Mapping of water-related ecosystem services in the uMngeni catchment using a daily time-step hydrological model for prioritisation of ecological infrastructure investment – Part 1: Context and modelling approach

South Africa is a semi-arid country which frequently faces water shortages, and experienced a severe drought in the 2016 and 2017 rainfall seasons. Government is under pressure to continue to deliver clean water to the growing population at a high assurance of supply. Studies now show that the delivery of water may be sustained not only through built infrastructure such as dams and pipelines, but also through investment in ecological infrastructure (EI). A daily time-step hydrological model was used to map areas which should be prioritised for protection or rehabilitation to sustain the delivery of water-related ecosystem services within the uMngeni catchment. We focused on three water-related ecosystem services, i.e.: water supply, sustained baseflow, erosion control/avoidance of excessive sediment losses. The two key types of degradation were modelled, namely, overgrazing and the invasion of upland areas by Black Wattle (Acacia mearnsii). This, Part 1 of a paper in 2 parts, provides a discussion on the role of EI in delivering water-related ecosystem services, describes the motivation for the study, and the methods used in modelling and mapping the catchment. The results of this modelling exercise are presented in Part 2, which also explores and illustrates the potential hydrological benefits of rehabilitation and protection of EI in the uMngeni Catchment.


INTRODUCTION
South Africa, as a semi-arid country, frequently faces water shortages and in the 2016 and 2017 rainfall seasons experienced a severe drought. Government is under pressure to continue to deliver clean water to the growing population at a high assurance of supply. Several studies have suggested that the delivery of water may be sustained not only through built infrastructure such as dams and pipelines, but also through investment in ecological infrastructure.
Ecological infrastructure (EI) is de ned as 'naturally functioning ecosystems that produce and deliver valuable services to people'. is term is similar to the widely used 'natural capital', which is de ned as 'the world's stocks of natural assets which include geology, soil, air, water and all living things (Natural Capital Forum, 2017) ' (Jewitt et al., 2015a p. 1). Delivery of water-related ecosystem services is highly dependent on healthy EI (Brauman et al., 2007), which plays a key role in determining the catchment's capacity to rstly receive precipitation, and in turn the distribution of water through varying soil/water responses. e condition of the catchment (e.g. pristine vs overgrazed) therefore determines the partitioning of rainfall above and below the earth's surface, as well as the distribution of water within a catchment. Healthy vegetation cover protects, and its root system binds, the topsoil, reducing its exposure and mobilisation by wind, rainfall and surface runo . e role of EI in delivering water-related ecosystem services is well recognised (Brauman et al., 2007;Guswa et al., 2014;Elmqvist et al., 2015). ese services include, amongst others, ood attenuation, water puri cation through biophysical and biological processes, i.e., retention of sediments and nutrients, pollution dilution, sustaining base ows during dry periods and provision of water supply of high quality (Elmqvist et al., 2007;Guswa et al., 2014), see Fig. 1).
Degradation of EI through various human-induced processes such as overgrazing, inappropriate burning regimes, poor agricultural practices (livestock and cropping) and the proliferation of invasive alien plants (IAPs, see de nitions of 'invasive ' and 'alien' in Richardson et al., 2000) reduces its capability to deliver water-related ecosystem services of the highest quality. In this study, we have concentrated on the outputs from the modelling of two key anthropogenic drivers of degradation, namely, overgrazing and the proliferation of IAPs.
Degradation can have a marked e ect on catchment hydrology (Fig. 2), such as reducing stream ows (water supply), causing high-energy runo which mobilises excessive amounts of sediments, and reducing in ltration of precipitation to the lower layers of soil with associated lower volumes of base ow and groundwater recharge. ese e ects lead to negative impacts on water-related ecosystem services, such as reducing ood attenuation capacity, water supply and water quality. Additionally, all of these can a ect human communities in terms of health, agricultural productivity and safety. is is particularly important in rural and peri-urban areas where 578 people are immediately dependent on run-of-river water supply and quality. e e ective rehabilitation of degraded areas, when taking into account the need for considering the entire ecosystem and the reinstatement of ecological processes, can improve the delivery of water-related ecosystem services.
Perhaps the most important aspect of water distribution is the partitioning of water into surface and sub-surface water, the latter o en being derived from in ltration and percolation through the soil pro le, as a result of which rainfall becomes shallow or deep groundwater which contributes to sustained base ows and thus water supply (Kosgei et al., 2007;Wenninger et al., 2008;Van Tol et al., 2010). Dilution of pollutants through a su cient and sustained water supply has a direct bearing on water quality. is, in turn, has a marked e ect on a number of ecosystem service bene ts to society, including human health (Keeler et al., 2012). Identi cation of socio-economic needs such as human health (and hence desired bene ts derived from ecosystem services) can drive the mapping of ecosystem services and in turn the identi cation of priority areas for investment into ecological infrastructure protection and/or rehabilitation. Such investments could include the securing and rehabilitation of naturally functioning ecosystems, including grasslands, riparian zones and wetlands.
In naturally perennial systems, base ow is maintained by healthy ecological infrastructure through providing steady in ltration and percolation. Base ow drives the functionality of many water-related ecosystem services (see Fig. 3), notably water quality and run-of-river abstraction in the dry season (both of which are key considerations in times of drought) and for aquatic ecosystem function throughout the year to support the ecological reserve, and ensure that primary water users have sustained access to su cient, good quality water.
In contrast to base ow, surface or near-surface runo (referred to as quick ow), i.e., the water which runs o the surface or near-surface following a rainfall event, does not in ltrate to the lower layers of soil (Le Maitre et al., 2014). While it contributes to the water supply of the river, should the natural balance between quick ow and base ow be disrupted, too much quick ow can mobilise excessive sediments and nutrients from the surface (Dlamini et al., 2014). Sediments and

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nutrients are moved downslope and deposited in lower-lying areas and water courses, changing the area's geomorphological structure and potentially compromising the quality of the water in the river. Prevention of excessive sediment mobilisation is therefore another key ecosystem service. Generation of higher amounts of sediment than are characteristic of the system results in degradation, and this sediment is likely to be transported towards, and within, water courses, altering natural ow paths and ecosystem processes, and/or be deposited in dams. Man-made dams are designed to contain and consistently supply water to domestic, industrial and agricultural users. Sedimentation may thus reduce their capacity and lifespan (Csiki and Rhoads, 2010) and lead to more frequent spilling and/or the need for costly dredging, and a loss of storage capacity.

Mapping of ecosystem services
Decision making based on the concept of ecosystem services has gained academic and political traction over recent years, and it is important that these services are able to be mapped and quanti ed (Daily et al., 2009;Seppelt et al., 2011). Brauman et al. (2007) identi ed the potential knowledge gaps of water-related ecosystem services in terms of location, scale and connectivity, and the likelihood that mapping could make a useful contribution to ecosystem service assessments. A common approach to assessing ecosystem services is the use of proxy variables, or surrogates, particularly of land cover, to represent ecosystem processes and to map services using a geographical information system (GIS) (Egoh et al., 2008;Seppelt et al., 2011;Burkhard et al., 2012).
Focusing on water-related ecosystem services in South Africa, Egoh et al. (2008Egoh et al. ( , 2009Egoh et al. ( , 2011 mapped surface water supply (using runo ) and water ow regulation services (using groundwater) across South Africa. Spatially, results of these studies are presented at the spatial scale of quaternary catchments (i.e. delineated to the fourth level of disaggregation, average area of ~ 650 km 2 ), as well as at the temporal scale of annual averages, which is appropriate for national scale assessments and comparisons, but may not be adequate for municipal/catchment planning.
Although the spatial unit of analysis of many ecosystem service studies may be at a small enough scale to allow for catchment-scale development or rehabilitation planning, temporal scale is generally presented as an annual average, which does not take inter-annual variability, seasonality, nor impacts of individual hydrological events, into account. For catchment and municipal-scale planning, seasonality and inter-annual variability are vital aspects to consider with regard to South Africa's naturally discrete dry and wet seasons, and also the variations in summer rainfall which are associated with the cycle of the El-Niño Southern Oscillation (Malherbe et al., 2016).
Relatively few studies have been reported which use simulation models to map ecosystem services (Seppelt et al., 2011), and many rely on expert opinion to provide links to land cover data. e application of models that operate according to the biophysical principles and feedback mechanisms of the hydrological cycle that represent the water ow through the landscape over long time periods provides an advance in the way that maps of water-related ecosystem services can be derived. e value of daily time-step models in the valuation of water-related ecosystem services, particularly with respect to land use change and feedback mechanisms, has been speci cally recognised (Seppelt et al., 2011;Keeler et al., 2012), but has seen little application, particularly in South Africa. In this study, we have used a daily time-step hydrological model which has a hydrological 'memory'. e model carries through water volumes and states by way of a day-to-day water balance, taking feedback mechanisms/complexity into account. It is applied at a small spatial resolution, providing information appropriate to catchment-level decision making and providing a signi cant advance on previous studies.

Motivation for the study of the uMngeni catchment
roughout South Africa, water engineers from large municipalities and water boards face ongoing pressure in terms of water service delivery. Stakeholders such as these are, however, beginning to show a willingness to invest in the rehabilitation of upstream catchments for improved water availability and security downstream (e.g. e ekwini Municipality, 2012). It is, therefore, important for scientists and water resource managers to be able to guide potential investors in terms of where their money may be best spent, i.e., where the largest gains in water could be made through rehabilitation actions. us, our aim was to use a spatially explicit method for the prioritisation of areas for investment into EI assets in the uMngeni catchment. is paper describes the motivation for the use of the uMngeni catchment as a case study, as well as the methods used to prioritise areas for investment, and Part 2 describes the results and outputs.
e uMngeni catchment provides an excellent case study for the exploration of the potential value of EI rehabilitation interventions for several reasons. From an institutional perspective, the uMngeni Ecological Infrastructure Partnership (UEIP), which is made up of 23 signatories including both government and non-government agencies and tertiary institutions, all of whom recognise the role that investments in EI can play in the enhancement of water and sanitation services in the uMngeni catchment, has made a case for incorporating EI solutions into catchment management (Jewitt et al., 2015a). e South African National Biodiversity Institute (SANBI) has laid considerable groundwork in terms of the role of EI in delivering water-related ecosystem services (e.g. Blignaut et al., 2010;Holness and Skowno, 2013;SANBI, 2014). ese studies have found a strong link between healthy EI, delivery of ecosystem services and socio-economic development, and have attracted investment into South Africa to reduce the risks associated with water scarcity and water-related natural disasters such as droughts and oods (SANBI, 2014).

Study area
e uMngeni catchment (± 4 400 km 2 , 921 mm rainfall per annum; Umgeni Water, 2016) is located in the province of KwaZulu-Natal, South Africa, and hosts the country's secondlargest economic hub, and its largest trade port. It is a summer rainfall region mostly characterised by grassland, although much of this area has been cultivated. ere are also areas of thicket and bushland, with forest patches (Umgeni Water, 2016). Mean annual temperatures range between 14 and 22°C. ere is a current focus on trade, investment, imports and exports in the following key sectors: manufacturing (automotive, chemical, metals and maritime), agriculture, tourism, transport and logistics, and the green economy ( KZN Provincial Planning Commission, 2012). However, economic growth and rapid immigration from rural areas (known as urbanisation; United Nations, Department of Economic and Social A airs, Population Division, 2014), which exceeds the growth in employment, places increasing pressure on the catchment's natural resources.
e emphasis for delivery of water to the catchment's people is currently aimed at more investment into built infrastructure. However, the extent of degradation of EI and loss of natural land cover through transformation within the uMngeni catchment over time has compromised the system's natural ability to perform optimally in delivering strategically important waterrelated ecosystem services (Jewitt et al., 2015a). e local water authority states that the uMngeni River catchment, supported by a transfer scheme from the adjacent Mooi River catchment, is able to yield approximately 1 050 ML per day at a 99% level of assurance of supply from its various major supply dams, viz., Midmar, Albert Falls, Nagle and Inanda (Umgeni Water, 2015). In the 2013/14 nancial year, however, the demand exceeded this amount by over 75 ML per day. Demand is projected to increase to 1 800 ML per day by 2043/44 owing to further economic development (Umgeni Water, 2015), which will lead to a lower assurance of supply and a high risk of shortfall. e degradation of natural land (and loss of EI) in the uMngeni catchment over recent decades also implies a change in the partitioning of rainfall, as well as a reduction in the catchment's ability to sustain water-related ecosystem services. is is likely to have led to an increase in surface runo from areas overgrazed/trampled by livestock, or from hardened roads and roofs, which means that base ow and groundwater recharge is reduced, and may not be adequate to sustain the catchment in the dry season. In as little as 6 years (2005)(2006)(2007)(2008)(2009)(2010)(2011), the KwaZulu-Natal Province, in which the uMngeni catchment lies, has lost as much as 7.6% of its natural land due to anthropogenic transformation (mainly due to agriculture, timber plantations, the built environment, dams and mines; Jewitt et al., 2015b), which brings the total of natural land lost in the catchment to almost 48%.

MATERIALS AND METHODS
is project used established hydrological modelling and GIS techniques to map and model water-related ecosystem service delivery from land cover within the catchment. e following water-related ecosystem services were the focus of the initial mapping process, and they were selected on the basis of previous research elsewhere (e.g. Brauman et al., 2007), discussions with various experts in the eld, and available data: • Water supply: provision of water throughout the year for domestic, industrial, ecological and recreational use (modelled and mapped as stream ow). • Sustained base ow: maintenance of water supply during dry periods, and associated water quality maintenance due to assimilation and/or dilution of excess nutrients and waste (see Fig. 3). • Erosion control and avoidance of excessive sediment losses: avoidance of the mobilisation of excessive sediments from upslope land areas to watercourses and dams, thus a ecting the nutrient distribution in the landscape and reducing dam storage capacity, as well as resulting in turbidity in water courses. is includes the transport of soluble nitrates as well as phosphates -the latter, importantly, being sedimentbound (Pettersson et al., 1988).

The ACRU model
e ACRU (Agricultural Catchments Research Unit) model (Fig. 4), a detailed, daily time-step hydrological model which is able to operate at an appropriate spatial scale for planning, has been widely used for land use impact studies in South Africa, Eritrea, Zimbabwe, United States of America, Germany, New Zealand and Canada. e model has been used in the Upper ukela and Baviaanskloof in South Africa for similar ecosystem servicebased studies (Maloti Drakensberg Transfrontier Project, 2007;Blignaut et al., 2010;Mander et al., 2010). Importantly, Warburton et al. (2010) undertook a comprehensive simulation study of the hydrology of the uMngeni catchment with the ACRU model and con rmed the ability of the model to represent the high, low and total ows, with satisfactory comparison statistics (Table 1). ey concluded that the model was able provide a satisfactory simulation of stream ow from the range of climates and diversity of land uses present within the catchment.

Flow modelling in ACRU
Outputs from the ACRU model were used to derive maps of the areas of ecological infrastructure that generate water-related ecosystem services. In the model, processes directly a ected by land cover, i.e., canopy interception loss, evaporation from vegetated surfaces and soil water extraction by plant roots all directly contribute to total evaporation (Schulze, 1995). ese processes are controlled by a range of parameters including those which control the magnitude of interception and transpiration for di erent plants in their di erent stages of growth, rooting pattern and depth and those which a ect the composition of the soil and its in ltrability. is a ects the amount of water available in each of the soil horizons, which in turn a ects the amount of runo (in the form of quick ow or base ow) generated. e key output parameters from the model as they relate to the water-related ecosystem services, as already mentioned above, include:

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• Runo (water supply/stream ow) • Quick ow (non-delayed storm ow, i.e., water available at or near to the surface on the same day as the rainfall event; water supply) • Base ow (water which has in ltrated to lower soil layers and provides recharge to the groundwater store which then discharges into rivers and sustains ows in the dry season) • Sediment yield (soil mobilised/eroded from the landscape part of the catchment and entering the stream) Base ow is modelled explicitly within ACRU, with the value derived from soil water which has percolated out of the base of the sub-soil (B) horizon, and into a base ow store (Smithers and Schulze, 2004). e store which collects base ow is connected in the model to the stream channel, and releases water into the

Figure 4
Schematic representation of the ACRU model's water budget (Schulze, 1995) , 2004). e sediment yield functions used in the ACRU model consider, inter alia, storm ow (as the surrogate for sediment yield transport), peak discharge (used as an indicator of soil particle dislodgement), erodibility characteristics of soils, slope length and a vegetation cover factor that considers both above-ground and surface protection characteristics.

Setting up the sub-catchments and hydrological response units
Building from Warburton et al. (2010), the catchment has been delineated into 145 sub-catchments (Fig. 5). ese sub-catchments range in area from 37 to 11 000 ha, and are di erentiated on the basis of soils, altitude, topography, land cover, water management practices and gauging stations within the uMngeni catchment. e catchments are in turn grouped into 13 quaternary catchments. For the current study, the 13 quaternaries were further grouped into 6 'dam' catchments to analyse di erent user groupings based on population clusters and areas supplied by each of the dams and, in turn,

Figure 5
Dam catchments, quaternary catchments and sub-catchments within the uMngeni catchment used for this study  (Table 2). e assessment of ecosystem service requirements and bene ts formed part of a separate process of interactions with catchment stakeholders and information gathering on water use, water users and built infrastructure mapping, and is described by Mander et al. (2017). e 145 sub-catchments have each been further sub-delineated into 11 hydrological response units (HRUs), i.e., representative land areas with similar hydrological characteristics/responses, based on vegetation types, speci c land uses and classes of urbanisation. Although the sub-catchment boundaries are spatially explicit, the HRUs are not. Within each subcatchment, the non-irrigated land uses are linked to the areas of natural vegetation, which in turn are linked to the areas of commercial agriculture and riparian zones, such that each HRU's individual stream ows are logically routed through each sub-catchment (Fig. 6).

Land cover classes and parameterisation
Within each of the 145 sub-catchments, each of the 11 land cover types making up the sub-catchment is modelled individually as an HRU. e outputs from the model can therefore quantify and indicate the relative degree of delivery of each service from each land cover type in the various sub-catchments. e original model con guration (Warburton et al., 2010) was set up using information from the year 2000 National Land Cover imagery (NLC, 2000) and individual sub-catchments, with soils information (Schulze et al., 2008), together with default input values obtained from the ACRU User Manual (Smithers and Schulze, 2004) where no better information was available. is project, however, made use of more recent land cover data available at the time of writing, viz., the 2011 KwaZulu-Natal provincial land cover map (EKZNW and GTI, 2013). us, the area of each HRU was updated to re ect this. e land cover classes which were translated into HRUs for the modelling process are summarised for each sub-catchment in Table 3).
ree HRUs were targeted during this study to highlight hydrological di erences between degraded and healthy EI, namely the HRUs with invasive alien plants (IAPs), degraded vegetation (which was modelled as overgrazed land using the ACRU model hydrological attributes for overgrazed lands developed by Schulze et al. (2007) for the grasslands of KwaZulu-Natal and the Eastern Cape) for Maloti Drakensberg Transfrontier Project (2007), and untransformed natural vegetation (grassland or forest areas which were not considered by the mapping team to be degraded). Figure 7 shows their distribution and extent, and these HRUs are highlighted in bold in Table 3. Full details of the ACRU parameters used for the modelling process are provided in Table A1, Appendix. e 2011 land cover data do not contain a mapped coverage of IAPs. A mapped and ground-truthed coverage of invasive alien wattle species (notably Acacia mearnsii and A. dealbata) provided by Umgeni Water (dated 2007) was thus used to represent this HRU. We acknowledge that these data are outdated and limited, and that our estimates indicate that they are far more extensively distributed at the time of the research than in 2007. However, it was the most reliable dataset of IAPs available at the time of the study. Furthermore, wattle trees are acknowledged to be the most problematic alien plant species in South Africa at present (Le Maitre et al., 2013), and give an indication of hydrological responses to woody IAP species.
Parameters used for the HRUs infested by Acacia mearnsii are shown in Table 4. e default parameters provided within ACRU were used -however, the key parameter of canopy and interception loss (VEGINT) was increased to a value of 3.3 based on Schulze and Schütte (2014) and Bulcock and Jewitt (2012). is value was determined using eldwork based on cultivated wattle trees and may thus be higher than might be expected for an IAP infestation. Furthermore, anecdotal evidence suggests that IAPs 'thin out' when they have been established for many years (as opposed to newly established trees), and this may imply a lower water use than for cultivated plantations.

The e ects of severe overgrazing
e hydrological e ects of overgrazing, according to Maloti Drakensberg Transfrontier Project (2007), and based on the literature (e.g. Trimble and Mendel, 1995;Sahin and Hall, 1996;Illius and O'Connor, 1999), are summarised below: • A reduction in above-ground biomass, which in turn results in a decrease in transpiration, with the decrease dependent on whether the original natural veld had a relatively high or low biomass, as well as a decrease in canopy interception and the canopy's protective properties in regard to soil loss. • A reduction in litter or mulch on the soil surface, which results in increases in the rate of soil water evaporation, thus drying out the topsoil horizon more rapidly and exposing the soil to more severe erosion. • A possible compaction of the more exposed soil surface through rainfall compaction during convective events and trampling by livestock, which can result in a reduction in the in ltration of rain into the soil. Table 5 provides an example of how the parameters for degraded vegetation were derived based on the above for the Natal Mist Belt Ngongoni Veld natural vegetation type. ACRU parameters to be changed for the simulation of runo from degraded areas relative to natural conditions include the • e water use (crop) coe cient (CAY) is reduced by a factor of 1.4, because overgrazed areas have less above-ground biomass, but with a minimum CAY value of 0.2 in any month.
• e coe cient of initial abstraction (COIAM, an index of in ltrability of rainwater into the soil) is assigned a value of 0.10 for November to March (when thunderstorms occur), 0.15 for April, May and October and 0.20 for June to September, as a result of assumed trampling of grazing areas.
• e percentage litter/mulch (PCSUCO), is reduced to 10 % for all months of the year.
• e root colonisation in the subsoil (COLON), with reduced above-ground biomass, reduces to 60% in all months (and reduced to 50% if already lower than 60%). • e fraction of surface cover protection is reduced and with the resultant enhanced sediment losses the COVER-factor is increased accordingly to 0.24 in all months and for all Veld Types.

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Climatic data e ACRU model was run using daily historical climate data from 1961-1999 (Lynch, 2004), which at the time of the study was the most readily available, consistent and quality controlled dataset. It is recognised that the latest climate data have not been included in the model, but the available record is considered to be su ciently representative of the catchment's climate, including periods of oods and droughts. Owing to the focus on EI, i.e., terrestrial HRUs such as grasslands, and to allow for more e cient running of the model, each subcatchment was run individually, and results therefore derived and analysed for each. As explained above, the study focused on the quanti cation and mapping of two water-related ecosystem services, namely, water supply (in the form of base ow, surface runo and total stream ow) and sediment yield.  Acacia mearnsii CAY 0.9 0.9 0.9 0.9 0.9 0.9 0.9 0.9 0.9 0.9 0.9 0.9

CONCLUSION
ere is a growing recognition that investment in ecological infrastructure through rehabilitation and responsible land management can improve delivery of ecosystem services, and thus create a strong platform for socio-economic development.
is requires hydrological modelling at spatial and temporal scales which are adequate for planning to allow planners to align potential ecosystem service delivery with stakeholder needs. e ACRU model was set up to map the delivery of waterrelated ecosystem services associated with three broad land cover types in the uMngeni catchment. We incorporated recent available land cover data into an existing catchment con guration, and set up the model to calculate components of runo and sediment yield for each HRU in the catchment. e model incorporates hydrological feedback mechanisms, and responds to wet and dry spells in the rainfall record, thus proving extremely useful for identifying inter-and intra-seasonal catchment response characteristics. It should be noted that certain parameters have been updated between this version of the model and the con rmation study (Warburton et al., 2010). However, given the improvement in eld-based and information (e.g. Bulcock and Jewitt, 2012) and expert knowledge (Maloti Drakensberg Transfrontier Project, 2007) introduced in this version, we consider these changes to strengthen the model. We acknowledge that there remains a lack of direct eld-based measurements for several land use/cover types to inform model parameterisation. However, for a rapid, large-scale, comparative study such as this, we consider the model setup to be su ciently reliable for water resource planning. e results of this modelling exercise are presented in Part 2 of this paper ('Mapping of water-related ecosystem services in the uMngeni catchment using a daily time-step hydrological model for prioritisation of ecological infrastructure investment. Part 2: Outputs'; Hughes et al., 2018), which also discusses the identi cation of priority areas for each water-related ecosystem service within the catchment, and illustrates the useful contribution that can be made by detailed hydrological modelling towards achieving desirable socio-economic outcomes, such as the provision of a cleaner and more sustained supply of water to South Africa's people.  Monthly values of average crop coe cients (CAY), interception loss (VEGINT, mm.rainday -1 ), fraction of roots active in the topsoil (ROOTA), coe cient of initial abstraction (COIAM, which determines in ltrability into the soil and is used to estimate the rainfall abstracted by interception, surface storage and in ltration before storm ow commences) and percentage (%) of surface cover (mulch etc., PCSUCO) -the maximum evaporation from the soil can be suppressed by surface cover such as mulch, litter and surface rock. These parameters are provided for the healthy (pristine) and degraded Ngongoni Veld HRU as an example (Acocks, 1988), and for Acacia mearnsii. The ACRU model rules and hydrological attributes for overgrazed lands which were developed by Schulze et al. (2007) in the grasslands of KwaZulu-Natal and Eastern Cape for Maloti Drakensberg Transfrontier Project (2007), were used.