Material flow analysis of phosphorus through food consumption in two megacities in northern China

Material flow analysis of phosphorus through food consumption in two megacities in northern China

Chemosphere 84 (2011) 773–778 Contents lists available at ScienceDirect Chemosphere journal homepage: www.elsevier.com/locate/chemosphere Material ...

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Chemosphere 84 (2011) 773–778

Contents lists available at ScienceDirect

Chemosphere journal homepage: www.elsevier.com/locate/chemosphere

Material flow analysis of phosphorus through food consumption in two megacities in northern China Min Qiao, Yuan-Ming Zheng, Yong-Guan Zhu ⇑ State Key Lab of Regional and Urban Ecology, Research Center for Eco-Environmental Sciences, Chinese Academy of Sciences, Beijing 100085, China

a r t i c l e

i n f o

Article history: Received 25 September 2010 Received in revised form 1 December 2010 Accepted 20 January 2011 Available online 23 February 2011 Keywords: Phosphorus Food consumption Material flow analysis Megacities

a b s t r a c t The key stocks and flows of phosphorus (P) through food consumption in Beijing and Tianjin, two megacities in northern China, were explored using a material flow analysis (MFA) approach to construct a static model of P metabolism. A total of 4498 t P has accumulated with 72% of P flow imported through food consumption eventually remaining in Beijing in 2008. Around 64% of the total inflow of P (2670 t) remained in Tianjin in 2008. P in the uncollected sewage from both urban and rural residents and the effluents from sewage treatment plants has significant negative effects on water quality. An average of 55% the P flow remained in the sewage sludge through urban food consumption. The key problems in P metabolism and management in megacities are identified based on the quantitative analysis of P cycling through food consumption. Relevant solutions for improving P recycling efficiency are also discussed. It is important to link P flows with environmental regulations and to establish a strong coordination between urban and rural areas for nutrient recycling to attain sustainable development of megacities. Ó 2011 Elsevier Ltd. All rights reserved.

1. Introduction Phosphorus (P) is an essential element for food production and nearly 90% of societal use of P is for food production (including fertilizers, feed and food additives). However, P is a non-renewable resource, it has been claimed that global commercial phosphate reserves will be depleted within 50–100 years at the present rate of consumption, leaving behind lower quality and less accessible rocks (Smil, 2000). The increase in global demand for food and changing diets are two of the most important contributors to the increased demand for P because meat and dairy products require higher P inputs than other foods. Urbanization has a significant impact on the structure of food consumption. This is especially true in China because of its rapid economic development since the adoption of reform policies in the late 1970s. It has been reported that the level of urbanization in China has increased from 19.4% in 1980 to 44.9% in 2007 and consumption of animal-based foods increased from 61 g per capita daily in 1982 to 160 g per capita daily in 2002 (Wang, 2005). Moreover, urbanization has changed the biogeochemical cycling of P. Almost 100% of P eaten in food is excreted (Jönsson et al., 2004). In the past the nutrient flows from food via human excreta were typically recycled in a closed or approximately closed loop, but nowadays they more often end up in waterways via wastewater from urban centers or as sludge in landfills (Cordell et al., 2009). High anthropogenic nutrient loads are commonly the main cause of ⇑ Corresponding author. Tel.: +86 10 62936940; fax: +86 10 62923563. E-mail address: [email protected] (Y.-G. Zhu). 0045-6535/$ - see front matter Ó 2011 Elsevier Ltd. All rights reserved. doi:10.1016/j.chemosphere.2011.01.050

eutrophication in surface waters. Given the accelerated urbanization in developing countries and the slow natural mobilization of P, cities with high population densities, particularly capital cities, are becoming P ‘hotspots’ (Cohen, 2006). However, information is still lacking on P flows in these megacities. Material flow analysis (MFA) approaches have been widely used to analyze the global, national, or regional flows of P. Liu et al. (2008) quantified the global P flows associated with present day mining, farming, animal feeding, and household consumption, especially P movement in soil systems. Matsubae-Yokoyama et al. (2009) investigated the material flow of P within Japan including that in the iron and steel industry and found that the quantity of P in iron and steelmaking slag was almost equivalent to that in imported phosphate ore in terms of both the amount and concentration (Matsubae-Yokoyama et al., 2009). In contrast to these studies, close attention has been given to P movement linked to food consumption in the present study. The objective was to explore the flow of P in megacities considering their rapid urbanization and to indicate the potential environmental risk related to the output flows of P. This study was designed to provide useful information to help improve nutrient use efficiency in megacities.

2. Materials and methods 2.1. Background The geographical boundaries of the system analyzed were the land borders of Beijing and Tianjin, two of the four municipalities

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of China. Beijing, the national capital city is recognized as the political, educational, and cultural center. Tianjin is the largest coastal city in northern China and is also an important industrial base. The two megacities are the economic heart of north China and have exhibited rapid urbanization. The total and urban populations of Beijing between 1998 and 2008 increased from 10.01 and 6.79 million to 16.95 and 14.39 million, respectively (BMBS, 2009). Traditionally, the Chinese diet contained small quantities of animal sourced foods and high grain content. Economic growth and urbanization have had a significant impact on the shift of lifestyle such as the increased consumption of meat and refined carbohydrates. Furthermore, living in urban areas provides greater access to resources such as food markets and motorized transportation. For example, nowadays more than 90% of the vegetables in Beijing markets are supplied by other provinces such as Hebei and Shandong. Food consumption can therefore characterize part of the nutritional transition in these megacities. 2.2. Quantification methods The MFA approach is an analytical tool for assessing the flows and stocks of materials within a system defined in space and time. It is based on the Law of Mass Conservation to illustrate the complex socioeconomic systems of material metabolism and the principle is that of inflow equaling outflow plus accumulation (Fan et al., 2009). A static physical flow model is developed for P metabolism through food consumption in Beijing and Tianjin. For the sake of simplicity we qualified the P flow by considering seven sectors as presented in Fig. 1, with the P stored in the human body omitted from the calculation. The boundary for the MFA refers to the geographic boundaries of Beijing and Tianjin. The two cities contain both urban and rural areas. Considering that a large amount of food in urban area is provided from outside the city, the inflow of P is defined as the sum of P in the edible parts of all food consumed in the two cities without differentiating between locally and externally produced food. As shown in the Fig. 1, two subsystems, i.e. urban consumption and rural consumption, are distinguished due to their different dietary structures and waste disposal. The outflow of P through consumption is relatively difficult to estimate. For urban consumption, the excreta are mainly collected in sewage treatment plants. But for the rural area, the application of human excreta as organic fertilizer is more common. In recent years many optimized sewage treatment

techniques have been applied in the two megacities and the maximum P concentration permitted in effluents after treatment was set at 1.5 mg L 1 according to the Chinese Ministry of Environmental Protection (CMEP, 2002). After treatment, part of the effluent is discharged into aquatic systems and the P in that part will be exported from the city. However, the P in the reclaimed water which is utilized for irrigation of urban green landscapes will remain within the urban area. The conventional disposal methods for sewage sludge in China are landfill and application to agricultural crops (Wei et al., 2000), and this portion of P in sewage sludge will also stay in the cities. The food flux to solid waste refers to the P flux in garbage excluding the parts that have been reused by composting or other methods. The P in household garbage from both urban residents and rural residents will remain in the city because most of the garbage is also disposed of by landfill. Although the number of sewage treatment plants has increased dramatically in recent years, there is still some untreated sewage in which the P is piped directly into natural aquatic systems, especially in periurban and rural areas. An important outflow of P through food consumption is recycling through the application of human excreta as organic fertilizer which was a very common practice in ancient China. In the 1990s about 94% of human wastes in rural areas were returned to agricultural land. The recycling percentage is lower in urban than in rural areas but was still up to 90% in 1980 in urban areas (Liu et al., 2008). The recycled excretion is usually applied directly to agricultural land without treatment by dispersive families as families are the agricultural production units in China. The recycling percentage decreased dramatically with rapid urbanization and it may be safe to assume that about 10% of urban human wastes and about 60% of rural human wastes are recycled at present. Table 1 lists all the mathematical equations that were used to determine the amounts of P flow into and out of the two megacities. 2.3. Data sources This study addresses the P flow after rapid urbanization and, because of data limitations, the data on P flow analysis for food consumption were collected mainly from 2008. Four nationwide nutrition surveys organized by the Ministry of Health and the Ministry of Science and Technology with the help of State Statistical Bureau of China were conducted in 1959, 1982, 1992 and 2002. The results on daily dietary consumption of residents of Tianjin

U2 Reclaimed water

F1

W1

U4

Urban consumption

U1

Sewage treatment plant

W2

Aquatic

W3

U3

Food production system

solid waste disposal

system

R3

F2

Rural consumption

R1 R2

Fig. 1. Key phosphorus flows through food consumption. Dashed line indicates the border of the city.

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M. Qiao et al. / Chemosphere 84 (2011) 773–778 Table 1 Equations used for the calculation of phosphorus flow in Beijing and Tianjin. Flow

P flow description

From node

To node

Equation

F1 F2 U1 U2 U3 U4 W1 W2 W3 R1 R2 R3

Food consumption by urban population Food consumption by rural population Collected by urban sewage treatment system Direct discharge of domestic wastewater Household garbage Organic fertilizer from urban population Reclaimed water Discharge of treated wastewater Sewage sludge Household garbage Sewage Organic fertilizer from rural population

Food production Food production Urban consumption Urban consumption Urban consumption Urban consumption Sewage treatment plant Sewage treatment plant Sewage treatment plant Rural consumption Rural consumption Rural consumption

Urban consumption Rural consumption Urban sewage treatment plant Aquatic system Waste disposal Food production system Reclaimed water Aquatic system Solid waste disposal Waste disposal Aquatic system Food production system

F1 = P1  P2 F2 = P1  P2 U1 = P2  P3  X1 U2 = F1–U1–U3–U4 U3 = P2  X2  X3  (1 X4) U4 = P2  P3  X5 + P2  X2  X3  X4 W1 = X6  X7  X9  f W2 = (1 X6)X7  X9  f W3 = U1–W1–W2 R1 = P2  X3  (1–X8) R2 = F2–R1–R3 R3 = P2  P3  X5 + P2  X3  X8

in 2002 were used in this study. For Beijing residents the daily dietary intake of P was obtained from the latest survey in 2004 (Bao et al., 2007). The data on urban populations in Beijing and Tianjin as well as the urban sewage treatment rate in 2008 were from National Statistical Yearbook and the Regional Statistical Yearbook. The P concentration in solid waste of the two cities in 2008 is still unknown and the average P content in solid waste published in 2000 (Bian, 2000; Nie, 2000) was used in this study (Liu, 2004). Other key parameters are described in Table 2. 2.4. Uncertainty analysis There are clearly some uncertainties associated with the calculated data. Several factors such as variation in nutrient concentrations and possible inaccuracy of statistics will affect our results. In addition, the P flow of food consumed away from home, for example in restaurants, was not considered because no statistical data are available on the actual amounts of food consumed in restaurants in Beijing and Tianjin. It has been estimated that food consumed away from home comprises only 14% of the total food expenditure of Chinese urban households and thus represents only a small part of the P flow (Gould and Villarreal, 2006). 3. Results 3.1. Phosphorus flow through food consumption in Beijing in 2008 Fig. 2 presents an overview of P flows through food consumption in Beijing in 2008. According to our calculations, 5374 t and

849 t P in total were consumed by urban and rural residents, respectively. The largest outflow through food consumption in urban area is the flow to sewage treatment plants, representing about 3861 t P in 2008. Of this flow, 394 t P was discharged into natural aquatic systems after treatment, 544 t P was recycled as reclaimed water, and the remaining 2923 t P was landfilled within the city in the form of sewage sludge. Although the urban sewage treatment rate had increased to 78.9% in 2008, there were still about 1006 t P discharged directly due to the absence of sewage treatment plants and this accounted for 19% of the inflow of P. The P discharge in untreated sewage contributes most to water eutrophication in China. The outflow from food consumption to the final solid waste disposal constitutes only a small proportion based on the average P content in solid waste (Bian, 2000; Nie, 2000). China has a long tradition of use of human excreta as a fertilizer for crops but the percentage of human excreta used has decreased due to the rapid development of the chemical fertilizer industry. In large cities the utilization of human excreta is more difficult because of the increasing technical and economic costs of returning the nutrients to agricultural soils. Results showed that the return flow of manure was about 490 t P from urban residents and the sum of recycled P in human excreta was equivalent to ca. 11% of the nutrients in the phosphorus fertilizers applied to agricultural land in Beijing, which contained about 4463 t P (BMBS, 2009). In the case of rural residents most of the P flows in human excreta were reused but 38% of P flow was still discharged directly to the environment. A total of 4498 t P had accumulated. In other words, 72% of P flow imported through food consumption eventually remained in Beijing in 2008.

Table 2 Parameters in the phosphorus flow model. Parameter

Description

Unit

Beijing

1

Tianjin

References

Urban

Rural

Urban

Rural

1023

908.5

959.6

1017.9

P1

P intake from food consumption

mg d

P2 P3 X1 X2 X3 X4 X5 X6 X7 X8 X9

Population P in human excreta Urban sewage treatment rate Municipal solid waste collection rate Average P content in solid waste Composting rate of collected municipal solid waste Recycle percentage of human excreta Utilization rate of reclaimed water Disposal volume of municipal sewage Rural garbage reuse to croplands Maximal P concentration allowed in effluent after treatment Fraction of household sewage in municipal sewage drainage system

Thousand kg per 1 year 1 % % g per 1 year 1 % % % Million ton % mg L 1

14 391 0.34 78.9 98 1.26 4.1 10 58 1042.6 – 1.5

2559 0.34 – – 0.84 – 60 – – 10 1.5

9082 0.34 72.4 94 1.26 0 10 2 493.6 – 1.5

2678 0.34 – – 0.84 – 60 – – 10 1.5

Bao et al. (2007), Jiang et al. (2005), Wang (2005) NBSC (2009) Feng et al. (2009) BMBS (2009), TMBS (2009) BMBS (2009), TMBS (2009) Bian (2000), Nie (2000), Liu (2004) BMBS (2009), TMBS (2009) Chen and Tang (1999), Luo (2001) MOHURD, 2009 MOHURD (2009) Bian (2000), Liu (2004) CMEP (2002)

%

60



60



TMBS (2009)

f

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M. Qiao et al. / Chemosphere 84 (2011) 773–778

1006 Reclaimed water

5374

544

490

Urban consumption

3861

Sewage treatment plant

394

Aquatic

2923

17

Food production system

solid waste disposal

system

522

Rural consumption

1.9 325

849

Fig. 2. Phosphorus flows through food consumption in Beijing in 2008 (t).

3.2. Phosphorus flow through food consumption in Tianjin in 2008

4. Discussion

The flows of P in Tianjin in 2008 are illustrated in Fig. 3. The total inflow of P through food consumption was much less than in Beijing, mainly because of the smaller urban population. The urban residents in Tianjin consumed about 3181 t P and 70% of the P load or 2236 t P in wastewater was collected by sewage treatment plants. It is important to note that only a small fraction (2%) of the treated sewage was used as reclaimed water in Tianjin in 2008 (MOHURD, 2009). Thus, a large quantity of P flow (1792 t) remained in the city as sewage sludge and about 435 t P was eventually discharged into aquatic systems after treatment. The inflow of P through rural consumption was about 995 t P in Tianjin in 2008 and the reused P output from both urban and rural human excreta was 856 t P, accounting for ca. 5% of the nutrients in the phosphorus fertilizers applied in Tianjin. The solid waste P output was negligible in both urban and rural areas. Around 64% of the total inflow of P, that is, 2670 t P remained in Tianjin in 2008. The results are similar to previous studies which also indicate high levels of nutrient storage in metropolitan regions (Kennedy et al., 2007).

Based on the above analysis, we demonstrate that both Beijing and Tianjin input large quantities of P flow through food consumption but have lower P recycling efficiencies. An average of 55% of the P flow remained in the sewage sludge after urban food consumption, indicating a potential source of P for reuse. Actually, before the 1980s sewage sludge was widely used for land application in Beijing and Tianjin but most sewage sludge was not properly treated and this resulted in environmental pollution (Wang, 1997). Sewage sludge production in China increased rapidly together with a dramatic increase in municipal wastewater with the development of urbanization. However, the recycling of sewage sludge decreased substantially in recent years mainly because of the elevated economic cost of transporting sludge and removing toxic substances to meet application regulations (Wang et al., 2005). Most of the sewage sludge is landfilled within the city and this portion of P in sewage sludge will stay in the cities. Our material flow analysis of the two megacities reveals that the P content in the individual urban sewage sludge in 2008 were equivalent

625 Reclaimed water

3181

9

309

Urban consumption

2236

Sewage treatment plant

435

Aquatic

1792

11

Food production system

solid waste disposal

system

547

995

Rural consumption

2 446

Fig. 3. Phosphorus flows through food consumption in Tianjin in 2008 (t).

M. Qiao et al. / Chemosphere 84 (2011) 773–778

to 65% and 11% of the nutrients in chemical P fertilizers because the amounts of phosphorus fertilizers applied for agricultural production in Beijing and Tianjin were 10 222 t and 39 000 t, respectively. Therefore, application of sewage sludge on agricultural soils has great potential for improving soil fertility. In France the use of sludge on land accounts for about 60% of sludge production (Maisonnave et al., 2002). In Belgium about 57% of sewage sludge is land applied (Lyberatos et al., 2004). The environmental and economic benefits of land application of sewage sludge must be emphasized in China to improve nutrient recycling. On the other hand, P flows in uncollected sewage are of growing environmental concern. According to the statistical data, the total volumes of surface water in Beijing and Tianjin are 1.28 and 1.36 billion cubic meters (TMBS, 2009) in 2008, respectively. If we assume that all emitted P was discharged into surface waters, this would result in concentrations of 1.3 and 1.1 mg L 1 P in Beijing and Tianjin, respectively. Clearly, this poses a potential risk of water eutrophication. The development of urbanization is expected to generate very large amounts of wastewater in these megacities. Additional sewage treatment plants are required, especially in peri-urban areas, and more active techniques must be adopted to increase the disposal rates of nutrients in sewage sludge. Elevating sewage treatment rates and the percentage of sewage sludge applied to land can contribute to efficient recycling of P in megacities. Most importantly, however, the nutrients must be brought back into food production before they enter the sewage treatment system, that is, to overcome the so-called ‘end-of-the pipe’ treatment. Human excreta contain valuable nutrients and can be used as an effective fertilizer and soil conditioner, especially urine which contains 90% of the nitrogen, 50–65% of the phosphorus and 50–80% of the potassium (Heinonen-Tanski and WijkSijbesma, 2005). China has a long history of using human excreta as a fertilizer for crops, but nowadays the human waste generated in urban and rural areas is more and more difficult to accept by surrounding rural areas. On one hand, rapid urbanization requires higher costs for long distance transportation to agricultural land in peri-urban or rural areas. On the other hand, the nutrients in human excreta are greatly diluted with water in modern sanitation facilities of urban areas which makes recycling more difficult, not to mention contamination with potentially toxic elements or persistent organic pollutants (Chen et al., 2008). Therefore, capturing nutrients at source can drastically save water for flushing and is much more cost-effective. Ecological sanitation is based on this concept and the flow of nutrients is a closed loop. In several European countries there are some cases of urine and flush water being collected by separate urine pipes; faeces and flush water proceed to the sewage pipe (Lienert and Larsen, 2010). Urine-diverting toilets are also manufactured in Kunming, Yunnan province, China (Medilanski et al., 2006) and have proved to be a successful model for developing decentralized wastewater treatment alternatives and for alleviating the problems of water pollution. It is very important for developing countries to solve their sanitation problems, especially in the megacities such as Beijing and Tianjin. These cities are threatened by water scarcity, food insecurity and pollution as urbanization continues and sustainable development requires a strong coordination between urban and rural areas for nutrient recycling. Sustainable food production and consumption patterns present the most profound problems. The UN forecasts that today’s urban population of 3.2 billion will rise to nearly 5 billion by 2030, when three out of five people will live in cities. By 2015 there will be 26 cities with over 10 million people – 22 in developing countries (Brennan, 1999). Currently, at least 6000 t of food must be imported each day to feed a city of this size. Urbanization with poverty is a growing phenomenon; it is estimated that between one-quarter and one-third of all urban

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households in the world live in absolute poverty. The urban poor have to spend much of their income on food, in many cases more than 50% of their income. They will not be able to afford food from other countries or food grown far away in their own countries. There is a need to produce food closer to where people live. This represents a closed-loop approach to nutrients and water problems (Werner et al., 2000). Ecological sanitation is a decentralized operation and can be carried out at the household or community level as opposed to centrally operated systems. Based on a systematic material flow orientated recycling process; ecological sanitation can be constructed differently for urban and rural areas by a variety of low and high technology solutions (Larsen et al., 2001). For example, we can choose a urine-separating dry toilet for the peri-urban areas and a flushing urine-separating toilet (NoMix toilet) for the urban situation. The cost of ecological sanitation systems in megacities could be offset by the commercial value of the P they yield as well as the water resources saved. These new technologies certainly need to be further explored and tested and their large scale application in megacities of developing countries must be cautious. However, they can be tested in public toilets. In Beijing, there were about 5589 public toilets in 2008 and more than 3000 commercial buildings in Beijing have opened their toilets to the public. It would make a significant contribution to water saving and P recycling if all public toilets had ecological sanitation. In addition, it is also vitally important to establish rigorous water management and nutrient recycling concepts for decision-makers for the sustainable development of megacities. 5. Conclusion This study focuses on understanding the characteristics of P flows through food consumption in Beijing and Tianjin, two megacities in northern China. Material flow analysis was found to be a valuable tool for understanding the key stocks and flows of P. A large amount of P accumulated in urban sewage sludge after consumption. P in the uncollected sewage from both urban and rural residents as well as the effluents from sewage treatment plant contributes greatly to the eutrophication of surface waters. At present, measures must be implemented to increase sewage treatment rates and the percentage of sewage sludge applied to land to improve the efficiency of P cycling. However, in megacities in developing countries it is most important to overcome the socalled ‘end-of-the pipe’ treatment and bring the nutrients back into food production from source by solving sanitation problems first. Thus, it has become the most important mission for decisionmakers to develop and implement efficient strategies to facilitate P recycling in China. Acknowledgements This study was financed by the Chinese Academy of Sciences (KZCX1-YW-06-03) and the Chinese Ministry of Science and Technology (2007CB407301). References Bao, S.F., Zhao, L., Li, Z., Cong, T., Zheng, Z.X., Cheng, G.T., Zou, H.M., 2007. Dietary survey of residents in Beijing in 2004. J. Chin. Inst. Food Sci. Technol. 7, 9–17. Bian, Y.S., 2000. Wastes Disposal and Reuse for Ecological Agriculture. Chemical Industrial Press, Beijing, Beijing. BMBS (Beijing Municipal Bureau of Statistics)., 2009. Beijing Statistical Yearbook. Beijing Statistics Press, Beijing. Brennan, E.M., 1999. Population, urbanization, environment, and security: a summary of the issues. Environ. Change Secur. Project Rep. 5, 4–14. Chen, Z.L., Tang, Y.Z., 1999. Study on sustainable use of urban night soil in China. Urban Environ. Urban Ecol. 12, 42–49.

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Chen, M., Chen, J., Sun, F., 2008. Agricultural phosphorus flow and its environmental impacts in China. Sci. Total Environ. 405, 140–152. CMEP (Chinese Ministry of Environmental Protection),, 2002. Discharge Standard of Pollutants for Municipal Wastewater Treatment Plant (GB18918–2002). Chinese Environmental Science Publishing House, Beijing. Cohen, B., 2006. Urbanization in developing countries: current trends, future projections, and key challenges for sustainability. Technol. Soc. 28, 63– 80. Cordell, D., Drangert, J.O., White, S., 2009. The story of phosphorus: global food security and food for thought. Global Environ. Change 19, 292–305. Fan, Y.P., Hu, S.Y., Chen, D.J., Li, Y.R., Shen, J.Z., 2009. The evolution of phosphorus metabolism model in China. J. Clean. Prod. 17, 811–820. Feng, L.P., Guo, Z.Y., Xu, Z.C., Sun, J.W., Luo, M., Tan, Z.Y., 2009. The influence on emission of total nitrogen and total phosphorus in human excreta. China Sci. Technol. Inf. 1, 16–17. Gould, B.W., Villarreal, H.J., 2006. An assessment of the current structure of food demand in urban China. Agric. Econ. 34, 1–16. Heinonen-Tanski, H., Wijk-Sijbesma, C., 2005. Human excreta for plant production. Bioresour. Technol. 96, 403–411. Jiang, G.H., Li, J., Zhang, F.L., Zheng, W.L., Pan, Y., Yang, Y., Chang, G., Huo, F., 2005. Diet pattern and its analysis in surveyed population in Tianjin residence. Chin. J. Prev. Contr. Chron. Non-commun. Dis. 13, 202–204. Jönsson, H., Stintzing, A.R., Vinneras, B., Salomon, E., 2004. Guidelines on the Use of Urine and Faeces in Crop Production. EcoSanRes Publication Series. Report 2004-2 Stockholm Environment Institute, Stockholm. Kennedy, C., Cuddihy, J., Engel-Yan, J., 2007. The changing metabolism of cities. J. Ind. Ecol. 11, 43–59. Larsen, T.A., Peters, I., Alder, A., Eggen, R., Maurer, M., Muncke, J., 2001. Reengineering the toilet for sustainable wastewater management. Environ. Sci. Technol. 35, 192A–197A. Lienert, J., Larsen, T.A., 2010. High acceptance of urine source separation in seven European countries: a review. Environ. Sci. Technol. 44, 556–566. Liu, Y., 2004. Study on Phosphorus Societal Metabolism and Eutrophication Control Policy in China. Ph.D. Thesis. Liu, Y., Villalba, G., Ayres, R.U., Schroder, H., 2008. Global phosphorus flows and environmental impacts from a consumption perspective. J. Ind. Ecol. 12, 229– 247.

Luo, S.M., 2001. The Utilization of Human Excreta in Chinese Agriculture and the Challenge Ahead. Abstract Sets of the First International Conference on Ecological Sanitation, pp. 31–34. Lyberatos, G., Klimantos, P., Vassilakis, I., Kornaros, M., 2004. On the impact of land application of secondary sludge. Water, Air, Soil Pollut.: Focus 4, 349–357. Maisonnave, V., Montrejaud-Vignoles, M., Bonnin, C., Revel, J.C., 2002. Impact on crops, plants and soils of metal trace elements transfer and flux, after spreading of fertilizers and biosolids. Water Sci. Technol. 46, 217–224. Matsubae-Yokoyama, Kubo, H., Nakajima, K., Nagasaka, T., 2009. A material flow analysis of phosphorus in Japan: the iron and steel industry as a major phosphorus source. J. Ind. Ecol. 13, 687–705. Medilanski, E., Chuan, L., Mosler, H.J., Schertenleib, R., Larsen, T.A., 2006. Wastewater management in Kunming, China: a stakeholder perspective on measures at the source. Environ. Urban 18, 353–368. Ministry of Housing and Urban-Rural Development of China (MOHURD), 2009. China Urban Construction Statistical Yearbook, China Building Industry Press, Beijing. NBSC (National Bureau of Statistics of China)., 2009. China Statistical Yearbook. China Statistics Press, Beijing. Nie, Y.F., 2000. Handbook of Engineering and Techniques of Three-wastes Treatment. Chemical Industry Press, Beijing. Smil, V., 2000. Phosphorus in the environment: natural flows and human interferences. Ann. Rev. Energy Environ. 25, 53–88. TMBS (Tianjin Municipal Bureau of Statistics)., 2009. Tianjin Statistical Yearbook. Tianjin Statistics Press, Tianjin. Wang, M.J., 1997. Land application of sewage sludge in China. Sci. Total Environ. 197, 149–160. Wang, L.D., 2005. The Survey Report of the Nutrition and Health Status of the Chinese Residents in 2002. People’s Medical Publishing House, Beijing. Wang, C., Hu, X., Chen, M.L., Wu, Y.H., 2005. Total concentrations and fractions of Cd, Cr, Pb, Cu, Ni and Zn in sewage sludge from municipal and industrial wastewater treatment plants. J. Hazard Mater. 119, 245–249. Wei, Y.S., Fan, Y.B., Wang, M.J., Wang, J.S., 2000. Composting and compost application in China. Resour. Conserv. Recy. 30, 277–300. Werner, C., Schlick, J., Witte, G., Hildebrandt, A., 2000. Ecosan-closing the Loop in Wastewater Management and Sanitation. Proceedings of the International Symposium, Germany.