Overview There is increasing and competing demand for scarce water resources across Asia for household, industrial, municipal, and agricultural use. As a result, water shortages have become more frequent in many areas, while water quality has also deteriorated. Groundwater serves over a third of the world’s irrigated areas and provides 25%–40% of the world’s drinking water (Asian Development Bank 2016 and National Groundwater Association 2010). Of the 15 countries that are the biggest abstractors of groundwater, seven are in Asia and the Pacific, and South Asia alone accounts for around 50% of global groundwater use (ADB 2016 and Margat and van der Gun 2013). Current patterns of agricultural groundwater use are not sustainable and will result in permanent damage to both the quantity and quality of groundwater resources (Siebert et al. 2010). Increasing water pollution from household, industrial, and agricultural activities is a major concern for nearly all developing Asian countries. Irrigation, high levels of agrochemical consumption, and high sediment loads, are significant sources of nonpoint source water pollution (Chakraborty and Mukhopadhyay 2014; Evans et al. 2012; and FAO 2011). Only about a third of all wastewater in Asia is treated with the lowest treatment rates in South Asia (7%) and Southeast Asia (14%), according to FAO AQUASTAT. This is due largely to lack of (i) financial resources to build sewers and wastewater treatment facilities and (ii) well-defined policies (Sato et al. 2013). Pollution and overexploitation of natural capital–such as wastewater discharges and agricultural runoff and drainage, and logging for timber–can affect ecosystems’ capacity to provide fresh water and other resources and to regulate water quality and water table levels, as well as other processes. Poorly designed infrastructure and fragmented basin management approaches exacerbate these impacts (Grooten and Almond 2018 and United Nations World Water Assessment Programme 2015). Countries, such as India, People’s Republic of China (PRC), Philippines, and Thailand, have started large programs to rehabilitate degraded water resources through legislative or statutory authorities. However, enforcing regulations is challenging. Institutional capacities are not able to keep up with rapid industrialization. Monitoring is inadequate and costly, and as a result, compliance is typically poor. Market-based instruments offer flexible and innovative solutions for improving resource use and environmental quality and provide economic incentives to meet environmental goals. If properly designed and implemented, these can reduce pollution at the lowest cost with the potential to facilitate even greater reductions than command and control regulations. This article is adapted from the chapter on water of Greening Markets: Market-Based Approaches for Environmental Management in Asia. The chapter assesses the suitability of using different market-based instruments to address water use and pollution in Asia and provides recommendations and enabling conditions for specific interventions. Market-Based Instruments for Water Management Based on a systematic analysis that synthesizes findings from previous studies of the use of market-based instruments in selected countries in East Asia, South Asia, and Southeast Asia, the report identifies five categories of market-based instruments used to address inefficient use of irrigation water, poor intersectoral allocation of water, poor surface water quality, and failure to protect and value ecosystems: markets for trading water use and pollution rights; taxes, fees, and charges; subsidies; payments for ecosystem services; and information provision. The review resulted in the following findings. Water pricing may be effective though politically challenging. The efficient use of water requires prices equal to the marginal cost of providing the water, including the external costs associated with its use. While this type of pricing encourages users to limit water use, cost recovery may be difficult to achieve if marginal costs are lower than average costs or average costs are decreasing (Easter and Liu 2005). However, in most cases in Asia, long run marginal costs are above average costs due to economic and population growth, so this is not a concern. Volumetric pricing as a market-based instrument can tackle inefficient use of irrigation water by charging farmers the amount of irrigation water consumed or delivered. Findings suggest that volumetric water pricing can lead to increases in efficiency and/or shifts to high-value or less water-intensive crops (Kumar, Scott, and Singh 2011; Mukherji 2007; Shiferaw, Reddy, and Wani 2008; and Wang et al. 2010). However, pricing has largely been ineffective at current levels and increasing the price enough to have an impact on use has been politically difficult. Implementation can be costly as it requires an extensive network of water meters and a central water authority to set the price, monitor use, and collect fees. In Bangladesh, the Barind Multipurpose Development Authority pioneered a volumetric irrigation fee and pre-paid metering system in deep tube wells for a groundwater-based irrigation system, which resulted in substantial cost recovery of irrigation water supply (Gain, Mondal, and Rahman 2017). Intersectoral water allocations need functional markets and strong regulatory frameworks. In many cases, urban water supply can be augmented through transfers of water from agriculture (Molle and Berkoff 2006). Water can be transferred across sectors as a permanent change or as a temporary reallocation, such as during a drought. Two prominent examples of intersectoral water transfers in the PRC include transfers from agriculture to industrial, municipal, and hydropower use in Hubei’s Zhanghe Reservoir, and transfers of water-usage rights by the government in Ningxia (Moore 2015; Zhang 2012; and Zhang et al. 2016). Gradual permanent transfers can also occur when a source is increasingly diverted to supply a city (Molle and Berkoff 2006), as was the case in the Zhanghe Reservoir in the PRC and the Chao Phraya River in Thailand. Cases of temporary transfers have occurred in Chennai, India by buying water from surrounding wells in times of shortage and in Manila, Philippines, by reallocating water stored in reservoirs for agricultural use to municipal use. Of the transfer mechanisms, market-based instruments include (i) trading formal rights in a regulated market with positive experiences confined to economies with a strong legal, institutional, and regulatory background, such as the California Water Bank or other markets in Australia, Chile, and the United States and (ii) purchasing water from tankers in a free market (e.g., Chennai) or from neighbors in “spot markets,” such as warabandi in India and Pakistan (Molle and Berkoff 2006). Though infrequent, intersectoral and inter-regional water transfers can occur through formal administrative decisions with negotiation and compensation, or through water markets. Functional water markets for intersectoral and inter-regional water allocations require well-defined, quantifiable, and transferable property rights (Dinar, Rosegrant, and Meinzen-Dick 1997) and an accounting for hydrological realities such as return flows (Young 2014). Effluent taxes can put a price on polluting discharges. Effluent charges have been used successfully to address and curb pollution in the region. In 1978, Malaysia introduced one of the world’s first market-based instruments—effluent fees, paired with licensing—to control pollution from the palm oil and rubber industries (Hojat and Rahim 2012; Rahim 2005; Stavins 2001; and World Bank 1997). A year after the imposition of discharge standards, the pollution load fell by more than half (Catelo, Francisco, and Darvin 2016). Over a span of 2 decades, the organic pollution load decreased by about 90% and firms that owned crude palm oil and rubber mills also invested in wastewater treatment technology innovation. The Philippines introduced discharge fees on Laguna Lake in 1997. This decreased by 88% the biochemical oxygen demand discharges between 1997 and 1999 (Stavins 2001 and Wheeler et al. 2000) and reduced the industrial sector’s contribution to lake pollution from 40% in 1997 to only 11% in 2006. Increased wastewater treatment, wastewater recycling, waste minimization, and voluntary closure or plant relocation also contributed to less wastewater discharge. Nutrient taxes can address nonpoint source pollution of water from agriculture. Taxing discharge can be challenging as nonpoint source pollution, such as agricultural runoff, may be difficult to observe or monitor. Nutrient taxes—an input-based policy instrument used to reduce pollution—provide a solution. Output-based policies can also encourage farmers to shift to less fertilizer-intensive crops through taxes or subsidies (Sun, Delgado, and Sesmero 2016). Additionally, perverse incentives that contribute to pollution, such as subsidies for fertilizer or payments to encourage land use change, need to be reduced. Tradable discharge permits require a strong regulatory framework to be effective. In a system of tradable discharge permits, the water management authority limits the amount of emissions for a particular ecosystem, then divides the total amount of emissions into a fixed number of permits. After the initial allocations (through auctions or past levels of discharge), the holders can be allowed to trade their permits in a secondary market (Borghesi 2014). Through this system, pollution abatement can be allocated to firms that have the most efficient production and abatement technologies. In some situations, tradable discharge permits systems can outperform taxes and voluntary best management practices in terms of welfare and environmental effectiveness (Borghesi 2014; Johansson and Moledina 2005; and Young and Karkoski 2000). The political feasibility of a tradable permits program is also often higher than for an environmental tax because the initial allocation of rights to legally discharge emissions has a high market value (Borghesi 2014). However, they require strong monitoring and enforcement of environmental regulations to be effective in pollution abatement. Information asymmetries between regulators and market participants also make compliance difficult (Borghesi 2014). Incentives are needed to promote the use of green infrastructure. In rapidly growing cities, surface runoff of rainwater has become a major source of water pollution and flooding because of poor infrastructure and extreme weather events. Policy instruments can facilitate the uptake of green infrastructure projects, such as rainwater collection systems, green roofs, permeable pavements, and nature-based solutions for drainage to manage runoff, as an alternative or complement to traditional flood protection infrastructure. Development, financing, and tax incentives encourage investments and installation of green infrastructure for residential and non-residential users. Singapore’s Skyrise Greenery Incentive Scheme funds up to 50% of the cost of installing rooftop and vertical greenery (Government of Singapore, National Parks 2020). Behavioral nudges help influence decision-making on water use. Psychological interventions, or behavioral nudges, to influence water users’ behavior and decision-making can complement the use of market-based instruments (Russell and Fielding 2010). These include tools, such as social comparison messages (Ferraro and Price 2013 and Torres, Marcela, and Carlsson 2016), information provision on water quality (Brown et al. 2017), and a combination of technical information, moral persuasion, and social comparison (Bernedo, Ferraro, and Price 2014). They are likely to be most attractive for short-term use during droughts and in middle-income countries where households already have sewer connections and where wastewater treatment is already provided. (Nauges and Whittington 2019). Creating and defining property rights is necessary for successful implementation. This will ensure that water is available for the environment and for downstream users. The rights can then be traded at market-determined prices. For instance, by installing meters, water markets and water users (companies or individuals) can trade rights or entitlements to use water at the market equilibrium price (Easter and Liu 2005; Gómez, Delacámara, and Pérez- Blanco 2013; Hanak et al. 2011; Rey, Calatrava, and Garrido 2011; and Young 2010). Implementation can be challenging because property rights must be defined simply and clearly enough to be easily traded, while sufficiently reflecting the reality and complexity of the underlying ecosystem service; property rights must align with existing institutional and legal frameworks; the nature of the property right will depend on the characteristics of the good or service and the proposed market structure; and property rights must account for the variable nature of water availability. Thus, most water rights confer an entitlement that depends directly or indirectly on the amount of water stored upstream. A hybrid policy of information provision and effluent charges may achieve pollution reduction goals. In general, effluent charges and pollution taxes for industrial pollution in Asia have been set too low and enforcement has been weak. However, information provision and labeling for point source water pollution were successful in several countries, including Indonesia, Malaysia, PRC, and Philippines. Experience suggests that a policy mix of both information provision and effluent charges is the best way forward in most locations. Effluent charges incentivize innovation, while information provision can help correct information asymmetries with the public and make noncompliance costlier for polluters. Scaling up payments for ecosystem services shows promise. Due to lack of knowledge and capacity, many policy makers have failed to recognize the economic value of healthy ecosystems and build on basin-wide and cross-sectoral synergies needed for improved water management (United Nations World Water Assessment Programme 2015). In response, there have been increasing efforts to implement and invest in payments for ecosystem services schemes in developing countries for watershed protection and biodiversity conservation, among others. These schemes have been implemented in the region with varying levels of success. Scaling up successfully requires several enabling conditions, including political support, sustainable financing, lean institutional setup, effective tools and systems, clearly demonstrated impact, and flexibility to adapt to different conditions across target ecosystems and communities. Social benefits can also facilitate political will and resources to drive and expand programs and environmental investments (Porras 2015; Porras 2018; and Porras, Steele, and Mohammed 2016). In Viet Nam, a national program was developed to protect watersheds that had been overexploited. This helped to reduce the government’s financial burden for forest conservation and protection, as well as improved economic conditions and created sustainable livelihoods for communities protecting and managing the forests (Vietnam Forest Protection and Development Fund 2016). The success of such schemes also depends on well-informed ecosystem valuation studies, which quantify the price or value that consumers would be willing to pay or apply to protect ecosystem services, which can be incorporated into national income accounts and used to inform country planning and decision-making (Boelee 2011 and Dasgupta 2021). Valuation methods, coupled with information on how resources are used by involved communities, can help design markets for ecosystem services (Adhikari 2009). Recommendations The report provides the following recommendations for future applications of market-based instruments to improve water management and reduce water pollution: Employ behavioral nudges during droughts by using information to induce low-cost behavior changes in water use. Design and implement hybrid policy instruments to address water use and waste discharge, including both an effluent charge and an information provision policy, which can mitigate costs in policy implementation and create incentives for adopting environment-friendly technology and innovation. Expand payments for ecosystem services schemes under the right enabling conditions, including political and financial support, strong institutional setup, and transparency and communication. Resources Journal Articles A. E. V. Evans et al. 2012. Water Quality: Assessment of the Current Situation in Asia. International Journal of Water Resource Development. 28 (2). pp. 195–216. A. H. M. Hojat and K. A. Rahim. 2012. Effluent Charge Reform for Controlling Water Pollution in the Malaysian Crude Palm Oil Industry. Environment and Development Economics. 17 (6). pp. 781–794. A. K. Gain, M. S. Mondal, and R. Rahman. 2017. From Flood Control to Water Management: A Journey of Bangladesh Towards Integrated Water Resources Management. Water. 9. 55. A. Mukherji. 2007. The Energy-Irrigation Nexus and Its Impact on Groundwater Markets in Eastern Indo-Gangetic Basin: Evidence From West Bengal, India. Energy Policy. 35. pp. 6413–6430. B. Shiferaw, V. R. Reddy, and S. P. Wani. 2008. Watershed Externalities, Shifting Cropping Patterns and Groundwater Depletion in Indian Semi-Arid Villages: The Effect of Alternative Water Pricing Policies. Ecological Economics. 67 (2). pp. 327–340. C. M. Gómez, G. Delacámara, and C. D. Pérez-Blanco. 2013. Water Trading. In J. Mysiak et al, eds. Evaluating Economic Policy Instruments for Sustainable Water Management in Europe: Synthesis Report. EPI-Water. C. Nauges and D. Whittington. 2019. Social Norms Information Treatments in the Municipal Water Supply Sector: Some New Insights on Benefits and Costs. Water Economics and Policy. 5 (3). C. Zhang et al. 2016. Managing Scarce Water Resources in China’s Coal Power Industry. Environmental Management. 57 (6). pp. 1188–1203. D. Chakraborty and K. Mukhopadhyay. 2014. Water Pollution and Abatement Policy in India: A Study From an Economic Perspective. In A. Dinar et al., eds. Global Issues in Water Policy. 10. New York: Springer. J. Brown et al. 2017. Seeing, Believing, and Behaving: Heterogeneous Effects of an Information Intervention on Household Water Treatment. Journal of Environmental Economics and Management. 86. pp. 141–159. J. Wang et al. 2010. Water Governance and Water Use Efficiency: The Five Principles of WUA Management and Performance in China. JAWRA Journal of the American Water Resources Association. 46. pp. 665–685. K. A. Rahim. 2005. Market-Based Instruments for Environmental Protection: Piloting Presumptive Charge and Emissions Trading in Malaysian SMIs. International Journal of Business and Society. 6. pp. 1–36. M. Bernedo, P. J. Ferraro, and M. Price. 2014. The Persistent Impacts of Norm-Based Messaging and Their Implications for Water Conservation. Journal of Consumer Policy. 37 (3). pp. 437–452. M. D. Kumar, C. A. Scott, and O. P. Singh. 2011. Inducing the Shift From Flat-Rate or Free Agricultural Power to Metered Supply: Implications for Groundwater Depletion and Power Sector Viability in India. Journal of Hydrology. 409. pp. 382–394. M. D. Young. 2014. Designing Water Abstraction Regimes for an Ever-Changing and Ever-Varying Future. Agricultural Water Management. 145. pp. 32–38. P. J. Ferraro and M. K. Price. 2013. Using Nonpecuniary Strategies to Influence Behavior: Evidence From a Large-Scale Field Experiment. Review of Economics and Statistics. 95 (1). pp. 64–73. R. C. Johansson and A. Moledina. 2005. Comparing Policies to Improve Water Quality When Dischargers of Pollutants Are Strategic. Water International. 30. pp. 166–173. S. Borghesi. 2014. Water Tradable Permits: A Review of Theoretical and Case Studies. Journal of Environmental Planning and Management. 57 (9). pp. 1305–1332. S. M. Moore. 2015. The Development of Water Markets in China: Progress, Peril, and Prospects. Water Policy. 17 (2). pp. 253–267. S. Russell and K. Fielding. 2010. Water Demand Management Research: A Psychological Perspective. Water Resources Research. 46 (5). S. Siebert et al. 2010. Groundwater Use for Irrigation—A Global Inventory. Hydrology and Earth System Sciences. 14. pp. 1863–1880. S. Sun, M. S. Delgado, and J. P. Sesmero. 2016. Dynamic Adjustment in Agricultural Practices to Economic Incentives Aiming to Decrease Fertilizer Application. Journal of Environmental Management. 177. pp. 192–201. T. Sato et al. 2013. Global, Regional, and Country Level Need for Data on Wastewater Generation, Treatment, and Use. Agricultural Water Management. 130. pp. 1–3. T. Young and J. Karkoski. 2000. Green Evolution: Are Economic Incentives the Next Step in Nonpoint Source Pollution Control? Water Policy. 2. pp. 151–173. World Bank. 1997. Five Years After Rio: Innovations in Environmental Policy. Environmentally Sustainable Development. Studies and Monographs Series No. 18. Washington, D.C.: World Bank. Papers A. Dinar, M. Rosegrant, and R. Meinzen-Dick. 1997. Water Allocation Mechanisms: Principles and Examples. Policy Research Working Paper Series No. 1779. Washington, D.C.: World Bank. B. Adhikari. 2009. Market-Based Approaches to Environmental Management: A Review of Lessons from Payment for Environmental Services in Asia. Asian Development Bank Institute [ADBI] Working Paper No. 134. Tokyo, Japan: Asian Development Bank Institute. F. Molle and J. Berkoff. 2006. Cities versus Agriculture: Revisiting Intersectoral Water Transfers, Potential Gains and Conflicts. Research Report 10. Colombo: International Water Management Institute. J. Torres, M. Marcela, and F. Carlsson. 2016. Social Norms and Information Diffusion in Water-Saving Programs: Evidence From a Randomized Field Experiment in Colombia. Working Papers in Economics 652. University of Gothenburg, Department of Economics. R. N. Stavins. 2001. Experience with Market-Based Environmental Policy Instruments. Discussion Paper 01-58. Washington, DC: Resources for the Future. Publications Asian Development Bank (ADB). 2016. Asian Water Development Outlook 2016: Strengthening Water Security in Asia and the Pacific. Manila. ADB. 2021. Greening Markets: Market-Based Approaches for Environmental Management in Asia. Manila. D. Wheeler et al. 2000. Greening Industry: New Roles for Communities, Markets and Governments. New York: Oxford University Press for the World Bank. E. Boelee, ed. 2011. Ecosystems for Water and Food Security. Nairobi, Kenya and Colombo, Sri Lanka: United Nations Environment Programme/International Water Management Institute. E. Hanak et al. 2011. Managing California’s Water: From Conflict to Reconciliation. San Francisco: Public Policy Institute of California. I. Porras. 2015. Solutions for Less Poverty and Better Ecosystems. London, United Kingdom: International Institute for Environment and Development (IIED). I. Porras, P. Steele, and E. Mohammed. 2016. Upscaling Solutions: The Role of Conditional Transfers for Poverty Reduction and Ecosystem Management. London, United Kingdom: IIED. J. Margat and J. van der Gun. 2013. Groundwater around the World. Leiden, Netherlands: CRC Press/Balkema. K. W. Easter and Y. Liu. 2005. Cost Recovery and Water Pricing for Irrigation and Drainage Projects. Washington, D.C.: World Bank. L. Rey, J. Calatrava, and A. Garrido. 2014. Opportunities for Water Trading (WP2). In IWRM-NET Water Cap & Trade. Water Markets Scenarios for Southern Europe: New Solutions for Coping with Increasing Water Scarcity and Drought Risk? Final Project Report. L. Zhang. 2012. Advancing Water Rights Reform in North PRC [in Chinese]. In S. Jia, ed. Record of Chinese Water Rights Underway: A Case Study of Ge’ermu [in Chinese]. Beijing: PRC Water Conservancy and Hydropower Press. pp. 43–62. M. A. O. Catelo, H.A. Francisco, and B.A.C. Darvin. 2016. Economic Instruments in Environmental and Natural Resource Management in Southeast Asia and China: Lessons and Way Forward. M. Grooten and R. E. A. Almond, eds. 2018. Living Planet Report 2018: Aiming Higher. Gland, Switzerland: World Wide Fund for Nature. M. Young. 2010. Environmental Effectiveness and Economic Efficiency of Water Use in Agriculture. In OECD. OECD Studies on Water. Paris, France. P. Dasgupta. 2021. The Economics of Biodiversity: The Dasgupta Review. London: HM Treasury. United Nations World Water Assessment Programme. 2015. The United Nations World Water Development Report 2015: Water for a Sustainable World. Paris, France: UNESCO. Vietnam Forest Protection and Development Fund (VNFF). 2016. Assessment Report: 8 Years of Organization and Operation of Forest Protection and Development Fund (2008–2015) and 5 Years of Implementing the Policy on Payment for Forest Environmental Services (2011–2015). Ha Noi: VNFF. Web Pages Food and Agriculture Organization of the United Nations (FAO). AQUASTAT–FAO’s Global Information System on Water and Agriculture. (accessed 28 February 2018). Government of Singapore, National Parks. 2020. Skyrise Greenery Incentive Scheme. I. Porras. 2018. Fighting Poverty by Protecting the Environment Through Payment for Ecosystem Services. Development Asia. 2 February. National Groundwater Association. 2010. Facts About Global Groundwater Usage. Ask the Experts Dale Whittington Professor of Environmental Sciences & Engineering, City & Regional Planning, and Public Policy, University of North Carolina Since 1986, Dale Whittington has worked for the World Bank and other international agencies on the development and application of techniques for estimating the economic value of environmental resources in developing countries, with a particular focus on water and sanitation and vaccine policy issues. Isao Endo Environment Specialist, Environment Thematic Group, Sustainable Development and Climate Change Department, Asian Development Bank Isao Endo is an Environment Specialist working on natural resource management at ADB. He manages technical assistance to promote natural capital investments with a focus on nature-based solutions and market-based instruments, supporting ADB’s operation to integrate these innovative approaches into project design. He holds a bachelor’s degree in Economics from Sophia University and a master's degree in Environmental Management from Yale University. Asian Development Bank (ADB) The Asian Development Bank is committed to achieving a prosperous, inclusive, resilient, and sustainable Asia and the Pacific, while sustaining its efforts to eradicate extreme poverty. Established in 1966, it is owned by 68 members—49 from the region. Its main instruments for helping its developing member countries are policy dialogue, loans, equity investments, guarantees, grants, and technical assistance. Follow Asian Development Bank (ADB) on Leave your question or comment in the section below: View the discussion thread.