels: low salinity stress level 1 (salinity < 5‰), medium salinity stress level 2 (5‰ ≤ salinity ≤ 15‰), and high salinity stress level 3 (salinity > 15‰). The level values ​​directly reflect the degree of stress that soil salinity places on plants. The third factor is the topographic slope factor, which is calculated grid by grid cell. The calculation formula is S = Δh / Δx, where Δh is the elevation difference between adjacent grid cells (unit: m), and Δx is the horizontal distance between adjacent grid cells (unit: m). The S value reflects the steepness of the terrain. The steeper the slope, the more unstable the tidal flat terrain. The factor value is retained to three decimal places.

[0026] Finally, the calculated tidal scour intensity index, salinity stress level, and topographic slope factor are integrated with the fused original hydrological, soil, and topographic data. The data are then structured and organized by raster unit, with each raster unit labeled with its geographic coordinates, environmental parameter values, and core evaluation factor values. This results in a multidimensional environmental feature set that reflects the intensity of tidal scour and site conditions. This feature set is a rasterized spatial dataset that can comprehensively and accurately reflect the environmental heterogeneity of the target area. It serves as the core data foundation for subsequent species screening, time window determination, and vegetation layout design.

[0027] S202, Based on the multidimensional environmental feature set, select the target specifications of deep-rooted herbaceous plants and salt-tolerant woody plants with established root networks, determine the optimal planting time during the plant's dormancy period, and output the matching scheme of species combination and time window. Specifically, the tidal erosion intensity index and salinity stress level, which are concentrated in multidimensional environmental features, can be analyzed and matched with the pre-built coastal wetland plant germplasm resource bank to screen out a list of candidate species that can tolerate the target environmental stress. The core of this step is to analyze the key environmental stress characteristics of the target area and accurately match them with a pre-established germplasm resource bank to screen suitable plants for the water and salt stress environment of the intertidal zone in the estuary. This provides a basis for determining the scope of subsequent species specifications. The specific implementation method is as follows: First, the multidimensional environmental feature set was analyzed in a targeted manner to extract the tidal scour intensity index and salinity stress level data of all grid cells in the set. The dominant tidal scour intensity range and salinity stress level of the target area were calculated by spatial statistical method. The dominant range and level are the environmental stress characteristics that account for more than 70% of the entire target area, which can accurately reflect the core environmental stress type of the target area. For example, the tidal scour intensity index I ≥ 0.8 in the strong tidal scour area and the soil salinity in the moderate salinity stress area is stable at 5‰-15‰. After analysis, it is clear that the target area needs to select coastal wetland suitable plants that have both corresponding scour resistance and salt tolerance. The pre-constructed coastal wetland plant germplasm resource bank is a localized database of suitable plants. It contains complete information on typical suitable plants for coastal wetlands in my country, including species classification, core biological characteristics, environmental stress tolerance indicators, root development characteristics, seedling age suitability, and field planting test data. Among them, the environmental stress tolerance indicators include the plant's salinity tolerance threshold, water flow shear force limit, and flooding tolerance duration. These thresholds and limits are derived from indoor stress tests and long-term field monitoring, which can accurately reflect the actual tolerance capacity of plants.

[0028] Species matching employed a dual-index threshold matching method. First, salinity stress level was used as the first matching dimension, matching the dominant salinity range of the target area with the salinity tolerance thresholds of plants in the germplasm resource bank. Plants with salinity tolerance thresholds not lower than the highest salinity value in the target area were selected, while species with insufficient salt tolerance were eliminated. Second, tidal erosion intensity index was used as the second matching dimension. Based on the shear stress resistance requirements corresponding to the index, plants in the germplasm resource bank with deep root structures, the ability to form underground root networks, and shear stress resistance limits not lower than the shear stress of the target area were selected, while species with shallow roots and weak erosion resistance were eliminated. After both matching processes, the results were integrated and deduplicated. Plants that met the stress tolerance requirements but were unsuitable for the intertidal mudflat conditions of estuaries were also removed. The plants were categorized into deep-rooted herbaceous plants and salt-tolerant woody plants, and key information such as core stress tolerance characteristics, root development cycle, and seedling age type were labeled for each species. Finally, a list of candidate species capable of tolerating the target environmental stress was generated, laying the core foundation for subsequent precise selection of species specifications.

[0029] Root development characteristics data of deep-rooted herbaceous plants and salt-tolerant woody plants were extracted from the candidate species list. The root network maturity age required for herbaceous plants was determined based on the scour intensity index. Three-year-old reeds were output as the target specifications for deep-rooted herbaceous plants. The core of this step is to analyze the root development patterns of candidate herbaceous plants based on the tidal erosion requirements of the target area, determine the maturity age at which a stable soil-fixing root network can be formed, and finally select suitable target specifications for herbaceous plants. The specific implementation method is as follows: Root development characteristics data of all deep-rooted herbaceous plants and salt-tolerant woody plants were extracted from the candidate species list. For herbaceous plants, key data extracted included root maturity age, rhizome tillering ability, root network formation time, shear stress resistance at different seedling ages, and conditions for underground root cushion structure formation. For woody plants, key data extracted included root type, initial root depth, root lignification degree, and the correlation between seedling age and root development. All data were derived from field experiments and indoor observations in the germplasm resource bank to ensure data authenticity and suitability. Based on the tidal erosion intensity index, the soil stabilization and wave mitigation requirements of herbaceous plant roots in the target area were quantified. The tidal erosion intensity index is positively correlated with the shear stress resistance of herbaceous plants; the higher the index value, the stronger the shear stress resistance required. The core determinant of shear stress resistance is the maturity of the root network. Only when the root network is fully formed and an underground root cushion structure is established can effective anchoring of the topsoil and effective reduction of tidal hydrodynamic forces be achieved.

[0030] A comparative analysis of the root development characteristics of candidate deep-rooted herbaceous plants was conducted. As a native dominant deep-rooted herbaceous plant in coastal wetlands, reed exhibits distinct stages in root development. 1-2 year old reeds only form slender fibrous root structures, without a complete underground root network or obvious root cushion structure, resulting in weak resistance to water flow shear and inability to meet the soil stabilization and wave dissipation requirements in areas with moderate to strong tidal erosion. 3-year-old reeds, on the other hand, have fully developed underground rhizomes, forming a dense and interwoven root network and a stable underground root cushion structure. The rhizomes possess strong tillering ability, and their resistance to water flow shear is more than three times higher than that of 1-2 year old seedlings. This effectively anchors the surface soil and reduces tidal erosion kinetic energy, making them suitable for intertidal zones in estuaries with varying tidal erosion intensities. Based on this, the maturity age of the root network of herbaceous plants was determined to be 3 years. The final target specification for deep-rooted herbaceous plants was 3-year-old reeds. At the same time, the additional characteristics of this specification were clarified, namely, the reeds must be of local seed source, retain rhizomes with tillering ability, the diameter of the rhizomes should be controlled at 0.5-0.8cm, each clump should retain 3-5 dormant buds, and the reeds should be obtained by rhizome tillering. These characteristics can ensure that the reeds can be quickly established after planting and form a continuous protective belt.

[0031] Based on the assessment of salt tolerance requirements of woody plants according to the salt stress level, and combined with the salt tolerance test data of plants of different ages in the germplasm resource bank, two-year-old container seedlings of Tamarix chinensis that have undergone salt acclimatization treatment were selected as the target specifications for salt-tolerant woody plants. The core of this step is to analyze the salt tolerance and growth characteristics of candidate woody plants at different seedling ages, based on the salinity stress requirements of the target area, and to screen out target sizes of woody plants that can adapt to high-salt environments after salinity acclimatization. The specific implementation method is as follows: Based on the salinity stress level of the target area, the salt tolerance requirements of woody plants are accurately assessed. The salinity stress level is positively correlated with the salinity tolerance threshold of woody plants. Low salinity stress level 1 (salinity < 5‰) requires the salinity tolerance threshold of woody plants to be ≥ 8‰, medium salinity stress level 2 (5‰ ≤ salinity ≤ 15‰) requires the salinity tolerance threshold to be ≥ 15‰, and high salinity stress level 3 (salinity > 15‰) requires the salinity tolerance threshold to be ≥ 20‰. At the same time, the dynamic changes in water and salt in the intertidal zone of the estuary also require woody plants to have a certain salinity adaptability and be able to tolerate short-term salinity fluctuations. Salt tolerance test data of candidate salt-tolerant woody plants at different seedling ages were extracted from the germplasm resource bank. The data included core indicators such as lignification degree, root integrity, unacclimated salt tolerance threshold, salt tolerance improvement after salt acclimation, and planting survival rate of 1-year-old, 2-year-old, and 3-year-old seedlings. At the same time, the adaptability of each seedling age to wild planting was combined to exclude types that are too old and difficult to transplant, or too young and have weak stress resistance.

[0032] As a typical salt-tolerant woody plant in coastal wetlands, tamarisk exhibits significant differences in salt tolerance and growth characteristics at different seedling ages. One-year-old tamarisk seedlings have low lignification, fine and poorly intact root systems, and a salt tolerance threshold of only 8‰ in their unacclimated state. Even after salinity acclimation, the improvement in salt tolerance is limited, and the seedling recovery period after planting is long, resulting in extremely low survival rates in the high-salt environment of the intertidal zone in estuaries. While three-year-old tamarisk seedlings have high lignification and strong salt tolerance, their excessive size makes them susceptible to damage. Container seedlings are difficult to cultivate, easily damaging the taproot during transplantation, and their adaptability is not as good as 2-year-old seedlings. Two-year-old tamarisk container seedlings have moderate lignification, complete root systems with preliminary lignification, and the root ball effectively protects the roots. In their unacclimated state, their salt tolerance threshold reaches 12‰, and after salinity acclimation, this threshold can be increased to over 18‰, meeting the salt tolerance requirements for medium to high salt stress levels. Furthermore, container seedlings have a short recovery period after transplanting, allowing for rapid root development. Based on this, and combined with the salt tolerance requirements assessed by salinity stress levels, 2-year-old tamarisk container seedlings were selected as the target specification for salt-tolerant woody plants. The core requirements for this specification were defined as follows: plant height controlled at 60-80cm, root ball diameter approximately 15cm, and at least 3 months of salt tolerance acclimation before planting. The salinity of the acclimation solution should be consistent with the average salinity of the target area, gradually increasing to 1.2 times the highest salinity of the target area, thus achieving a targeted improvement in the salt tolerance of tamarisk.

[0033] Based on topographic elevation data and historical meteorological data with multidimensional environmental features, the temperature variation pattern and tidal spring tide distribution of the target area are analyzed to determine the dormant period when plant transpiration is weak and the tidal flats are relatively stable. Finally, a matching scheme containing species combinations and optimal planting time is output.

[0034] The core of this step is to analyze the suitable planting time by combining the topography, meteorology, and tidal characteristics of the target area, and to integrate the selected species specifications with the optimal planting time to form a standardized species combination and time window matching scheme. The specific implementation method is as follows: First, the necessary basic data is integrated and analyzed. Topographic elevation data is extracted from multi-dimensional environmental features. This data reflects the flooding frequency and elevation distribution of the tidal flats in the target area, and helps to judge the stability of the tidal flats. At the same time, historical meteorological data and tidal monitoring data of the target area over the past 10 years are collected. The historical meteorological data includes core indicators such as monthly average temperature, monthly minimum temperature, and seasonal precipitation distribution. The tidal monitoring data includes information such as the monthly distribution patterns of astronomical high tides and typhoon high tides, and the degree of disturbance of the tidal flat matrix. All data ensure the continuity of the time series and the spatial representativeness. Based on the analysis of historical meteorological data on temperature variation patterns in the target area, the intensity of plant transpiration is significantly positively correlated with temperature. When the average monthly temperature is above 15℃, plants are in a vigorous growth period with strong transpiration. In the high-salt environment of the intertidal zone of the estuary, plants are prone to physiological water shortage, resulting in a high mortality rate during the seedling establishment period after planting. When the average monthly temperature is below 10℃, both herbaceous and woody plants enter a natural dormancy period, and the above-ground parts turn yellow or fall off. Transpiration is significantly reduced, and water stress is greatly reduced. Planting at this time can effectively reduce the water consumption of plants and is conducive to the establishment and development of underground roots.

[0035] Analysis of tidal flat stability based on tidal spring tide distribution data reveals that the stability of the intertidal matrix in the estuary is closely related to the spring tide distribution. From July to October, typhoons are frequent and spring tides are concentrated. During this period, tidal dynamics are strong, and the intertidal matrix is ​​severely eroded and disturbed, making seedlings susceptible to erosion after planting, resulting in a low success rate of establishment. From October of the same year to April of the following year, spring tides are less frequent, tidal dynamics are weak, and the intertidal matrix is ​​relatively stable. Combined with topographic elevation data, it can be seen that the frequency of tidal flat flooding is low during this period, allowing seedling roots to contact the air, which is beneficial for root respiration and root development. Based on the analysis of temperature variation patterns and tidal flat stability, the optimal planting period during the plant dormancy period was determined. This period must simultaneously meet two core conditions: low transpiration and relatively stable tidal flats. Overall, December to March of the following year is the optimal period. During this period, the average monthly temperature in the target area is below 10℃, plant transpiration is reduced to its lowest level of the year, underground roots are in a latent development period, and they can quickly take root after planting. Furthermore, it completely avoids the typhoon and spring tide periods, the stability of the tidal flat matrix reaches its best level of the year, and the risk of seedling erosion is greatly reduced.

[0036] Finally, the species specifications determined in the preliminary screening were integrated with the optimal planting time to output a matching scheme that includes species combinations and time windows. The scheme clearly defines the core species combination as 3-year-old local seed reeds (deep-rooted herbaceous plants) and 2-year-old container seedlings of tamarisk (salt-tolerant woody plants) that have undergone at least 3 months of salinity acclimatization. It also marks the detailed target specifications, acclimatization requirements, and propagation methods of each species, and clarifies that the optimal planting time is from December of the current year to March of the following year. The scheme also explains the environmental advantages and suitability of this planting time. The scheme combines the accuracy of species specifications with the practicality of planting time, providing a clear basis for the subsequent design of vegetation spatial layout.

[0037] S203. Based on the matching scheme, and combined with topographic elevation data, design a strip-shaped alternating layout with herbaceous plant belts as the wave-facing protection layer and woody plant belts as the wave-recovery layer to generate a multi-layered planting structure model with stepped wave-dissipating function. Specifically, topographic profiles perpendicular to the coastline of the target area can be extracted based on the digital elevation model to identify the boundary elevations of high tide shoals, mid-tide shoals, and low tide shoals, and generate topographic zoning data. The core of this step is to extract profile lines that reflect the topographic undulations of the tidal flats through spatial analysis of a high-precision digital elevation model, and to determine the boundary elevations of the tidal flat zones by combining tidal hydrological characteristics. This achieves refined topographic zoning of the intertidal zone of the estuary, providing a topographic spatial basis for subsequent vegetation layout. The specific implementation method is as follows: The digital elevation model (DEM) is based on high-precision raster data acquired using UAV-borne LiDAR, with a spatial resolution of 1 meter and an elevation error of no more than ±0.1 meters. Before extracting topographic profiles, the model's edges are cropped to retain only the tidal flat topographic data of the target restoration area, eliminating invalid areas such as land-based man-made structures and water bodies. The extraction of topographic profiles follows the principles of equal spacing and full coverage, with profiles laid out perpendicular to the coastline. The lateral spacing of the profiles is set according to the topographic complexity of the target shoreline: 500 meters in areas with gentle terrain, and 300 meters in areas with significant topographic undulations and winding shorelines, ensuring that all profiles completely cover the target area and accurately reflect the longitudinal elevation changes of the tidal flats. The extraction process uses a profile generation tool, starting from the coastline baseline and extending 100 meters outward from the mean low tide level. Each profile records continuous elevation-horizontal distance coordinate data, with elevation values ​​using the local theoretical depth datum as the zero point and horizontal distance measured from the coastline baseline, both in meters.

[0038] To identify the boundary elevations of high tide shoals, mid-tide shoals, and low tide shoals, it is necessary to combine tidal level characteristic data from the original hydrodynamic parameter set and select three core tidal level values—mean high tide level (H1), mean mid-tide level (H2), and mean low tide level (H3)—as the boundary criteria. These three tidal level values ​​are the statistical averages of monitoring the target area over three consecutive tidal cycles, accurately reflecting the flooding frequency and tidal influence range of the tidal flats. The specific zoning criteria are as follows: areas with elevation values ​​higher than H1 in the digital elevation model are high tide shoals, which have the lowest flooding frequency and the most stable tidal matrix; areas with elevation values ​​between H1 and H2 are mid-tide shoals, which are subject to alternating high and low tides and are the core area with the strongest tidal erosion; areas with elevation values ​​between H2 and H3 are low tide shoals, which are chronically flooded and have complex hydrodynamic conditions. All extracted topographic profiles are segmented by elevation according to this standard. Then, spatial interpolation is used to extend the zoning results of the profiles to the entire target area, generating topographic zoning data that combines raster and vector data. The raster data has the same resolution as the digital elevation model, while the vector data labels the boundary lines, core elevation range, and geographic coordinates of each tidal flat zone. At the same time, the tidal action characteristics of each zone are labeled. The final topographic zoning data can clearly reflect the spatial matching relationship between the topography and tidal action of the tidal flats in the target area.

[0039] Based on the species combination and topographic zoning data in the matching scheme, it is determined that the wave protection layer should be deployed in the mid-to-low tidal flat area where the tidal erosion is most intense, and the preliminary layout range of the herbaceous plant protection belt is output. The core of this step is to combine the functional characteristics of species combinations with the hydrodynamic features of tidal flat zones to determine the core deployment area of ​​the wave-facing protection layer, delineate the preliminary spatial range of the herbaceous plant protection zone, and achieve a precise match between vegetation function and site environment. The specific implementation method is as follows: First, the functional positioning of species combinations in the matching scheme is analyzed. The scheme identifies 3-year-old reeds as deep-rooted herbaceous plants with a dense underground rhizome network and root cushion structure, exhibiting strong resistance to water flow shearing forces. They effectively anchor the surface soil and reduce tidal erosion, making them a core construct species for the wave-facing protective layer. 2-year-old containerized tamarisk seedlings are salt-tolerant woody plants with weak initial root development, requiring a stable, low-hydrodynamic environment for growth, making them a core construct species for the community restoration layer. Combining the tidal characteristics of the topographic zoning data, the mid-to-low tidal flat area is the region most severely affected by tidal erosion. This area experiences high tidal velocity, strong wave kinetic energy, and poor tidal substrate stability, making it a core protective area for vegetation construction. Conversely, the high tidal flat area has low flooding frequency and weak hydrodynamics, suitable for the root development of woody plants. Therefore, the core deployment area for the wave-facing protective layer is determined to be the entire mid-to-low tidal flat region, utilizing the soil-fixing and wave-dissipating functions of reeds to create a stable environmental foundation for subsequent woody plant planting.

[0040] The initial layout of the herbaceous vegetation protection zone should adhere to the principles of parallel shoreline, conformity to topography, and full coverage. The protection zone should run strictly parallel to the coastline to ensure comprehensive lateral reduction of tidal dynamics. Its longitudinal extent should perfectly match the elevation range of the low and medium tidal flats, from the average low tide level (H3) to the average mid-tide level (H2), ensuring coverage of all areas with strong erosion. The lateral extent of the protection zone should cover the entire low and medium tidal flat area of ​​the target shoreline, with no blind spots. For low and medium tidal flat areas with a slope greater than 5°, the longitudinal extent of the protection zone should be appropriately extended 10-20 meters towards the high tide level to compensate for the increased hydrodynamic erosion caused by the slope. For areas with abrupt topographic changes such as shallow ditches and depressions within the tidal flats, the protection zone should extend naturally with the terrain to ensure continuity of protection. The final output of the preliminary layout of the herbaceous plant protection zone is vector boundary data, which is marked with the geographical coordinates, four boundaries, longitudinal elevation intervals and lateral length of the protection zone. At the same time, it is associated with the corresponding topographic zoning features and hydrodynamic intensity data, providing a clear spatial reference for the subsequent layout of the woody plant restoration zone.

[0041] On the leeward side of the herbaceous plant protection zone, the location of the woody plant restoration zone is determined based on the topographic uplift and wave energy attenuation patterns to ensure that it is in a low-energy deposition environment and outputs a strip structure with alternating herbaceous and woody plant arrangements. The core of this step is to utilize the wave-dissipating effect of the herbaceous plant protective belt and the natural characteristics of tidal flat uplift to determine the optimal location for the woody plant restoration belt, constructing an alternating strip layout of herbaceous plants protecting woody plants, and ensuring that the woody plants are in a stable, low-energy sedimentation environment. The specific implementation method is as follows: When tidal waves pass through the herbaceous plant protective belt, their energy is attenuated by the obstruction of the above-ground stems of the reeds and the anchoring effect of their underground roots. Following the law that wave energy decreases exponentially with the increase of the width of the vegetation belt, the protective belt formed by three-year-old reeds can reduce the kinetic energy of tidal waves by 60%-80%, and the attenuation effect of wave energy reaches its peak on the lee side of the protective belt. At the same time, the tidal flat topography of the target area has a natural upward trend from the low tide flat to the high tide flat, and the hydrodynamic force is further weakened with the rise in topography. The combination of these two factors creates a low-energy sedimentation environment with weak hydrodynamic force and easy sediment deposition on the lee side of the herbaceous plant protective belt. This environment can effectively reduce the risk of erosion of the tamarisk root system and provide stable substrate conditions for its rooting and development, making it the optimal location for the woody plant restoration belt.

[0042] When determining the location of the woody plant restoration zone, the principles of close proximity to the protection zone, conformity to elevation, and suitability to sedimentation are followed. The restoration zone is located close to the leeward side of the herbaceous plant protection zone, with a distance of 0-5 meters between them to ensure full utilization of the wave-dissipating effect of the protection zone and to avoid additional hydrodynamic disturbance areas. The elevation range of the restoration zone is set in the high tide tidal flat area from the average mid-tide level (H2) to the average spring tide high tide level (H1). This area has a low flooding frequency, stable tidal flat matrix, and is located in a sediment deposition zone, which can gradually improve soil fertility and suit the growth needs of tamarisk. For areas with extremely strong tidal erosion, the restoration zone is appropriately moved inward by 5-10 meters towards the high tide tidal flat to further enhance the stability of the growth environment.

[0043] Based on the location of herbaceous plant protection zones and woody plant restoration zones, a strip structure with alternating herbaceous and woody plant arrangements is output. This structure is a strip-like alternating arrangement parallel to the coastline, with core features including herbaceous plants on the wave-facing side, woody plants on the leeward side, continuous strips, and elevation stratification. The structure clearly marks the arrangement direction, spatial relative position, elevation range, and core function of each herbaceous plant protection zone and woody plant restoration zone. Simultaneously, the strip structure is spatially correlated with topographic zoning data and hydrodynamic data, marking key parameters such as tidal erosion intensity, wave energy attenuation rate, and sediment deposition rate for each zone. This strip structure is in vector format, consistent with the geographic coordinate system and spatial resolution of the previously laid out data, and can intuitively reflect the spatial configuration relationship between herbaceous and woody plants, providing a basic framework for subsequent layout optimization.

[0044] By combining tidal level data and wave attenuation models from hydrodynamic parameters, the efficiency of the zonal layout in reducing tidal energy at each level is calculated. The width ratio and alternation frequency of herbaceous plant zones and woody plant zones are optimized, and finally a multi-layered planting structure model with stepped wave dissipation function is generated.

[0045] The core of this step is to quantitatively analyze the tidal energy reduction effect of the strip layout using a wave attenuation model, optimize the strip width ratio and alternation frequency based on the hydrodynamic characteristics of the target area, and construct a multi-layered planting structure model with stepped wave dissipation function to achieve gradual reduction of tidal energy and scientific optimization of vegetation layout. The specific implementation method is as follows: First, an empirical wave attenuation model suitable for intertidal vegetation in estuaries is selected. This model, based on linear wave theory, uses tidal data, wave characteristic parameters, vegetation belt width, and vegetation density as core calculation factors. It can accurately quantify the energy reduction efficiency of herbaceous vegetation on tidal waves. The core calculation logic of the model is: wave energy reduction efficiency η = 1 - e^(-k × B × n), where k is the wave reduction coefficient of reed vegetation, determined by the stem density and diameter of 3-year-old reeds, with a value of 0.05-0.08 m^-1; B is the width of the herbaceous vegetation belt in meters; and n is the planting density of reeds in clumps per square meter. Combining tidal data from the original hydrodynamic parameter set, key parameters such as mean tidal range, maximum tidal range, mean wave height, and mean wavelength are extracted and substituted into the wave attenuation model to calculate the tidal energy reduction efficiency under different herbaceous vegetation belt widths and planting densities. At the same time, the comprehensive energy reduction efficiency of the herbaceous-woody zonal layout is calculated by combining the auxiliary wave reduction effect of woody vegetation belts.

[0046] The width ratio of herbaceous and woody plant zones was optimized, with a core optimization goal of achieving a comprehensive energy reduction efficiency of ≥80%. Considering the hydrodynamic characteristics and species growth characteristics of the intertidal zone, the width of the herbaceous plant zone was set at 15-25 meters, and the width of the woody plant zone at 4-6 meters. This width ratio ensures wave dissipation while also considering the growth space for species and the rationality of the community structure. For areas with strong scour (Tidal scour intensity index I ≥ 0.8), the width of the herbaceous plant zone was optimized to 20-25 meters, and the width of the woody plant zone to 5-6 meters. For example, in the strong tidal mudflat area on the south bank of Hangzhou Bay, a width ratio of 20 meters for herbaceous plant zone and 5 meters for woody plant zone was adopted, achieving a comprehensive energy reduction efficiency of over 85%. For areas with weak scour (Tidal scour intensity index I < 0.5), the width of the herbaceous plant zone was optimized to 15-20 meters, and the width of the woody plant zone to 4-5 meters, reducing seedling consumption while ensuring wave dissipation.

[0047] The number of alternations in the strip layout is optimized based on the longitudinal length of the target restoration area (the horizontal distance from the mean low tide level to the mean high tide level) and the intensity of tidal scouring. The number of alternations follows the principle of more alternations for strong scouring and fewer alternations for weak scouring. In areas with a longitudinal length greater than 100 meters, multiple alternations are made according to the width ratio of herbaceous to woody plants to form a stepped wave-dissipating structure, allowing tidal energy to be gradually reduced as it passes through multiple herbaceous protective strips. In areas with a longitudinal length less than 100 meters, 1-2 alternations are sufficient to meet the wave-dissipating requirements. During the alternation process, the width of subsequent herbaceous plant strips can be appropriately reduced by 5-10 meters based on the energy reduction effect of the preceding strips, achieving precise optimization of the layout.

[0048] Based on the optimization of width ratio and alternation frequency, a multi-layered planting structure model with stepped wave-dissipating function was finally generated. This model is a three-dimensional structural model integrating spatial layout, functional characteristics, and quantitative parameters. The spatial resolution and geographic coordinate system of the model are consistent with all previous data. The core of the model includes five key elements: First, spatial layout elements, marking the precise location, width, alternation frequency, direction, and elevation range of herbaceous and woody plant zones; second, species configuration elements, specifying the plant species and seedling specifications for each zone; third, wave-dissipating function elements, marking the tidal energy reduction efficiency of each herbaceous plant zone and the overall efficiency of the stepped wave-dissipating system; fourth, environmental matching elements, associating environmental parameters such as tidal erosion intensity, sediment deposition rate, and soil salinity for each zone; and fifth, construction adaptability elements, marking the terrain adaptability characteristics of each zone and key considerations for planting operations. This model realizes the multi-layered spatial configuration of herbaceous and woody plants, and achieves the gradual reduction of tidal energy through a stepped, alternating strip layout, providing a complete structural basis for subsequent vegetation density calculation and seedling demand statistics.

[0049] S204. Based on the multi-layered planting structure model, calculate the planting density, strip width, and number of alternating units for each species to generate an estuarine intertidal vegetation construction scheme that includes spatial configuration and seedling requirements.

[0050] Specifically, the layout parameters of the herbaceous plant protective strip and the woody plant restoration strip can be extracted from the multi-layered planting structure model. Combined with the clump growth characteristics and crown size of the target species, the theoretical number of clumps per unit area can be calculated to generate the basic planting density of herbaceous plants and woody plants. The core of this step is to extract basic layout information from the multi-layered planting structure model, combine it with the biological characteristics of the target species to quantitatively calculate the theoretical number of clumps, and determine the basic planting density that can balance the growth space and functional performance of the species, providing a benchmark for subsequent density optimization. The specific implementation method is as follows: Core layout parameters for herbaceous plant protective zones and woody plant restoration zones were extracted from the multi-layered planting structure model. These parameters included the spatial distribution range, lateral coverage length, longitudinal elevation range, and relative positions between zones. All parameters retained geographic coordinates and dimensional standards consistent with the model to ensure accurate matching between subsequent density calculations and spatial layout. Simultaneously, the biological characteristics of the target species were analyzed, focusing on the clump-forming characteristics and crown size of 3-year-old reeds and 2-year-old tamarisk container seedlings. 3-year-old reeds are typical clump-forming herbs with strong tillering ability in their rhizomes, expanding outwards shortly after planting. The effective crown width of a single mature clump is 0.4-0.5 meters, a core dimension for ensuring dense reed stems and forming an effective wave-dissipating layer. 2-year-old tamarisk container seedlings are single woody plants. Crown growth is slow before the root system is firmly established after planting, with an initial effective crown width of 0.8-1.0 meters. This crown width ensures sufficient photosynthetic space for tamarisk seedlings and avoids nutrient competition caused by overly dense planting.

[0051] The calculation of basic planting density is based on the core principle of matching the row spacing with the crown width, adopting a square row spacing layout. The calculation formula is: theoretical number of clumps per unit area = 1 ÷ (row spacing × row spacing). The row spacing value is slightly larger than the lower limit of the effective crown width of the species, which ensures the initial planting density requirements while reserving space for subsequent growth. For 3-year-old reeds, considering their effective crown width of 0.4-0.5 meters, the row spacing is set at 0.5 meters × 0.5 meters. Substituting into the formula, the theoretical number of clumps per unit area is calculated to be 4 clumps / square meter. This density allows the reeds to quickly form a dense stem layer and root network after planting, playing a role in wave dissipation and soil stabilization. For 2-year-old container seedlings of tamarisk, considering their initial effective crown width of 0.8-1.0 meters, the row spacing is set at 1.0 meter × 1.0 meter. Substituting into the formula, the theoretical number of clumps per unit area is calculated to be 1 clump / square meter. This density avoids nutrient and space competition among tamarisk seedlings, improving the rooting and survival rate. After the calculation is completed, the plant spacing and the theoretical number of clumps per unit area are linked with the corresponding species and planting zone type to generate basic planting density data for herbaceous and woody plants. The data clearly marks the basis for the density calculation and species characteristic parameters to ensure the scientific nature and suitability of the density.

[0052] Based on the calculation results of the tidal scour intensity index and wave attenuation model, the basic planting density is corrected, and the planting of herbaceous plants is increased in areas with strong scour to enhance wave dissipation capacity, thus generating the optimized actual planting density. The core of this step is to differentiate the planting density based on the tidal scouring intensity and wave dissipation requirements of the target area, focusing on increasing the planting density of herbaceous plants in areas with strong scouring, so that the density is precisely matched with the wave dissipation function requirements, generating an actual planting density that can directly guide construction. The specific implementation method is as follows: First, the core basis for density correction is clarified. One is the grading results of the tidal scour intensity index, which divides the index into three levels: strong scour (I≥0.8), moderate scour (0.5≤I<0.8), and weak scour (I<0.5). A higher level indicates stronger regional tidal hydrodynamics and a higher requirement for the density of the reed wave-dissipating layer. The second is the calculation results of the wave attenuation model, which clearly shows a positive correlation between reed planting density and wave energy attenuation efficiency; for every 20% increase in density, wave attenuation efficiency can increase by 10%-15%. Based on this, the density correction range for different scour levels is determined. Correction is only applied to herbaceous reeds on the wave-facing side. Woody tamarisk, due to its placement on the leeward side in a low-energy sedimentary environment with less hydrodynamic disturbance, and because overly dense planting would affect its root development and crown growth, maintains its basic planting density without correction, except in areas with superimposed high salt stress.

[0053] The basic planting density of reeds was adjusted accordingly. In areas with strong scour to improve wave dissipation and soil stabilization, the spacing between plants and rows was increased to 0.4 m × 0.4 m, and the number of clumps per unit area was increased to 6.25 clumps / m², a 56.25% increase compared to the basic density. This resulted in a denser stem layer and root network, effectively resisting the shearing force of strong water flow. In areas with moderate scour, the tidal hydrodynamics were moderate, so the basic planting density (0.5 m × 0.5 m, 4 clumps / m²) was maintained, balancing wave dissipation and growth space for the species. In areas with weak scour, the tidal hydrodynamics were weak, so high-density planting was not necessary. The spacing between plants and rows was appropriately widened to 0.6 m × 0.6 m, and the number of clumps per unit area was adjusted to 2.78 clumps / m², reducing seedling consumption while ensuring normal tillering growth of reeds. If the target area contains areas with salinity stress level 3 and weak erosion, the density of tamarisk will be slightly adjusted, with the spacing between plants and rows widened to 1.2 meters × 1.2 meters, and the number of clumps planted per unit area reduced to 0.69 clumps / square meter. This will provide more space for tamarisk seedlings to absorb nutrients and alleviate the growth stress caused by the high salinity environment.

[0054] After the correction is completed, the actual planting density is spatially bound to the tidal scour intensity zone and salinity stress zone of the target area to generate actual planting density data in raster form. The raster resolution is consistent with the multidimensional environmental feature set. Each raster cell is labeled with the actual plant spacing and number of clumps per unit area for the corresponding species. At the same time, density correction instructions are attached to clarify the basis and purpose of density adjustment in each area, and finally form an actual planting density system that can be directly connected to construction.

[0055] Based on the alternating layout design in the topographic profile data and multi-layered planting structure model, the strip width of each alternating unit is calculated, and the total number of alternating units is determined according to the longitudinal length of the target restoration area, generating complete spatial configuration parameters for the strip layout. The core of this step is to combine the layout design with terrain features and multi-layered planting structure model, quantitatively calculate the strip width and total number of alternating units, and integrate them to form a strip layout configuration system that includes all spatial dimension parameters. This provides a spatial basis for subsequent seedling quantity calculations. The specific implementation method is as follows: The alternating unit is a combination of herbaceous plant protective strips and woody plant restoration strips, serving as the basic building block of the alternating strip layout. The strip width is calculated based on the optimized results of the multi-layered planting structure model, combined with the tidal scour intensity classification and elevation characteristics of the topographic profile data of the target area for precise quantification. The width of the herbaceous reed strip is set according to the scour intensity classification: wide reed strips of 20-25 meters are laid in areas of strong scour to fully reduce tidal energy using a wide and dense reed layer; the width is 18-22 meters in areas of moderate scour, ensuring both wave dissipation and space utilization efficiency; and the width is 15-20 meters in areas of weak scour, sufficient to meet basic wave dissipation requirements. The width of the tamarisk strip is limited by the space for sediment deposition and the growth needs of the species, and is uniformly set at 4-6 meters. If the width of the reed strip is 20 meters or more, the width of the tamarisk strip is matched with 5 meters; if the width of the reed strip is less than 20 meters, the width of the tamarisk strip is matched with 4 meters. This width ratio can ensure that the tamarisk strip is within the wave-damping protection range of the reed strip and has sufficient growth space.

[0056] The total number of alternating units is determined based on the longitudinal length of the target restoration area. Longitudinal length refers to the horizontal distance perpendicular to the coastline, from the mean low tide level to the mean high tide level, extracted and calculated from topographic profile data, in meters. First, the total width of a single alternating unit is calculated, which is the sum of the width of the reed strip and the width of the tamarisk strip. Then, the theoretical number of alternating units is calculated using the formula: Total number of alternating units = Longitudinal length of the target restoration area ÷ Total width of a single alternating unit. The result is rounded to the nearest integer. If the remainder is greater than half the total width of a single alternating unit, one alternating unit is added on the high tide beach side to ensure vegetation cover in the high tide beach area. If the remainder is less than half, the remainder is incorporated into the tamarisk strip of the last alternating unit, and the width of the tamarisk strip is appropriately widened (maximum not exceeding 8 meters) to avoid scattered planting strips.

[0057] After calculating the strip width and the total number of alternating units, the complete spatial configuration parameters for the strip layout are integrated and generated. The parameter system includes core spatial parameters and auxiliary layout parameters. The core parameters include the width of the reed strip, the width of the tamarisk strip, the total width of a single alternating unit, the total number of alternating units, the longitudinal length of the target restoration area, and the lateral coverage shoreline length. The auxiliary layout parameters include the orientation of the planting strip, the elevation range of each strip, the connection distance between strips, and the fine-tuning method of the layout at the high tide / low tide beach ends. All parameters are labeled with dimensions and calculation basis, and are spatially correlated with topographic zoning data and tidal erosion intensity zoning data to ensure that the parameters can accurately guide the on-site planting layout.

[0058] Multiply the actual planting density, strip width, and number of alternating units by the total area of ​​the target restoration area to calculate the total number of 3-year-old reed beds and 2-year-old tamarisk container seedlings required. Then summarize the seedling specifications and quantity requirements to finally generate an estuarine intertidal vegetation construction scheme that includes spatial configuration and seedling requirements.

[0059] The core of this step is to quantitatively calculate the total number of seedlings required for the target restoration area by analyzing spatial and density parameters. This, combined with the target species specifications, forms a complete seedling demand system. Finally, by integrating spatial configuration parameters and seedling demand information, a vegetation construction plan that can directly guide engineering construction is generated. The specific implementation method is as follows: First, the precise number of seedlings is calculated. Based on the spatial configuration parameters of the strip layout, the planting area of ​​a single reed strip and a single tamarisk strip is calculated. The calculation formula is: Planting area of ​​a single strip = Strip width × Horizontal coverage shoreline length. Then, the total planting area is calculated. Total reed strip planting area = Planting area of ​​a single reed strip × Total number of alternating units. Total tamarisk strip planting area = Planting area of ​​a single tamarisk strip × Total number of alternating units. Subsequently, the theoretical total number of seedlings is calculated based on the actual planting density. The calculation formula is: Theoretical total number of seedlings = Total planting area × Actual number of clumps planted per unit area. The theoretical total number of container seedlings for 3-year-old reeds and 2-year-old tamarisks is calculated separately. Considering the losses that will occur during the transportation, digging, and planting of seedlings on site, a loss coefficient is adjusted to ensure planting density and vegetation coverage. Three-year-old reeds are propagated by rhizome tillage, and the loss coefficient is set at 10%. Two-year-old tamarisk seedlings are container seedlings with intact root systems and high survival rates, and the loss coefficient is set at 8%. The actual number of seedlings required after adjustment = the theoretical total number of seedlings × (1 + loss coefficient). The result is rounded to the nearest integer to avoid decimal seedling counts.

[0060] Taking the restoration project of strong tidal flats on the south bank of Hangzhou Bay as an example, if the horizontal coverage shoreline length is 1000 meters, the total number of alternating units is 4, the width of the reed strip is 20 meters and the actual density is 4 clumps / square meter, and the width of the tamarisk strip is 5 meters and the actual density is 1 clump / square meter, the calculated area of ​​a single reed strip is 20 × 1000 = 20000 square meters, the total area of ​​the reed strip is 20000 × 4 = 80000 square meters, the theoretical total number of reeds is 80000 × 4 = 320000 clumps, and the actual required number is 320000 × 1.1 = 352000 clumps; the area of ​​a single tamarisk strip is 5 × 1000 = 5000 square meters, the total area of ​​the tamarisk strip is 5000 × 4 = 20000 square meters, the theoretical total number of tamarisks is 20000 × 1 = 20000 plants, and the actual required number is 20000 × 1.08 = 21600 plants.

[0061] After calculating the number of seedlings, summarize the target specifications for each species. Three-year-old reeds must be of local origin, retaining rhizomes with tillering ability, with a rhizome diameter of 0.5-0.8cm, and retaining 3-5 dormant buds per clump. They should be obtained through rhizome tillering. Two-year-old container seedlings of tamarisk should be controlled at a height of 60-80cm, with a root ball diameter of about 15cm. Before planting, they need to undergo salt tolerance acclimatization for no less than 3 months. The salinity of the acclimatization solution should be matched with the average salinity of the target area and gradually increased to 1.2 times the highest salinity. Finally, all information was integrated to generate an intertidal vegetation construction plan for the estuary. The plan consists of two core modules: the first is the spatial configuration module, which fully presents all spatial parameters of the strip layout, actual planting density, instructions for adjusting the density of different zones, and precautions for layout and construction; the second is the seedling requirement module, which clearly indicates the specifications, theoretical quantity, loss coefficient, actual required quantity, and seedling cultivation and acclimatization requirements for reeds and tamarisks. At the same time, it also includes construction support suggestions, including planting time, planting method, and key points for post-construction maintenance. All data in the plan are quantified and clearly defined, and the layout design is precisely matched with the environmental characteristics of the target area, which can directly guide the on-site construction of intertidal vegetation in the estuary.

[0062] Another embodiment of the present invention provides an estuarine intertidal vegetation construction system based on root-based synergistic soil stabilization, see [link to relevant documentation]. Figure 3 The system may include: The data acquisition module 301 is used to collect hydrodynamic parameters, soil salinity distribution and topographic elevation data of the target area, and generate a multi-dimensional environmental feature set reflecting the intensity of tidal erosion and site conditions. The determination module 302 is used to screen out the target specifications of deep-rooted herbaceous plants and salt-tolerant woody plants with established root networks based on the multidimensional environmental feature set, determine the optimal planting time during the plant's dormancy period, and output a matching scheme for species combination and time window. Design module 303 is used to design, based on the matching scheme and combined with terrain elevation data, a strip-shaped alternating layout with herbaceous plant belts as the wave-facing protection layer and woody plant belts as the wave-recovery layer, to generate a multi-layered planting structure model with stepped wave-dissipating function. The generation module 304 is used to calculate the planting density, strip width and number of alternating units of each species according to the multi-layered planting structure model, and generate an estuarine intertidal vegetation construction scheme that includes spatial configuration and seedling requirements.

[0063] This invention also provides a storage medium storing a computer program, wherein the computer program is configured to execute the steps in any of the above method embodiments when running.

[0064] This invention also provides an electronic device, including a memory and a processor, wherein the memory stores a computer program, and the processor is configured to run the computer program to perform the steps in any of the above method embodiments.

[0065] The above description, based on the embodiments shown in the figures, details the structure, features, and effects of the present invention. The above description is only a preferred embodiment of the present invention, but the present invention is not limited to the scope of implementation shown in the figures. Any changes made in accordance with the concept of the present invention, or equivalent embodiments modified to have equivalent changes, that do not exceed the spirit covered by the specification and figures, should be within the protection scope of the present invention.

Claims

1. A method for constructing intertidal vegetation in estuaries based on root-based synergistic soil stabilization, characterized in that, The method includes: Collect hydrodynamic parameters, soil salinity distribution and topographic elevation data of the target area to generate a multi-dimensional environmental feature set reflecting the intensity of tidal erosion and site conditions. Based on the multidimensional environmental feature set, target specifications for deep-rooted herbaceous plants and salt-tolerant woody plants with established root networks are screened out, and the optimal planting time during the plant's dormancy period is determined, outputting a matching scheme for species combinations and time windows. Based on the matching scheme, and combined with topographic elevation data, a strip-shaped alternating layout is designed with herbaceous plant belts as the wave-facing protection layer and woody plant belts as the wave-recovery layer, generating a multi-layered planting structure model with stepped wave-dissipating function. Based on the multi-layered planting structure model, the planting density, strip width, and number of alternating units for each species are calculated to generate an estuarine intertidal vegetation construction scheme that includes spatial configuration and seedling requirements.

2. The method according to claim 1, characterized in that, The collected hydrodynamic parameters, soil salinity distribution, and topographic elevation data of the target area are used to generate a multi-dimensional environmental feature set reflecting the intensity of tidal erosion and site conditions, including: Hydrological monitoring sections are set up in the target area along the direction perpendicular to the coastline. The flow velocity and direction data and tidal level change data during the tidal cycle are continuously collected by an acoustic Doppler current profiler and a pressure-type tide gauge to generate the original set of hydrodynamic parameters. Soil sampling points were set up at the monitoring section using the grid sampling method. The soil salinity value of each sampling point was measured using a portable salinity meter and conductivity meter. A spatial distribution map of soil salinity was generated by the Kriging interpolation algorithm. A drone-borne lidar was used to perform oblique photogrammetry on the target area to obtain high-precision point cloud data, which was then filtered and classified to generate a digital elevation model. The original hydrodynamic parameter set, soil salinity spatial distribution map and digital elevation model are spatially registered and fused to calculate the tidal erosion intensity index, salinity stress level and topographic slope factor, and finally generate a multidimensional environmental feature set.

3. The method according to claim 2, characterized in that, Based on the multidimensional environmental feature set, the target specifications for deep-rooted herbaceous plants and salt-tolerant woody plants with established root networks are screened out, and the optimal planting time during the plant's dormancy period is determined. A matching scheme between species combinations and time windows is output, including: The tidal scouring intensity index and salinity stress level, which are concentrated in a multidimensional environmental feature set, were analyzed and matched with a pre-built coastal wetland plant germplasm resource bank to screen out a list of candidate species that can tolerate the target environmental stress. Root development characteristics data of deep-rooted herbaceous plants and salt-tolerant woody plants were extracted from the candidate species list. The root network maturity age required for herbaceous plants was determined based on the scour intensity index. Three-year-old reeds were output as the target specifications for deep-rooted herbaceous plants. Based on the assessment of salt tolerance requirements of woody plants according to the salt stress level, and combined with the salt tolerance test data of plants of different ages in the germplasm resource bank, two-year-old container seedlings of Tamarix chinensis that have undergone salt acclimatization treatment were selected as the target specifications for salt-tolerant woody plants. Based on topographic elevation data and historical meteorological data with multidimensional environmental features, the temperature variation pattern and tidal spring tide distribution of the target area are analyzed to determine the dormant period when plant transpiration is weak and the tidal flats are relatively stable. Finally, a matching scheme containing species combinations and optimal planting time is output.

4. The method according to claim 3, characterized in that, The process involves designing a strip-shaped alternating layout, based on the matching scheme and topographic elevation data, with herbaceous plant belts as the wave-facing protection layer and woody plant belts as the wave-recovery layer, to generate a multi-layered planting structure model with stepped wave-dissipating function. This includes: Based on the digital elevation model, the topographic profile lines perpendicular to the coastline of the target area are extracted, the boundary elevations of high tide shoals, mid tide shoals and low tide shoals are identified, and topographic zoning data is generated. Based on the species combination and topographic zoning data in the matching scheme, it is determined that the wave protection layer should be deployed in the mid-to-low tidal flat area where the tidal erosion is most intense, and the preliminary layout range of the herbaceous plant protection belt is output. On the leeward side of the herbaceous plant protection zone, the location of the woody plant restoration zone is determined based on the topographic uplift and wave energy attenuation patterns to ensure that it is in a low-energy deposition environment and outputs a strip structure with alternating herbaceous and woody plant arrangements. By combining tidal level data and wave attenuation models from hydrodynamic parameters, the efficiency of the zonal layout in reducing tidal energy at each level is calculated. The width ratio and alternation frequency of herbaceous plant zones and woody plant zones are optimized, and finally a multi-layered planting structure model with stepped wave dissipation function is generated.

5. The method according to claim 4, characterized in that, The process involves calculating the planting density, strip width, and number of alternating units for each species based on the multi-layered planting structure model, and generating an estuarine intertidal vegetation construction scheme that includes spatial configuration and seedling requirements, including: The layout parameters of the herbaceous plant protective strip and the woody plant restoration strip are extracted from the multi-layered planting structure model. Combined with the clump growth characteristics and crown size of the target species, the theoretical number of clumps per unit area is calculated to generate the basic planting density of herbaceous plants and woody plants. Based on the calculation results of the tidal scour intensity index and wave attenuation model, the basic planting density is corrected, and the planting of herbaceous plants is increased in areas with strong scour to enhance wave dissipation capacity, thus generating the optimized actual planting density. Based on the alternating layout design in the topographic profile data and multi-layered planting structure model, the strip width of each alternating unit is calculated, and the total number of alternating units is determined according to the longitudinal length of the target restoration area, generating complete spatial configuration parameters for the strip layout. Multiply the actual planting density, strip width, and number of alternating units by the total area of ​​the target restoration area to calculate the total number of 3-year-old reed beds and 2-year-old tamarisk container seedlings required. Then summarize the seedling specifications and quantity requirements to finally generate an estuarine intertidal vegetation construction scheme that includes spatial configuration and seedling requirements.

6. A system for constructing intertidal vegetation in estuaries based on root-based synergistic soil stabilization, characterized in that, The system includes: The data acquisition module is used to collect hydrodynamic parameters, soil salinity distribution and topographic elevation data of the target area, and generate a multi-dimensional environmental feature set that reflects the intensity of tidal erosion and site conditions. The determination module is used to screen out the target specifications of deep-rooted herbaceous plants and salt-tolerant woody plants with established root networks based on the multidimensional environmental feature set, determine the optimal planting time during the plant's dormancy period, and output a matching scheme between species combination and time window. The design module is used to design, based on the matching scheme and combined with topographic elevation data, a strip-shaped alternating layout with herbaceous plant belts as the wave-facing protection layer and woody plant belts as the wave-recovery layer, to generate a multi-layered planting structure model with stepped wave-dissipating function. The generation module is used to calculate the planting density, strip width and number of alternating units of each species based on the multi-layered planting structure model, and generate an estuarine intertidal vegetation construction scheme that includes spatial configuration and seedling requirements.

7. The system according to claim 6, characterized in that, The acquisition module is specifically used for: Hydrological monitoring sections are set up in the target area along the direction perpendicular to the coastline. The flow velocity and direction data and tidal level change data during the tidal cycle are continuously collected by an acoustic Doppler current profiler and a pressure-type tide gauge to generate the original set of hydrodynamic parameters. Soil sampling points were set up at the monitoring section using the grid sampling method. The soil salinity value of each sampling point was measured using a portable salinity meter and conductivity meter. A spatial distribution map of soil salinity was generated by the Kriging interpolation algorithm. A drone-borne lidar was used to perform oblique photogrammetry on the target area to obtain high-precision point cloud data, which was then filtered and classified to generate a digital elevation model. The original hydrodynamic parameter set, soil salinity spatial distribution map and digital elevation model are spatially registered and fused to calculate the tidal erosion intensity index, salinity stress level and topographic slope factor, and finally generate a multidimensional environmental feature set.

8. The system according to claim 7, characterized in that, The determining module is specifically used for: The tidal scouring intensity index and salinity stress level, which are concentrated in a multidimensional environmental feature set, were analyzed and matched with a pre-built coastal wetland plant germplasm resource bank to screen out a list of candidate species that can tolerate the target environmental stress. Root development characteristics data of deep-rooted herbaceous plants and salt-tolerant woody plants were extracted from the candidate species list. The root network maturity age required for herbaceous plants was determined based on the scour intensity index. Three-year-old reeds were output as the target specifications for deep-rooted herbaceous plants. Based on the assessment of salt tolerance requirements of woody plants according to the salt stress level, and combined with the salt tolerance test data of plants of different ages in the germplasm resource bank, two-year-old container seedlings of Tamarix chinensis that have undergone salt acclimatization treatment were selected as the target specifications for salt-tolerant woody plants. Based on topographic elevation data and historical meteorological data with multidimensional environmental features, the temperature variation pattern and tidal spring tide distribution of the target area are analyzed to determine the dormant period when plant transpiration is weak and the tidal flats are relatively stable. Finally, a matching scheme containing species combinations and optimal planting time is output.

9. A storage medium, characterized in that, The storage medium stores a computer program, wherein the computer program is configured to execute the method of any one of claims 1-5 when it is run.

10. An electronic device comprising a memory and a processor, characterized in that, The memory stores a computer program, and the processor is configured to run the computer program to perform the method of any one of claims 1-5.

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