The aim of this study was to examine the abilities of the mesoscale ecohydrological model Soil And Water Integrated Model (SWIM) to simulate discharge, soil moisture, and groundwater dynamics in a small-scale forested catchment. Moreover, the influence of two lateral flow computation techniques on the simulation efficiency was assessed. Generally, the discharges were simulated poorly. Groundwater level was estimated reasonably taking into account that the model was not designed for small-scale catchments. The soil moisture simulation exhibited good correspondence with the observed data in the warmer season (April–August). Both the dynamics and the magnitude were estimated sufficiently well. On the other hand, the colder season does not comply satisfactorily with the modelled data, as the decline of moisture content (in the non-precipitation periods) has no model response. The kinematic storage method was found to be more reliable in the case of a small-scale forested catchment compared to the exponential storage lateral flow estimation approach.
INTRODUCTION
Soil moisture plays a key role in the hydrological cycle and also in the entire ecosystem. It controls the flux of water between soil, vegetation, and atmosphere. As the water cycle is subjected to various stresses, there is a need for an estimation of the impacts of these stresses on the soil moisture regime. The reason is that the volume of water stored within the soil has a direct effect on vegetation growth, crop yield, and, in particular, the volume and timing of runoff. Several studies have indicated the important consequences of soil moisture deficit within catchments (Entin et al. 2000; Daly & Porporato 2005). Hence, understanding of soil moisture variability is important for the modelling of the climate system and improves hydrological simulation. It also provides the background for hydrological forecasting systems as antecedent moisture conditions and their patterns represent crucial parameters.
Recently, mesoscale hydrological models have been widely applied for estimating not only the discharge, but also the nutrient dynamics and the complex influence of climate change on various catchments (Ficklin et al. 2009; Huang et al. 2009). These models are considered to be appropriate for simulations of the hydrological cycle in mesoscale (ranging from 100 to 10,000 km2) and macroscale (>10,000 km2) areas. However, the application of these types of models at larger scale is based on the assumption that they are able to predict the particular components of the hydrological cycle in a reasonable way. This assumption can be efficiently validated only at the small scale as the required data are usually not available for larger areas. The hydrological models Soil and Water Assessment Tool (SWAT) and Soil and Water Integrated Model (SWIM) represent the aforementioned type of models and have very similar components concerning the modelling of the hydrological cycle (Krysanova et al. 2005). The mesoscale ecohydrological model SWIM was chosen in this study as a tool for hydrological modelling.
SWIM has already been used for a number of studies investigating the impact of climate or land-use changes on the hydrological cycle (Holsten et al. 2009; Nemeckova et al. 2011), nutrient dynamics (Hesse et al. 2008; Huang et al. 2009), and crop yield (Krysanova et al. 2005). The performance of the SWAT/SWIM type of model with regard to discharge at the macroscale was verified by several authors (e.g. Srinivasan et al. 1998; Hattermann et al. 2005; Koch et al. 2013). However, the SWAT/SWIM type of model was originally designed for rural areas (Arnold et al. 1993). Nevertheless, using this type of model for meso- and macroscale tasks (where detailed measurements are not available) means that certain parts of the landscape are usually covered by forest. Hence, the assessment of the model's performance in a small-scale forested catchment is a valuable source of information for modellers using this type of model in areas with diverse land cover.
A number of the existing models such as Système Hydrologique Européen Model (e.g. Abbott et al. 1986), TOPMODEL (Beven & Kirkby 1979), SWAT (Arnold et al. 1993), and SWIM (Krysanova et al. 1998, 2005), which operate at the larger scale, use different methods for the soil moisture estimation. In spite of numerous applications of models of the SWAT/SWIM type, only a few contributions have dealt explicitly with soil moisture (DeLiberty & Legates 2003; Holsten et al. 2009; Li et al. 2010). These studies are primarily focussed on average monthly soil moisture values or trend analysis in modelled datasets. Thus, a reliable evaluation of this model component concerning the daily soil moisture records in both the vegetation season and the dormant season is missing. This is especially important when the SWAT/SWIM type of model is used for large-scale analysis of climate or land-use change in various components of the hydrological cycle (Ficklin et al. 2009; Huang et al. 2010) or, for example, to validate a satellite-based estimation of actual evapotranspiration (Fang et al. 2012).
The primary motivation for this experiment originates in the need to establish a modelling scheme that would enable reliable year-round soil moisture content estimation in mesoscale catchments with diverse land cover. This might be further used for the improvement of impact studies (climate and land-use change, agricultural management) on the hydrological regime and also for more accurate determination of the moisture saturation level of various regions, which is necessary for hydrological forecasting systems.
Thus, the main aims of this study are:
to assess the ability of the mesoscale SWIM model to simulate the rainfall–runoff relation in a small-scale forested catchment (0.99 km2);
to investigate the reliability of soil water content and groundwater level simulations;
to assess the influence of two different approaches of lateral subsurface flow estimation (kinematic and exponential storage) on discharge, soil moisture, and groundwater level simulations.
METHODS USED AND DATA PROCESSING
Study area and data
Study site location and overview map of the Liz catchment with forest age shown.
Study site location and overview map of the Liz catchment with forest age shown.
The meteorological data necessary to run the model were obtained from the meteorological station located next to the experimental catchment (330 m from its border and 1,000 m from the centre of the catchment) at the altitude of 830 m.a.s.l. It is located on the meadow and thus records open rainfall without the influence of interception losses. Hence, the station is considered to be representative. The datasets consist of precipitation, air temperature, air relative humidity, and solar radiation records from the period of 2007–2010. The water level is measured by the ultrasonic probe in the catchment's closing profile and the long-term average is equal to 0.011 m3s–1 (1975–2010).
The suction pressure of soil water was measured by a set of tensiometers (UMS T8) at three depths (15, 40, and 60 cm). As these data were available from July 2008, the study deals with 2 subsequent years (2009–2010), in which only 2 days of measurements are missing. The precise location of the soil moisture measurement was chosen in order to represent the average age of the forest, the average hillslope angle, and approximately average altitude within the catchment. The soil moisture content was derived from suction pressure using a retention curve proposed by Van Genuchten (1980). The exact parameters of the retention curves are displayed in Table 1.
Parameters of van Genuchten expression of retention curves for three depths
. | Depth . | ||
---|---|---|---|
. | 15 cm . | 40 cm . | 60 cm . |
ϴr [%] | 0.00 | 0.17 | 0.16 |
ϴs [%] | 0.73 | 0.53 | 0.50 |
α [–] | 0.09 | 0.05 | 0.06 |
n [–] | 1.19 | 1.60 | 1.47 |
. | Depth . | ||
---|---|---|---|
. | 15 cm . | 40 cm . | 60 cm . |
ϴr [%] | 0.00 | 0.17 | 0.16 |
ϴs [%] | 0.73 | 0.53 | 0.50 |
α [–] | 0.09 | 0.05 | 0.06 |
n [–] | 1.19 | 1.60 | 1.47 |
θr and θs – residual and saturated volumetric water contents, respectively; α and n – shape parameters of the retention curve.
The groundwater level has been measured manually once a week by the acoustic device in a borehole since 1976. For the purpose of groundwater level monitoring, a network of four boreholes was created. For this study, the borehole near the closing profile of the Liz experimental catchment was chosen. This borehole has an inner diameter of 150 mm and depth of 12 m, and the groundwater level of the unconfined aquifer ranges from 1.7 to 8.2 m from the ground surface.
Four layers of spatial data are necessary for the hydrological model: a subbasin map, a digital elevation model, a soil map, land cover characteristics, and optionally a map of the river network. The subbasin map was derived by the model's MapWindow interface from the digital elevation model (Czech Geodesy Agency). Land cover data were extracted from the CORINE land cover database, and the soil map (Nemeckova 2008) was created based on the experimental datasets from the Czech University of Life Sciences.
Ecohydrological model SWIM
The ecohydrological model SWIM is a continuous-time semi-distributed model which integrates hydrological processes, vegetation and crop growth, erosion, and nutrient dynamics at the catchment scale. It is based on two previously developed tools: SWAT (Arnold et al. 1993) and MATSALU (Krysanova et al. 1989). SWIM was used in this study as it fulfils the requirements of data availability and distributed character. Moreover, it enables the estimation of the soil moisture content in several soil layers and has its own geographic information system (GIS) interface.
SWIM is spatially disaggregated into a three-level scheme: basin, subbasin and hydrotope. The hydrotope is a spatial unit of unique geographical properties and therefore it may be assumed to be a unit of uniform hydrological response and nutrient cycle behaviour. Hydrotopes are derived by means of the GIS tools by overlaying three input layers: the map of land use, the soil map, and the map of subbasins.
This physically based model includes calculations of the individual hydrological processes following specific techniques: the water percolation–storage routing technique based on the Simulator for Water Resources in Rural Basins (SWRRB) (Arnold et. al. 1990), the direct runoff–Soil Conservation Service–Curve Number (SCS CN) technique, subsurface lateral flow (details are given in the following paragraph), groundwater recharge (Sangrey et al. 1984), evapotranspiration (Priestley & Taylor 1972; Ritchie 1972), vegetation cycle (Williams et al. 1984), snowmelt–degree day method (Knisel 1980), and river routing (Muskingum routing). All processes are calculated for each hydrotope in a daily step and then aggregated for the particular subbasin. A detailed description of the model can be found in Krysanova et al. (1998, 2005). SWIM proved to be a suitable tool for the simulations of the hydrological cycle in Central Europe (Hattermann et al. 2005; Nemeckova et al. 2011). The total runoff from the area is calculated as the sum of three components: direct runoff (in terms of SCS CN), subsurface lateral flow, and groundwater runoff.

The daily sum of precipitation, air temperatures (minimum, maximum, and average), relative humidity, and solar radiation represent the inputs into SWIM. The wind speed is optional.
RESULTS
Discharge calibration and validation
The original version of SWIM has 17 calibration parameters. The sensitivity analysis and description of most of these parameters may be found in Hattermann et al. (2005). The automatic parameter estimation algorithm (PEST) was chosen as a calibration tool. A detailed description of the PEST algorithm can be found in Doherty (2004). The advantage of this method consists in the automaticity of the calibration process, especially when SWIM requires a number of parameters to be calibrated. The objective function is represented by a sum of squared weighted residuals. The model calibration was conducted separately for two lateral flow calculation techniques (kinematic storage and SWRRB) using the daily time step. Hence, two model set-ups (one using SWRRB and the second using the kinematic storage lateral flow estimation technique) were compared. The calibration period consisted of a 2-year period (2007–2008) and the validation period was represented by the following 2 years (2009–2010). The validation period was extracted from a continuous simulation (starting in 2007) using the entire calibration period to set-up initial hydrologic conditions. In the validation period, the soil moisture content as well as groundwater level measurements were available.
The values of selected model parameters concerning both lateral flow modelling techniques
Parameter . | Units . | Kinematic storage . | SWRRB . |
---|---|---|---|
Evapotranspiration correction on sky emissivity | [–] | 0.99 | 0.98 |
Base flow factor – return flow travel time | [–] | 0.95 | 0.97 |
Groundwater recession | [–] | 0.50 | 0.83 |
Groundwater delay | [day] | 185.00 | 99.44 |
Temperature of snowfall | [°C] | 0.50 | 0.50 |
Temperature of snowmelt | [°C] | 0.00 | 0.00 |
Snowmelt rate | [mm day–1] | 0.26 | 0.26 |
Correction of saturated hydraulic conductivity | [–] | 0.50 | 0.46 |
Correction of winter precipitation amount | [–] | 1.15 | 1.06 |
Parameter . | Units . | Kinematic storage . | SWRRB . |
---|---|---|---|
Evapotranspiration correction on sky emissivity | [–] | 0.99 | 0.98 |
Base flow factor – return flow travel time | [–] | 0.95 | 0.97 |
Groundwater recession | [–] | 0.50 | 0.83 |
Groundwater delay | [day] | 185.00 | 99.44 |
Temperature of snowfall | [°C] | 0.50 | 0.50 |
Temperature of snowmelt | [°C] | 0.00 | 0.00 |
Snowmelt rate | [mm day–1] | 0.26 | 0.26 |
Correction of saturated hydraulic conductivity | [–] | 0.50 | 0.46 |
Correction of winter precipitation amount | [–] | 1.15 | 1.06 |
The error statistics of the model performance concerning discharge simulation for the entire calibration (2007–2008) and validation (2009–2010) periods
. | Kinematic storage . | SWRRB . | ||
---|---|---|---|---|
. | Calibration . | Validation . | Calibration . | Validation . |
NS [–] | 0.44 | 0.21 | 0.33 | 0.22 |
RMSE [m3s−1] | 0.007 | 0.013 | 0.008 | 0.013 |
RE [%] | 65 | 122 | 71 | 116 |
R [–] | 0.64 | 0.46 | 0.61 | 0.49 |
B [%] | –8.1 | –7.9 | –20.9 | –19.5 |
. | Kinematic storage . | SWRRB . | ||
---|---|---|---|---|
. | Calibration . | Validation . | Calibration . | Validation . |
NS [–] | 0.44 | 0.21 | 0.33 | 0.22 |
RMSE [m3s−1] | 0.007 | 0.013 | 0.008 | 0.013 |
RE [%] | 65 | 122 | 71 | 116 |
R [–] | 0.64 | 0.46 | 0.61 | 0.49 |
B [%] | –8.1 | –7.9 | –20.9 | –19.5 |
NS – Nash–Sutcliffe index; RMSE – root mean square error: the average square difference between observed and modelled discharge; RE – relative error: root mean square error divided by the observed average discharge; R – correlation coefficient; B – difference between the average observed and modelled discharges.
The average yearly values of runoff components [mm] in the validation period (2009–2010)
Lateral flow approach . | Precipitation . | Direct runoff . | Lateral flow . | Groundwater flow . | Actual evapotranspiration . |
---|---|---|---|---|---|
SWRRB | 916 | 0 | 12 | 363 | 484 |
Kinematic storage | 916 | 3 | 92 | 343 | 482 |
Lateral flow approach . | Precipitation . | Direct runoff . | Lateral flow . | Groundwater flow . | Actual evapotranspiration . |
---|---|---|---|---|---|
SWRRB | 916 | 0 | 12 | 363 | 484 |
Kinematic storage | 916 | 3 | 92 | 343 | 482 |
Discharge simulation in the years 2007–2010 using the kinematic storage method and the SWRRB technique for the Liz gauging station.
Discharge simulation in the years 2007–2010 using the kinematic storage method and the SWRRB technique for the Liz gauging station.
Simulated yearly values of actual evapotranspiration ranged from 450 to 600 mm with annual averages of 500 and 525 mm, depending on the model set-up. These values correspond to the acceptable range (Greminger 1984) and are only slightly higher than those observed by Tuzinsky (2002).
The error statistics demonstrated the fact that SWIM is not a suitable tool to simulate discharge in such a small-scale area. Although it is able to simulate the response of the catchment to rainfall, the recession curves are estimated inadequately. The main discrepancies between observed and simulated discharges might be explained by an inaccurate estimation of the snowmelt process. Nevertheless, the kinematic storage lateral flow estimation approach represents a more efficient opportunity to simulate discharge in the small-scale forested catchment compared to the SWRRB approach (particularly with regard to the long-term water balance and high-flow episodes).
Soil moisture simulations
Simulated and observed soil moisture content at depths of (a) 15, (b) 40, and (c) 60 cm (2009–2010).
Simulated and observed soil moisture content at depths of (a) 15, (b) 40, and (c) 60 cm (2009–2010).
Based on the observed character of soil moisture dynamics the year was split into warm and cold periods. The warm period was defined as 1 April to 31 August, and therefore nearly coincides with the vegetation period (from 1 May to 7 October) defined by Tesar et al. (2001). The colder period spans from the beginning of September to the end of March.
According to Figure 3(a), the simulated water content at the depth of 15 cm was significantly underestimated by the model and the mean value would always be a better estimate (Table 5). This is caused either by the influence of hysteresis or by the extremely variable porosity present in the top soil layer. Hence, in this top layer it is better to assess only the dynamics of the water content. However, it did not comply satisfactorily with the modelled values on the yearly basis. Only in the case of summer and autumn periods were there several similarities (Figure 3(a)). The detailed statistics in Table 6 show that both modelling approaches had very similar results in terms of root mean square error (RMSE), correlation coefficient, and soil water balance.
The Nash–Sutcliffe coefficients concerning soil moisture simulations in the various soil layers and for the entire soil profile (total soil moisture content (SMC)) in the validation period 2009–2010
Period . | Lateral flow . | 15 cm . | 40 cm . | 60 cm . | Total SMC . |
---|---|---|---|---|---|
Cold 2009 | Kinematic storage | –0.79 | –1.82 | –2.92 | –0.80 |
SWRRRB | –0.82 | –1.04 | –1.68 | –0.64 | |
Warm 2009 | Kinematic storage | –4.56 | 0.44 | 0.33 | 0.62 |
SWRRRB | –5.33 | 0.15 | 0.15 | 0.35 | |
Cold 2010 | Kinematic storage | –2.51 | –0.72 | –0.40 | –0.36 |
SWRRRB | –2.62 | –0.31 | 0.16 | –0.04 | |
Warm 2010 | Kinematic storage | –5.13 | –0.04 | 0.07 | 0.37 |
SWRRRB | –5.75 | –0.70 | –0.45 | –0.05 |
Period . | Lateral flow . | 15 cm . | 40 cm . | 60 cm . | Total SMC . |
---|---|---|---|---|---|
Cold 2009 | Kinematic storage | –0.79 | –1.82 | –2.92 | –0.80 |
SWRRRB | –0.82 | –1.04 | –1.68 | –0.64 | |
Warm 2009 | Kinematic storage | –4.56 | 0.44 | 0.33 | 0.62 |
SWRRRB | –5.33 | 0.15 | 0.15 | 0.35 | |
Cold 2010 | Kinematic storage | –2.51 | –0.72 | –0.40 | –0.36 |
SWRRRB | –2.62 | –0.31 | 0.16 | –0.04 | |
Warm 2010 | Kinematic storage | –5.13 | –0.04 | 0.07 | 0.37 |
SWRRRB | –5.75 | –0.70 | –0.45 | –0.05 |
The performance of soil moisture simulations in the various soil layers in the validation period 2009–2010 (notation defined in the caption of Table 2)
Depth . | Lateral flow . | RMSE [cm3cm–3] . | R [–] . | Balance [%] . |
---|---|---|---|---|
15 cm | Kinematic storage | 0.136 | 0.25 | –24.7 |
SWRRB | 0.141 | 0.27 | –25.9 | |
40 cm | Kinematic storage | 0.046 | 0.27 | 8.2 |
SWRRB | 0.042 | 0.19 | 4.4 | |
60 cm | Kinematic storage | 0.040 | 0.35 | 7.2 |
SWRRB | 0.035 | 0.32 | 4.2 | |
Total SMC | Kinematic storage | 0.034 | 0.51 | 4.5 |
SWRRB | 0.033 | 0.42 | 2.1 |
Depth . | Lateral flow . | RMSE [cm3cm–3] . | R [–] . | Balance [%] . |
---|---|---|---|---|
15 cm | Kinematic storage | 0.136 | 0.25 | –24.7 |
SWRRB | 0.141 | 0.27 | –25.9 | |
40 cm | Kinematic storage | 0.046 | 0.27 | 8.2 |
SWRRB | 0.042 | 0.19 | 4.4 | |
60 cm | Kinematic storage | 0.040 | 0.35 | 7.2 |
SWRRB | 0.035 | 0.32 | 4.2 | |
Total SMC | Kinematic storage | 0.034 | 0.51 | 4.5 |
SWRRB | 0.033 | 0.42 | 2.1 |
SMC – soil moisture content.
For the depth of 40 cm, the model performance was slightly more reliable than in the case of 15 cm, as documented, for example, by the total predicted soil water volume (Table 6) or Nash–Sutcliffe coefficient (Table 5). According to Figure 3(b), the model simulation was again more satisfactory in the warmer period of the year. The most obvious discrepancies were connected with winter soil moisture declines that were not estimated at all. Hence, in the winter period the use of the mean value would be more efficient (Table 5). The SWRRB lateral flow model set-up estimated the soil moisture balance better and the kinematic storage approach gave higher correlations and a more efficient NS index (in the warm season).
The model performance in the last layer measured by the tensiometer (60 cm) is shown in Figure 3(c). It exhibited behaviour similar to that in the above layer. Even the amplitude of the soil water content curve was close to that of the adjacent layer, implying that the soil within these two depths acts as one homogenous unit, at least from a soil moisture point of view. The only difference from the previous soil layer is represented by the correlation coefficient between the observed and simulated data (Table 6), which is similar using both methods studied (SWRRB and kinematic storage).
Comparison of the simulated and observed monthly average soil moisture contents in the Liz catchment (2009–2010).
Comparison of the simulated and observed monthly average soil moisture contents in the Liz catchment (2009–2010).
The seasonal error statistics of the total (entire soil column SMC) soil moisture simulations (notation defined in the caption of Table 2)
Period . | Lateral flow . | RMSE [cm3cm−3] . | R [–] . | Balance [%] . |
---|---|---|---|---|
Cold 2009 | Kinematic storage | 0.042 | 0.52 | 7.8 |
SWRRB | 0.041 | 0.48 | 7.2 | |
Warm 2009 | Kinematic storage | 0.020 | 0.83 | 0.4 |
SWRRB | 0.026 | 0.77 | –3.4 | |
Cold 2010 | Kinematic storage | 0.041 | 0.53 | 9.5 |
SWRRB | 0.035 | 0.54 | 7.0 | |
Warm 2010 | Kinematic storage | 0.019 | 0.68 | –1.9 |
SWRRB | 0.025 | 0.63 | –4.9 |
Period . | Lateral flow . | RMSE [cm3cm−3] . | R [–] . | Balance [%] . |
---|---|---|---|---|
Cold 2009 | Kinematic storage | 0.042 | 0.52 | 7.8 |
SWRRB | 0.041 | 0.48 | 7.2 | |
Warm 2009 | Kinematic storage | 0.020 | 0.83 | 0.4 |
SWRRB | 0.026 | 0.77 | –3.4 | |
Cold 2010 | Kinematic storage | 0.041 | 0.53 | 9.5 |
SWRRB | 0.035 | 0.54 | 7.0 | |
Warm 2010 | Kinematic storage | 0.019 | 0.68 | –1.9 |
SWRRB | 0.025 | 0.63 | –4.9 |
Model performance of the total soil moisture content simulation in the cold season (1 September–31 March).
Model performance of the total soil moisture content simulation in the cold season (1 September–31 March).
Comparison of the simulated and observed daily soil moisture in the Liz catchment in the cold season (upper panel) and warm season (lower panel). Kinematic approach – dark circles; SWRRB – white circles.
Comparison of the simulated and observed daily soil moisture in the Liz catchment in the cold season (upper panel) and warm season (lower panel). Kinematic approach – dark circles; SWRRB – white circles.
Model performance for the total soil moisture content in the warm season (1 April–31 August).
Model performance for the total soil moisture content in the warm season (1 April–31 August).
Groundwater level simulations
The observed and simulated groundwater level in the years 2007–2010.
Groundwater level simulations documented the ability of the hydrological model to capture its fundamental fluctuations in the small-scale catchment. Based on the error statistics (with the exception of the correlation coefficient) and the recession curve shape, the kinematic storage model set-up represented the more reliable option.
DISCUSSION
The ecohydrological model SWIM, which has generally very similar hydrological components to the well-established SWAT model, proved to have limited or no ability to simulate the discharge in the small-scale Liz experimental catchment. The results of discharge simulations are worse than those acquired from the SWAT model simulations in small agricultural catchments by Srinivasan et al. (2005) and Kannan et al. (2007), but they outperform the simulations by Spruill et al. (2000); however, in this work a karst-influenced catchment has been studied. The poor model performance concerning discharge simulations is caused by a combined effect of several issues. First, the winter inconsistency between observed and simulated discharges is determined by a complex character of the snowmelt process. The most pronounced difference is in April 2009 when snow has not started to melt until the temperature of 5 °C was exceeded (the snowmelt threshold is usually slightly above 0 °C). Hence, the simple degree day method (used in this version of SWIM) is not always able to capture the dynamics of snowmelt in forest. Variable parameters of the degree day method or different snowmelt method would be beneficial. Second, a possible source of uncertainty for forested plots is represented by the rate of interception. SWIM allows it to be varied according to the leaf area index to a maximum value of 2.5 mm, which is less than the observed 4.8 mm (Dohnal et al. 2014). Only if the SCS CN curves technique is activated will the interception exceed this threshold. Moreover, coniferous forest might intercept even more precipitation in the form of snow in the winter period (Sipek & Tesar 2014) and therefore modify the runoff response to precipitation. On the contrary, the influence of deposited precipitation (originating from fog), which might add approximately 7% to the total annual vertical precipitation in this region (Elias & Tesar 1994), was neglected. These first two points stress the uncertainty concerning the precipitation inputs in the forested plot. Finally, the rainfall–runoff relation in the area might be more complicated than described by the model design. For example, the introduction of macropore flow (as a fourth source runoff) might help to better estimate the reaction of the forested area to rainfall. The need for another source of runoff is indicated by shapes of simulated recession curves (see Figure 2), which do not always follow observed discharges (especially following high-flow periods).
The soil moisture simulations exhibited contrasting results. The yearly course of simulation was therefore divided into two distinct periods according to the model efficiency. First, in the warmer part of the year (April–August), the dynamics of the total soil moisture content are simulated quite accurately. The minimum and maximum values are predicted well and only peak values of the moisture content are slightly underestimated, which might be caused by the daily time step of the model. The results from this period are comparable to those obtained by Li et al. (2010) using the SWAT model in China or DeLiberty & Legates (2003), who used the SWAT model for soil moisture simulations in Oklahoma, USA. The results for the summer are only slightly worse than the soil moisture simulations performed by another type of model dealing explicitly with soil moisture accounting (Brocca et al. 2008; Chen et al. 2014). Secondly, in the colder part of the year the dynamics of soil moisture seem to be represented inadequately by the model. Although the main process of soil moisture content refilling is observed. These declines might be explained by winter transpiration (Moore et al. 2011) or by percolation to deeper layers. The depth distribution of the moisture content is simulated poorly in the entire year. Moreover, the function of the field capacity concept recorded in this particular layer is problematic, as the water is drained just after moisture reaches the threshold value. Hence, no significantly higher values of simulated soil moisture content are observed.
The groundwater level estimation using the kinematic storage lateral flow approach confirms that the groundwater module in SWIM is able to reproduce the observed water table dynamics in the small-scale forested catchment satisfactorily enough to serve as the lower boundary condition for plant water uptake. The results from the SWRRB approach are less satisfactory as the fluctuations of the groundwater level are significantly higher than the observed ones. This is caused by the model calibration with respect to discharge and the nature of both lateral flow estimation approaches. As no direct runoff is observed, total runoff is generated only by subsurface lateral flow and groundwater runoff. As the SWRRB approach generates only a small portion of subsurface lateral flow compared to the kinematic storage approach (Table 3), the groundwater is the key runoff component and therefore its fluctuation has to correspond closely to observed discharge. However, the runoff from the area partially originates from the soil profile (Cislerova 2005), and the observed groundwater fluctuations are less pronounced (Figure 8). The kinematic storage approach is therefore more suitable for hydrological modelling in mountainous areas with highly permeable soils, where a significant contribution of subsurface lateral flow might be expected.
CONCLUSIONS
The aim of this study was to examine the ability of the mesoscale ecohydrological model SWIM to simulate the rainfall–runoff relationship within a small-scale forested mountainous catchment. In addition, a comparison of two different approaches of lateral flow estimation was performed.
SWIM has a limited ability to estimate the discharge in a small-scale forested catchment. This is probably caused by a larger uncertainty concerning precipitation inputs (interception and snowmelt process) compared to rural areas, variable soil hydraulic characteristics, and also by the character of the rainfall–runoff relation (significance of subsurface lateral flow). Estimates of the total soil moisture content in the forested area simulated by this type of hydrologic model are reliable only in the warm part of the year. The values of the soil moisture content should be dealt with carefully in the winter season as there are certain periods when they are significantly overestimated. The depth distribution of the soil moisture in particular soil layers is also not described well by the model. The observed uncertainty of the soil moisture simulation in the winter period and its year-round depth distribution represent main outcomes of the presented study. The fluctuations of the groundwater level were estimated sufficiently well.
The kinematic storage subsurface lateral flow estimation proved to be superior to the SWRRB approach, especially because of its ability to generate more subsurface lateral flow (which is a significant runoff component in forested mountainous catchments). This is even more important when soil is highly permeable and the SCS curve number (which is an inherent part of the model) does not allow direct runoff to be generated.
The results are especially valuable for modellers who wish to thoroughly describe the year-round hydrological cycle in landscapes with diverse land cover. This also includes the studies concerning the impact of climate and land-use changes on water resources. Further research will be focussed on the rate of evapotranspiration in the winter period as well as on the mechanism responsible for the soil water percolation. Furthermore, the possible introduction of new correction factors for the soil parameters will be a topic of interest. This is crucial, because even measured values of hydrologic soil parameters might encounter errors, which may significantly influence the behaviour of the soil water content calculation.
ACKNOWLEDGEMENT
The research was supported by the Technology Agency of the Czech Republic (TA02021451).