Nitrogen fertilizer warning for China

万方数据万方数据万方数据农田土壤固碳措施的温室气体泄漏和净减排潜力作者：逯非， 王效科， 韩冰， 欧阳志云， 郑华， LU Fei， WANG Xiao-Ke， HAN Bing，OUYANG Zhi-Yun， ZHENG Hua作者单位：中国科学院生态环境研究中心城市与区域生态国家重点实验室,北京,100085刊名：生态学报英文刊名：ACTA ECOLOGICA SINICA年，卷(期)：2009，29(9)引用次数：0次1.United Nations Kyoto Protocol to the United Nations Framework Convention on Climate Change 2009l R.Bruce J P The potential of world cropland soils to sequester C and mitigate the greenhouse effect 1999(2)3.Follett R F Soil management concepts and carbon sequestration in cropland soils 2001(1-2)l R Carbon sequestration 2008(1492)l R Soil Carbon sequestration impacts on global climate change and food security 2004(5677)l R Carbon management in agricultural soils 2007(2)l R World cropland soils as a source or sink for atmospheric carbon 20018.Post W M.Izaurralde R C.Jastrow J D Enhancement of carbon sequestration in US soils 2004(10)9.Hartemink A E.McBratney A A soil science renaissance 2008(2)10.Pan G.Li L.Wu L Storage and sequestration potential of topsoil organic carbon in 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J.Godinho V P Carbon sequestration in agricultural soils in the Cerrado region of the Brazilian Amazon 200854.Baker J M.Ochsner T E.Venterea R T Tillage and soil carbon sequestration-What do we really know? 2007(1)55.Wu L.Wood Y.Jiang P Carbon Sequestration and Dynamics of Two Irrigated Agricultural Soils in California 2008(3)56.Coneth A J.Blair G J.Rochester I J Soil organic carbon fraction in a Vertisol under irrigated cotton production as affected by burning and incorporating cotton stubble 1998(4)57.Dormaar J F.Carefoot J M Effect of straw management and nitrogen fertilizer on selected soil properties as potential soil quality indicators of an irrigated dark brown Chernozemic soil 1998(3)58.Wu H.Guo Z.Peng C Land use induced changes of organic carbon storage in soils of China 2005(3)59.Mosier A R Nitrous oxide emissions from agricultural soils 1994(3)60.Smith K A.McTaggart I P.Dobbie K E Emissions of N2O from Scottish agricultural soils,as afunction of fertilizer N 1998(2-3)61.Burger M.Jackson L E.Lundquist E J Microbial responses and nitrous oxide emissions during wetting and drying of organically and conventionally managed soil under tomatoes 2005(2)62.Scheer C.Wassmann R.Kienzler K Nitrous oxide emissions from fertilized,irrigated cotton (Gossypium hirsutum L.) in the Aral Sea Basin,Uzbekistan:Influence of nitrogen applications and irrigation practices 2008(2)63.Xu C.Shaffer M J.Al-kaisi M Simulating the impact of management practices on nitrous oxide emissions 1998(3)systems of the irrigated areas in the Aral Sea Basin 2008(10)65.Liu X J.Mosier A R.Halvorson A D Dinitrogen and N2O emissions in arable soils:Effect of tillage,N source and soil moisture 2007(9)66.Robertson G P.Grace R R Greenhouse gas fluxes in tropical and temperate agriculture:The need fora full-cost accounting of global warming potentials 2004(1-2)67.Wang M X Methane Emission from Rice Fields in China 200168.Huang Y.Sass R L.Fisher J R F M Model estimates of methane emission from irrigated rice cultivation of China 1998(8)69.Yan X Y.Yagi K.Akiyama H Statistical analysis of the major variables controlling methane emission from rice fields 2005(7)70.Zhang W.Huang Y.Zheng X H Modeling Methane Emission from Rice Paddies:Model Sensitivity Analysis 2006(5)71.Powlson D S.Riche A B.Coleman K Carbon sequestration in European soils through straw incorporation:Limitations and alternatives 2008(4)72.Cao G L.Zhang X Y.Wang Y Q Estimation of emissions from field burning of crop straw in China 2008(5)73.Powlson D S.Whitmore A P Soil carbon sequstration-What is genuine climate change mitigation and what is not? 200874.Smith P.Powlson D S.Smith J U Meeting Europe′s climate change commitments:quantitative estimates of the potential for carbon mitigation by agriculture 2000(5)75.Dendoncker N.Van Wesemael B.Rounsevell M D A Belgium′s CO2 mitigation potential under improved cropland management 2004(1)76.Huang Y.Zhang W.Zheng X Modeling methane emission from rice paddies with various agricultural practices 200477.Zou J W.Liu S W.Qin Y M Sewage irrigation increased methane and nitrous oxide emissions from rice paddies in southeast China 2009(4)78.McCarl B A.Schneider U A Greenhouse gas mitigation in US agriculture and forestry 2001(5551)79.Smith P.Martino D.Cai Z Policy and technological constraints to implementation of greenhouse gas mitigation options in agriculture 2007(1)80.West T O.Six J Considering the influence of sequestration duration and carbon saturation on estimates of soil carbon capacity 2007(1-2)81.Marland G.Garten.G R Jr.Post W M Studies on enhancing carbon sequestration in soils 2004(9-10)82.West T O.Marland G Net carbon flux from agriculture:carbon emissions,carbon sequestration,crop yield,and land-use change 2003(1)83.韩冰.王效科.逯非中国农田土壤生态系统固碳现状和潜力 2008(2)84.陈泮勤.王效科.王礼茂中国陆地生态系统碳收支与增汇对策 200885.逯非.王效科.韩冰中国农田施用化学氮肥的固碳潜力及其有效性评价 2008(10)87.王效科.李长生中国农田生态系统的N2O排放量研究 2000(4)88.王明星中国稻田甲烷排放 200189.张稳.黄耀.郑循华稻田甲烷排放模型研究--模型灵敏度分析 2006(5)1.期刊论文PAN Genxing.赵其国.蔡祖聪.PAN Genxing.ZHAO Qiguo.CAI Zucong《京都议定书》生效后我国耕地土壤碳循环研究若干问题-中国基础科学2005,7(2)地球系统碳循环与全球变化研究的一个重要任务是阐明陆地生态系统的碳汇演变及其对日益升高的大气CO2的收集与固定能力以及未来趋势.土壤有机碳是地球陆地生态系统最重要和活跃的碳库,同时又是土壤肥力和基础地力的最重要的物质基础,它影响着耕地生产力及其稳定性.随着<京都议定书>的生效,农业土壤碳循环及固碳潜力的研究将越来越成为国际全球变化研究中的主流趋势,国际科学界十分关注人为利用管理下土壤固碳潜力的变化.配合土壤固碳机理及其影响因素的研究,分析与预测未来通过改变管理政策与农业技术途径而可能达到的固碳能力成为今后研究的发展方向.我国农业面临着稳定耕地生产能力和补偿工业温室气体减排的压力和挑战,但我国耕地地力不稳、有机碳水平较低的现状又为实行固碳农业带来了机遇.我国所处的自然环境和社会经济背景条件的特殊性决定了我国耕地农业利用与土壤碳循环的特殊性,而这种特殊性对耕地土壤固碳潜力及其过程的影响是国际陆地生态系统碳循环研究中没有解决而又只能由我国自己来解决的重大科学理论问题.当前,我国急迫需要启动对耕地土壤碳循环与固碳潜力及其调控途径的重大基础研究,摸清国家尺度耕地土壤的固碳能力,认识耕地固碳与生产力保持的耦合机制,明确耕地土壤固碳与稳产的技术途径体系,为我国建立农业固碳与生产力稳定的长效机制和温室气体减排的环境外交提供可靠依据.2.学位论文颉鹏河西绿洲农田生态系统土壤碳汇时空演变研究2009随着全球温室效应的加剧，为探索降低大气温室气体浓度的对策，陆地生态系统碳循环及碳收支研究成为当前全球变化研究的热点问题。

生物炭对土壤氮素转化的影响摘要：由于生物炭具有很大的比表面积，具有更高的化学稳定性和热稳定性，可以将碳封存等特性被作为土壤改良剂应用于农业。

并且在氮素转化方面取得了一些结果：（1）生物炭可以提高硝化速率，一方面是其自身对NH+的氧化，一方面由于其促进了硝化微生物的活性；（2）生物炭大的比表面积对N/和NH3具有吸附作用；（3）生物炭可以减少温室气体20的排放；（4）生物炭可以减少NO-N的淋洗。

关键字：生物炭；硝化速率；NH4+；NH3；NO3--N生物炭，又称生物质炭（biochar）是指作物秸秆、畜禽粪便等生物质废弃物在完全或部分缺氧条件下通过低温热解（V700C）而产生的一类高度芳香化难熔性富“ C'固态物质。

由于生物炭具有很大的比表面积，具有更高的化学稳定性和热稳定性，可以将碳封存等特性被作为土壤改良剂应用于农业。

1 生物炭对硝化作用的影响人们对生物炭为什么会促进硝化作用进行深入研究。

研究发现，硝化作用是受某种因素抑制的，而活性炭似乎可以减缓这种抑制。

同时发现，在所有活性炭改良土壤中，酚类化合物的浓度都下降了[1]。

继而推测：酚类物质可能会抑制硝化作用或者是会固定硝化作用所产生的NC3-，而生物炭同活性炭相似，同样具有较大的比表面积，是一种多孔，疏水结构，这使它能够吸附一些疏水的化合物。

已经有非常多的文献报道了生物炭加入到土壤当中后，可以减少可溶的自由态的酚类化合物。

随后的研究也证实了天然火或者农业焚烧所产生的生物炭对酚类和芳香族疏水化合物的确有吸收作用。

而这些酚类化合物会抑制硝化细菌的增长，生物炭有可能是吸附了酚类化合物，从而间接促进了硝化作用。

生物炭能够吸附酚类物质只是它能促进硝化作用的原因之一，原因之二是生物炭本身可以催化氧化NH4+[2]。

实验表明，将无菌生物炭加到无菌样品中，硝化作用有所增加，表明生物炭的氧化表面能促进一定数量的NH+氧化。

木头灰分一般包含较高浓度的金属氧化物，有CaO MgO F^Q, TQ2, CrQ 将生物炭暴露在可溶的灰分里，可以给生物炭活性表面增加这些很有可能引起催化反应的氧化物。

如何减少氮排放英语作文Title: Mitigating Nitrogen Emissions: Strategies and Solutions。

In the modern era, nitrogen emissions have become a pressing environmental concern, with significant implications for ecosystems, human health, and the climate. Addressing this challenge requires a multifaceted approach that encompasses policy initiatives, technological innovations, and individual behavioral changes. In this essay, we will explore various strategies to reduce nitrogen emissions and their potential impact on mitigating environmental degradation.First and foremost, agricultural practices stand out as a primary contributor to nitrogen emissions, particularly through the excessive use of synthetic fertilizers. To mitigate this, promoting precision agriculture techniques can significantly reduce nitrogen usage while maintaining or even increasing crop yields. Precision agricultureinvolves utilizing advanced technologies such as GPS-guided machinery and remote sensing to precisely apply fertilizers, thereby minimizing excess nitrogen runoff into waterwaysand atmospheric release.Additionally, optimizing nitrogen fertilizerapplication timing and rates based on crop needs and soil conditions can enhance nutrient uptake efficiency and minimize losses. This approach, known as "fertigation," involves applying fertilizers in tandem with irrigation water, ensuring that nutrients are delivered directly tothe root zone where they are most needed. By adopting fertigation practices, farmers can achieve higher cropyields with lower nitrogen inputs, thereby reducing emissions while improving economic outcomes.Furthermore, promoting the use of nitrogen-fixing crops, such as legumes, in crop rotation systems can naturally replenish soil nitrogen levels and reduce the need for synthetic fertilizers. Leguminous plants have symbiotic relationships with nitrogen-fixing bacteria in their root nodules, allowing them to convert atmospheric nitrogen intoa form that is readily available for plant uptake. By integrating legumes into crop rotations, farmers can enhance soil fertility, reduce nitrogen fertilizer requirements, and mitigate emissions associated with fertilizer production and application.In addition to agricultural measures, addressing nitrogen emissions from transportation and industrial sources is essential for comprehensive mitigation efforts. The transportation sector, particularly vehicles powered by internal combustion engines, contributes to nitrogen oxides (NOx) emissions, which can lead to air pollution and acid rain formation. Transitioning to electric vehicles (EVs) and implementing stricter emissions standards for combustion engines can significantly reduce NOx emissions, thereby improving air quality and reducing nitrogen deposition in sensitive ecosystems.Moreover, in industrial processes such as power generation and manufacturing, implementing cleaner production technologies and upgrading pollution control equipment can minimize nitrogen emissions. For instance,adopting selective catalytic reduction (SCR) systems in power plants and industrial facilities can effectively reduce NOx emissions by converting them into harmless nitrogen and water vapor through catalytic reactions. Additionally, implementing nitrogen capture and recycling technologies can mitigate emissions from industrial sources by capturing and reusing nitrogen compounds in various manufacturing processes, thereby minimizing waste and environmental impact.Furthermore, raising public awareness and fostering sustainable consumption patterns are crucial aspects of reducing nitrogen emissions. Educating consumers about the environmental impacts of nitrogen pollution and promoting eco-friendly lifestyle choices, such as reducing meat consumption (as livestock farming is a significant source of nitrogen emissions) and practicing sustainable gardening practices, can empower individuals to make informed decisions that contribute to emission reduction efforts.In conclusion, mitigating nitrogen emissions requires a concerted effort involving government policies,technological innovations, and individual actions. By implementing precision agricultural practices, promoting clean transportation and industrial technologies, and raising public awareness, society can effectively reduce nitrogen emissions and mitigate their adverse environmental effects. Embracing a holistic approach to nitrogen management is essential for fostering sustainable development and safeguarding the health of our planet for future generations.。

IFA化肥术语（中英对照）
一、肥料施用及相关词汇
中化化肥有限公司全心全意为中国农民服务全国免费服务电话：800-810-9991 1
中化化肥有限公司全心全意为中国农民服务全国免费服务电话：800-810-9991 2
二、土壤科学及相关词汇
中化化肥有限公司全心全意为中国农民服务全国免费服务电话：800-810-9991 3
中化化肥有限公司全心全意为中国农民服务全国免费服务电话：800-810-9991 4
三、肥料制造与分析及相关词汇
中化化肥有限公司全心全意为中国农民服务全国免费服务电话：800-810-9991 5
中化化肥有限公司全心全意为中国农民服务全国免费服务电话：800-810-9991
中化化肥有限公司全心全意为中国农民服务全国免费服务电话：800-810-9991 7
中化化肥有限公司全心全意为中国农民服务全国免费服务电话：800-810-9991 8
中化化肥有限公司全心全意为中国农民服务全国免费服务电话：800-810-9991 9
中化化肥有限公司全心全意为中国农民服务全国免费服务电话：800-810-9991 10
中化化肥有限公司全心全意为中国农民服务全国免费服务电话：800-810-9991 11
四、施用机械和方法及其他词汇
中化化肥有限公司全心全意为中国农民服务全国免费服务电话：800-810-9991 12。

中棉小康花匠的使用用法English Answer:How to Use ZhongMian Xiaokang Fertilizer:ZhongMian Xiaokang is a widely used fertilizer in China for various crops, including vegetables, flowers, and fruits. It is a type of compound fertilizer containing NPK (nitrogen, phosphorus, and potassium) as well as other essential nutrients. Here's how to effectively use it:1. Soil Preparation:Before applying ZhongMian Xiaokang, ensure the soil is well-drained and has good aeration.Test the soil to determine its pH level and nutrient composition.2. Fertilizer Application:Dosage: The recommended dosage of ZhongMian Xiaokang varies depending on the crop, soil conditions, and growth stage. Follow the instructions provided on the product label or consult an agricultural expert.Timing: For vegetables and flowers, apply thefertilizer during the transplanting and growth stages. For fruits, apply it during the seedling, flowering, and fruiting stages.Method: Spread the fertilizer evenly over the soil surface and mix it in lightly to ensure proper absorption.3. Water Management:Water the plants immediately after applying the fertilizer.Avoid overwatering, as it can lead to nutrient leaching.4. Monitoring:Monitor the plants regularly to assess their growth and health.If any signs of nutrient deficiencies or imbalances appear, adjust the fertilizer schedule accordingly.5. Safety Precautions:Wear protective gear (gloves, mask) when handling the fertilizer.Store the fertilizer in a cool, dry place away from children and pets.Additional Tips:Use ZhongMian Xiaokang in combination with organic fertilizers for optimal plant growth.Supplement with specific nutrient solutions if needed,based on soil test results.Avoid excessive or irregular fertilizer applications, as it can harm the plants and damage the soil.中文回答：中棉小康花匠使用方法。

赵伟东，郭宝玲，郑祥洲，等.烟-稻轮作不同施肥土壤N 2O 排放对水分的响应[J].农业环境科学学报,2023,42（7）：1655-1665.ZHAO W D,GUO B L,ZHENG X Z,et al.Effects of moisture content on N 2O emissions in different fertilized soils under tobacco-rice rotation[J].Journal ofAgro-Environment Science ,2023,42（7）：1655-1665.烟-稻轮作不同施肥土壤N 2O 排放对水分的响应赵伟东1，2，郭宝玲2，郑祥洲2*，汤水荣1*，孟磊1，张玉树2（1.海南大学热带作物学院，海口570228；2.福建省农业科学院土壤肥料研究所/福建省植物营养与肥料重点实验室，福州350013）Effects of moisture content on N 2O emissions in different fertilized soils under tobacco-rice rotationZHAO Weidong 1,2,GUO Baoling 2,ZHENG Xiangzhou 2*,TANG Shuirong 1*,MENG Lei 1,ZHANG Yushu 2（1.College of Tropical Crops,Hainan University,Haikou 570228,China;2.Institute of Soil and Fertilizer,Fujian Academy of Agricultural Sciences/Fujian Provincial Key Laboratory of Plant Nutrition and Fertilizer,Fuzhou 350013,China ）Abstract ：Nitrous oxide （N 2O ）emissions from soil with different fertilization treatments under flood-upland rotation are important for N 2Oemissions regulation.In this study,soil samples from a long-term fertilization positioning experiment （tobacco-rice rotation ）in a收稿日期：2022-10-20录用日期：2023-02-21作者简介：赵伟东（1997—），男，陕西陇县人，硕士研究生，从事土壤碳氮循环与环境效应研究。

LETTERdoi:10.1038/nature11917Enhanced nitrogen deposition over ChinaXuejun Liu 1*,Ying Zhang 1*,Wenxuan Han 1,Aohan Tang 1,Jianlin Shen 1,Zhenling Cui 1,Peter Vitousek 2,Jan Willem Erisman 3,4,Keith Goulding 5,Peter Christie 1,6,Andreas Fangmeier 7&Fusuo Zhang 1China is experiencing intense air pollution caused in large part by anthropogenic emissions of reactive nitrogen 1,2.These emissions result in the deposition of atmospheric nitrogen (N)in terrestrial and aquatic ecosystems,with implications for human and ecosys-tem health,greenhouse gas balances and biological diversity 1,3–5.However,information on the magnitude and environmental impact of N deposition in China is limited.Here we use nationwide data sets on bulk N deposition,plant foliar N and crop N uptake (from long-term unfertilized soils)to evaluate N deposition dynamics and their effect on ecosystems across China between 1980and 2010.We find that the average annual bulk deposition of N increased by approximately 8kilograms of nitrogen per hec-tare (P ,0.001)between the 1980s (13.2kilograms of nitrogen per hectare)and the 2000s (21.1kilograms of nitrogen per hectare).Nitrogen deposition rates in the industrialized and agriculturally intensified regions of China are as high as the peak levels of deposi-tion in northwestern Europe in the 1980s 6,before the introduction of mitigation measures 7,8.Nitrogen from ammonium (NH 41)is the dominant form of N in bulk deposition,but the rate of increase is largest for deposition of N from nitrate (NO 32),in agreement with decreased ratios of NH 3to NO x emissions since 1980.We also find that the impact of N deposition on Chinese ecosystems includes significantly increased plant foliar N concentrations in natural and semi-natural (that is,non-agricultural)ecosystems and increased crop N uptake from long-term-unfertilized crop-lands.China and other economies are facing a continuing chal-lenge to reduce emissions of reactive nitrogen,N deposition and their negative effects on human health and the environment.Atmospheric N deposition results from emissions of reactive nitro-gen (N r )species and their atmospheric transport;it expands the foot-print of local alterations to the N cycle 3.Although both natural and anthropogenic sources contribute to atmospheric N deposition,anthropogenic N r emissions (largely from the agricultural,industrial and transport sectors)have increased substantially since the industrial revolution began 9;they now make the dominant contribution to N deposition in many regions 3,10.Increased concentrations of N r in the atmosphere and,through deposition,in terrestrial or aquatic ecosys-tems,or both,degrade human health 1(notably through driving the formation of particulate matter and tropospheric ozone),alter soil and water chemistry 3,influence greenhouse gas balance 4and reduce biological diversity 5.The human and environmental costs associated with anthropogenic N r are well recognized,and active measures in Western Europe and North America have stabilized or reduced N r deposition in those regions 6,11,12.Even so,very large costs of excess N r have been reported in the European Union 8(J 70–320billion per year)and the United States 13.In contrast,over the past 30years China’s emissions have increased to the point that it has become by far the largest creator and emitter of N r globally 2.However,the rates and trends of N deposi-tion in China since the 1980s are not clear.We would also like to knowthe consequences of N deposition,for the people and ecosystems of China,its region and the world.Following rapid economic growth since the early 1980s,China’s gross domestic product was estimated at US$5.9trillion in 2010,mak-ing China the world’s second largest economy after the United States (/news/economy/world_economies_gdp).In around the year 2000,China surpassed the United States and the European Union (combined)in its production and use of N fertilizers.Moreover,less than half of the fertilizer N applied in China is taken up by crops 14;the rest is largely lost to the environment in gaseous (NH 3,NO,N 2O and N 2)or dissolved (NH 41and NO 32)forms 15,16.These fluxes—along with N r emitted during fossil fuel combustion—have resulted in some of the most pronounced air pollution on Earth 1.Increased N r emissions must have influenced atmospheric N depo-sition in and near China,but information on the magnitude,scope and consequences of any change has been lacking.Here we summarize available data nationwide on the bulk deposition of N r in terrestrial ecosystems.Also,we show that the N cycle has been altered in Chinese ecosystems,both within and outside croplands.Nitrogen deposition includes wet and dry deposition of both inor-ganic and organic N forms 2,17,but in most cases only the bulk depo-sition of inorganic N (NH 4-N and NO 3-N)has been measured systematically 6,18,19.Bulk N deposition denotes N input from precipi-tation as measured by an open sampler (Supplementary Methods);it is a relatively simple measure that includes wet deposition and a fraction of the dry deposition,and it is suitable for regional comparisons.We constructed a national data set incorporating all the available bulk N deposition results from monitoring sites throughout China between 1980and 2010(Supplementary Fig.1).This data set was used to test the magnitude and trend of atmospheric N deposition in relation to anthropogenic emissions of reduced and oxidized forms of N.In spite of site-to-site variability in the data,bulk N deposition increased significantly with time (P ,0.001),with an average annual increase of 0.41kilograms of nitrogen per hectare (kgN ha 21)between 1980and 2010(Fig.1a and Supplementary Table 1).The increase in bulk N deposition was driven mainly by increased volume-weighted N concentrations in rain water (0.063mgN l 21yr 21on average;Fig.1b)because annual precipitation in the study area has not changed significantly in the past 30years (Supplementary Fig.2and Sup-plementary Table 1).NH 4-N was the dominant form in bulk deposi-tion,but the ratio of NH 4-N to NO 3-N in bulk precipitation decreased significantly with time (Fig.1c,Supplementary Fig.3and Supplemen-tary Table 1).Overall,annual bulk N deposition averaged 13.2and 21.1kgN ha 21in the 1980s and 2000s,respectively,showing an increase of approximately 8kgN ha 21,or 60%(P ,0.001).The increase in overall bulk N deposition and the change in the ratio of NH 4-N to NO 3-N in precipitation and deposition (Fig.1)are similar to the increasing trends of anthropogenic gaseous N r (NH 3and NO x )emissions and changes in their ratio since 1980(Fig.2a and Supplementary Fig.4a).The ratio of NH 4-N to NO 3-N in measured*These authors contributed equally to this work.1College of Resources &Environmental Sciences,China Agricultural University,Beijing 100193,China.2Department of Biology,Stanford University,Stanford,California 94305,USA.3VU University Amsterdam,1081HV Amsterdam,The Netherlands.4Louis Bolk Institute,Hoofdstraat 24,3972LA Driebergen,The Netherlands.5The Sustainable Soils and Grassland Systems Department,Rothamsted Research,Harpenden AL52JQ,UK.6Agri-Environment Branch,Agri-Food and Biosciences Institute,Belfast BT95PX,UK.7Institute of Landscape and Plant Ecology,University of Hohenheim,70593Stuttgart,Germany.28F E B R U A R Y 2013|V O L 494|N A T U R E |459bulk deposition decreased from about 5to 2,and the ratio of NH 3-N to NO x -N in calculated emissions decreased from about 4to 2.5;these changes are highly correlated (P ,0.01).Emissions of NH 3doubled (Fig.2a),reflecting increased agricultural production in that both the use of N fertilizer and the number of domestic animals (expressed as standard livestock units)have also doubled since the 1980s (Fig.2b and Supplementary Fig.4b).Fossil fuel power plants,industrial production and motor vehicles are the major sources of NO x in China and Asia 20.Coal consumption and the number of motor vehicles increased 3.2-and 20.8-fold,respectively,between the 1980s and the 2000s (Fig.2c and Supplementary Fig.4c),driving a more rapid percentage increase in NO x emission than in NH 3emission (Fig.2a),although the net increase in emission was still larger for NH 3than for NO x (about 6TgN versus 4TgN between the 1980s and the 2000s).The ratio of NH 4-N to NO 3-N in bulk precipitation (Fig.1c)changed in the same direction and by approximately the same magnitude as the ratio of NH 3-N to NO x -N emission over the same period (Fig.2a),despite uncertainties in ammonia emission inventories 2,21.We analysed the dynamics of bulk N deposition regionally by divid-ing deposition data into six areas:northern,southeast,southwest,north-east and northwest China and the Tibetan plateau.Human influenceson the N cycle differ substantially among these regions.In general,bulk N deposition showed increasing trends and ratios of NH 4-N to NO 3-N showed decreasing trends for all six regions between the 1980s and the 2000s (Supplementary Table 1);highly significant (P ,0.001)increases in bulk N deposition were found in northern,southeast and southwest China,significant (P ,0.05)increases were found in the Tibetan plat-eau and northeast China,and no significant (P 50.199)increase was found in northwest China (Supplementary Figs 5and 6).By comparison with the national average,we found both higher overall rates of depos-ition and higher annual rates of increase in deposition in the industria-lized and agriculturally intensified northern,southeast and southwest China.Annual bulk deposition rates were 22.6,24.2and 22.2kgN ha 21in northern,southeast and southwest China in the 2000s,respectively,with average rates of increase of 0.42,0.56and 0.53kgN ha 21yr 21.A more detailed study 22of all major deposition pathways shows that total annual N wet and dry deposition on the northern China plain (the central area of northern China)was about 80kgN ha 21.These levels are much higher than those observed in any region in the UnitedB u l k N d e p o s i t i o n (k g N h a –1)B u l k N c o n c e n t r a t i o n (m g N l –1)1980198519901995200020052010N H 4-N /N O 3-N i n p r e c i p i t a t i o nab cYearFigure 1|Trends in N deposition and its components in China between 1980and 2010.a ,Bulk N deposition;b ,bulk N concentration;c ,ratios of NH 4-N to NO 3-N in bulk precipitation.In spite of large site-to-site variability,both bulk N deposition and N concentration have increased significantly since 1980,and the ratio of NH 4-N to NO 3-N in bulk precipitation has decreasedsignificantly according to linear mixed models (all P ,0.001;Supplementary Table 1).Data sources are included in Supplementary Information.N f e r t i l i z e r u s e (T g N y r –1)Livestock unit (106 heads)N H 3 o r N O x e m i s s i o n (T g N y r –1)NH 3-N/NO x -NYearN o . o f v e h i c l e s (106)20406080100Coal consumption (109 t)c abFigure 2|Trends in NH 3and NO x emissions and their main contributors between 1980and 2010.a ,NH 3and NO x emissions and ratios of NH 3-N to NO x -N emission;b ,number of domestic animals (expressed as livestock units)and N fertilizer consumption;c ,number of motor vehicles and coal consumption.Data sources are cited in Supplementary Information.LETTER460|N A T U R E |V O L 494|28F E B R U A R Y 2013States 12,and are comparable to the maximum values observed in the United Kingdom 6and the Netherlands 7when N deposition was at its peak in the 1980s 8.Extensive long-term environmental inventories and experiments in China allow us to evaluate some of the consequences of this substantial and continuing increase in N deposition.We have summarized results of an ongoing survey of foliar N concentrations from non-agricultural ecosystems throughout China and from detailed studies of crop N uptake from croplands in long-term trials without N fertilizer (des-cribed as zero-N plots hereafter),which are used as reference plots in fertilization experiments.The foliar N data set provides information on how changes in N deposition have influenced plant tissue chemistry in unfertilized,non-agricultural ecosystems.Foliar N increased signifi-cantly (all P ,0.001)between the 1980s and the 2000s for woody,herbaceous and all plant species (Fig.3a,Supplementary Fig.7a and Supplementary Table 1).Foliar N increase for all species averaged 32.8%(24.069.2mg g 21(2000s)versus 18.167.2mg g 21(1980s)),with a higher increase in herbaceous plants than in woody plants (Fig.3a).In contrast,foliar phosphorus (P)did not change signifi-cantly (P 50.085)over the same period (Supplementary Fig.7b and Supplementary Table 1).Foliar N is largely determined by plant spe-cies and plant N nutritional status;foliar N of specific plant species should be stable in natural and semi-natural ecosystems unless some process changes the availability of N relative to other plant resources 23.Plant species in this study were sampled widely (Supplementary Fig.1)and analysed by standard procedures (Supplementary Information)—and the evaluation of foliar P should correct for any bias towards sampling high-nutrient plant species late in the record (suggesting no apparent changes in the soil environment)—so the increase in foliar N in unfertilized ecosystems most probably represents a widespread increase in plant N nutritional status caused by the cumulative effects of enhanced N deposition.In agricultural ecosystems,crop N uptake from zero-N plots in long-term experiments is controlled primarily by N deposition,because soil N pools are relatively stable after 5to 10years without N fertiliza-tion 22,24.We summarized the available data on N uptake from zero-N plots in long-term experiments between 1980and 2010(Supplemen-tary Information);N uptake by rice,wheat and maize in zero-N plots was significantly higher in the 2000s than in the 1980s (Fig.3b;all P ,0.05).The increase in N uptake averaged 11.3kgN ha 21across the three major cereals (Fig.3b and Supplementary Fig.8).Overall,the temporal patterns in bulk N deposition,foliar N and N uptake from zero-N plots are consistent with rapidly increased anthro-pogenic NH 3and NO x emissions over the past three decades.The lower ratio of reduced N to oxidized N in measured deposition agrees well with the decrease in the ratio of calculated emissions of NH 3to NO x ,reflecting a more rapid proportional increase in N r emissions from industrial and traffic sources than from agricultural sources.All these changes can be linked to a common driving factor,strong economic growth,which has led to continuous increases in agricul-tural and non-agricultural N r emissions and,consequently,increased N deposition.Although we did not measure the impact of atmospheric N r emis-sions and deposition from China on the global environment,recent studies indicate that N r deposited by China may be moving to sur-rounding marine ecosystems 25and perhaps to tropical and subtropical forests 26.Another study 27reported a strong abnormal spring increase in free tropospheric ozone concentrations in western North America between 1995and 2008,and suggested that NO x -induced ozone trans-port from Asia (mainly from China and India)to North America could be a major source.Clearly,N deposition has increased significantly in China and has affected both non-agricultural and agricultural ecosystems.So far,China’s economic growth model has relied mainly on the consump-tion of raw materials,and it has caused large anthropogenic N r emis-sions in addition to other environmental perturbations 28.For example,the emitted NH 3and NO x gases form secondary aerosols such as NH 4NO 3in PM 2.5(particulate matter with aerodynamic diameter #2.5m m)under favourable conditions,decrease visibility and damage human health.The Chinese government has recognized the impor-tance of protecting the environment while developing the economy;recently,it approved the first national environmental standard for limiting the amount of PM 2.5(ref.29).Our results demonstrate that deposition of reduced forms of N r continues to be of greatest importance in China (which is responsible for approximately 2/3of total deposition)but emission and deposition of oxidized N r are increasing more rapidly.Current environmental policy needs to focus more strongly on reducing present NH 3emis-sions from agricultural sources,whereas control of NO x emissions from industrial and traffic sources will become more important in the near future.It is time for China and other economies to take action to improve N-use efficiency and food production in agriculture and reduce N r emissions from both agricultural and non-agricultural sectors.These actions are crucial to reducing N deposition and its negative impact locally and globally.METHODS SUMMARYData sets on bulk N deposition,plant foliar N concentration and crop N uptake from non-N-fertilized soils were summarized from published data and measure-ments across ing 315references and our own deposition monitoringF o l i a r N (m g g –1)aFigure 3|Comparisons of foliar N concentrations and crop N uptake between the 1980s and 2000s.a ,Foliar N in woody,herbaceous and all plant species in non-agricultural ecosystems;b ,N uptake by rice,wheat and maize from zero-N plots in long-term experiments.Both foliar N (all P ,0.001)and N uptake (all P ,0.05)are significantly higher in the 2000s than in the 1980s.The black and red lines,lower and upper edges,bars and dots in or outside the boxes represent median and mean values,25th and 75th,5th and 95th,and ,5th and .95th percentiles of all data,respectively.LETTER 28F E B R U A R Y 2013|V O L 494|N A T U R E |461network(CAUDN),we constructed a nationwide data set of the amount of annual precipitation,volume-weighed N concentrations in precipitation and bulk N deposition,as well as the ratio of NH4-N to NO3-N deposition.A total of866 data points of annual volume-weighted N concentrations in precipitation and671 data points of annual bulk N deposition rates at270monitoring sites were sum-marized for the period1980–2010.To clarify regional variations,bulk N deposi-tion data from six separate regions were also summarized.Additionally,a total of 981observations of plant foliar N concentration and859observations of foliar P were collected from666natural and semi-natural terrestrial plant species or varieties at245sites distributed across the whole of China(based mainly on ref.30;Supplementary Fig.1),and a total of278data points of crop N uptake by rice,wheat and maize were summarized from non-N-fertilized soils in long-term experiments.Emissions of national anthropogenic NH3and NO x were sum-marized from published data2and updated to2010(Supplementary information). Data on N deposition,foliar N and crop N uptake,and other related parameters, were fitted(with year)using linear mixed models or nonlinear regression models for the interval1980–2010(SPSS13.0,SPSS Inc.).Differences in these data between the1980s(1980–1989)and the2000s(2000–2010)were compared statistically using an unpaired two-tail Student’s t-test.A significant difference is assumed when the P value is,0.05or as otherwise stated.Further details on the data sets and statistical methods are given in Supplementary Methods.Full Methods and any associated references are available in the online version of the paper.Received25June2012;accepted15January2013.Published online20February2013.1.Richter,D.D.,Burrows,J.P.,Nu¨ß,H.,Granier,C.&Niemeier,U.Increase intropospheric nitrogen dioxide over China observed from space.Nature437,129–132(2005).2.Liu,X.J.et al.Nitrogen deposition and its ecological impacts in China:an overview.Environ.Pollut.159,2251–2264(2011).3.Vitousek,P.M.et al.Human alteration of the global nitrogen cycle:sources andconsequences.Ecol.Appl.7,737–750(1997).4.Matson,P.,Lohse,K.A.&Hall,S.J.The globalization of nitrogen deposition:consequences for terrestrial ecosystems.Ambio31,113–119(2002).5.Clark,C.M.&Tilman,D.Loss of plant species after chronic low-level nitrogendeposition to prairie grasslands.Nature451,712–715(2008).6.Goulding,K.W.T.et al.Nitrogen deposition and its contribution to nitrogen cyclingand associated soil processes.New Phytol.139,49–58(1998).7.Erisman,J.W.et al.The Dutch N-cascade in the European perspective.Sci.China C48,827–842(2005).8.Sutton,M.A.et al.The European Nitrogen Assessment:Sources,Effects and PolicyPerspectives(Cambridge Univ.Press,2011).9.Galloway,J.N.et al.Transformation of the nitrogen cycle:recent trends,questions,and potential solutions.Science320,889–892(2008).10.Schlesinger,W.H.On the fate of anthropogenic nitrogen.Proc.Natl A106,203–208(2009).11.Bleeker,A.et al.in Atmospheric Ammonia:Detecting Emission Changes andEnvironmental Impacts(eds.Sutton,M.A.,Reis,S.&Baker,S.M.H.)123–180(Springer,2009).12.Holland,E.A.,Braswell,B.H.,Sulzman,J.&Lamarque,J.F.Nitrogen depositiononto the United States and Western Europe:synthesis of observations and models.Ecol.Appl.15,38–57(2005).pton,J.E.et al.Ecosystem services altered by human changes in nitrogencycle:a new perspective for US decision making.Ecol.Lett.14,804–815(2011).14.Zhang,F.S.et al.Nutrient use efficiencies of major cereal crops in China andmeasures for improvement.Acta Pedol.Sin.45,915–924(2008).15.Zhu,Z.L.&Chen,D.L.Nitrogen fertilizer use in China:contributions to foodproduction,impacts on the environment and best management strategies.Nutr.Cycl.Agroecosyst.63,117–127(2002).16.Ju,X.T.et al.Reducing environmental risk by improving N management inintensive Chinese agricultural systems.Proc.Natl A106,3041–3046 (2009).17.Erisman,J.W.&Draaijers,G.P.J.Studies in Environmental Science Vol.63,9(Elsevier,1995).18.Frink,C.R.,Waggoner,P.E.&Ausubel,J.H.Nitrogen fertilizer:retrospect andprospect.Proc.Natl A96,1175–1180(1999).19.Liu,X.J.et al.Nitrogen deposition in agroecosystems in the Beijing area.Agric.Ecosyst.Environ.113,370–377(2006).20.Klimont,Z.et al.Projections of SO2,NO x,NH3and VOC emissions in East Asia up to2030.Wat.Air Soil Pollut.130,193–198(2001).21.Schjørring,J.K.Atmospheric ammonia and impacts of nitrogen deposition:uncertainties and challenges.New Phytol.139,59–60(1998).22.He,C.E.,Liu,X.J.,Fangmeier,A.&Zhang,F.S.Quantifying the total airbornenitrogen-input into agroecosystems in the North China Plain.Agric.Ecosyst.Environ.121,395–400(2007).23.Pitcairn,C.et al.Diagnostic indicators of elevated nitrogen deposition.Environ.Pollut.144,941–950(2006).24.Jenkinson,D.S.,Poulton,P.R.,Johnston,A.E.&Powlson,D.S.Turnover ofnitrogen-15-labelled fertilizer in old grassland.Soil Sci.Soc.Am.J.68,865–875 (2004).25.Kim,T.W.,Lee,K.,Najjar,R.G.,Jeong,H.D.&Jeong,H.J.Increasing N abundance inthe northwestern Pacific Ocean due to atmospheric nitrogen deposition.Science 334,505–509(2011).26.Hietz,P.et al.Long-term change in the nitrogen cycle of tropical forests.Science334,664–666(2011).27.Cooper,O.R.et al.Increasing springtime ozone mixing ratios in the freetroposphere over western North America.Nature463,344–348(2010).28.Liu,J.G.&Diamond,J.China’s environment in a globalizing world.Nature435,1179–1186(2005).29.Zhang,Q.,He,K.B.&Huo,H.Cleaning China’s air.Nature484,161–162(2012).30.Han,W.X.,Fang,J.Y.,Reich,P.B.,Woodward,F.I.&Wang,Z.H.Biogeographyand variability of eleven mineral elements in plant leaves across gradients ofclimate,soil and plant functional type in China.Ecol.Lett.14,788–796(2011).Supplementary Information is available in the online version of the paper. Acknowledgements We thank X.Chen,A.Bleeker,X.Ju,J.Shen and R.Jiang for their comments on an earlier version of the manuscript or assistance during the manuscript revision,and we thank H.Liu,J.Lu¨,F.Chen,L.Wu and S.Qiu for providing data from long-term experiments.The authors also acknowledge all those who provided local assistance or technical help to the CAU-organized Deposition Network.This work was financially supported by the Chinese National Basic Research Program(2009CB118606),an Innovative Group Grant from the NSFC(31121062,41071151, 40973054)and the Sino-German Research Training Group(GK1070).Author Contributions X.L.and F.Z.designed the research.X.L.,Y.Z.,W.H.,A.T.,J.S.and Z.C.conducted the research(collected the data sets and analysed the data).X.L.,Y.Z. and P.V.wrote the manuscript.J.W.E.,K.G.,P.C.,A.F.and mented on the manuscript.Author Information Reprints and permissions information is available at/reprints.The authors declare no competing financial interests. Readers are welcome to comment on the online version of the paper.Correspondence and requests for materials should be addressed to F.Z.(zhangfs@).LETTER462|N A T U R E|V O L494|28F E B R U A R Y2013METHODSData sources for bulk N deposition.Bulk N deposition data are from two sources:monitoring results from a regional atmospheric deposition monitoring network(that is,the China Agricultural University-organized Deposition Network(CAUDN));and results published during the period1980–2010.Only bulk deposition data for inorganic N(NH4-N and NO3-N)were summarized in this study because no dry deposition data for N were reported in China in the 1980s and1990s2.Our data sets include year of monitoring at every site;location of every monitoring site;annual amount of precipitation;concentration and deposi-tion of NH4-N,NO3-N and total inorganic N(TIN);and ratios of NH4-N to NO3-N concentration and deposition in precipitation.Some sites that contained only portions of deposition data(that is,only concentration or deposition of inorganic N)were also included in our data sets.Briefly,bulk N deposition samples from the CAUDN were collected using always-open rain gauges(different from wet-only samplers)on a daily basis and measured by colorimetry(that is,continuous flow analysis)or ion chromatography.For literature deposition data,these are the two most common methods for measuring inorganic N(NH4-N and NO3-N)con-centrations in precipitation(for details,see references in Supplementary Table2). Bulk deposition rates of NH4-N,NO3-N and TIN were then calculated by mul-tiplying N concentration in precipitation by the amount of precipitation19.In this paper,we summarize866data points of N concentrations in rainwater and671data points of bulk N deposition rates from between1980and2010.All of the data originated from publications and our own results from the CAUDN.In all,we collected315references on annual N concentration and deposition results (including276journal articles,19dissertations and20monographs)(Supplemen-tary Table2)in this data set,covering270monitoring sites widely distributed in China(Supplementary Fig.1).The current bulk N deposition data sets are the most complete deposition data sets in China in spite of some minor weaknesses (that is,relatively fewer monitoring sites and data points in northeast China, northwest China and the Tibetan plateau).Therefore,our meta-analysis based on the data set should be reliable.The same results published in different sources (that is,journals,dissertations or monographs)were cited only once and only one reference source was listed in the following priority:English-language journals, Chinese-language journals,dissertations and monographs.To clarify regional variations,bulk N deposition data were also summarized on a regional basis(Supplementary Fig.1):northern China,comprising Beijing, Tianjin,Hebei,Henan,Shandong,Shanxi and Shaanxi provinces;southeast China,comprising Shanghai,Jiangsu,Zhejiang,Anhui,Hubei,Hunan,Jiangxi, Fujian,Guangdong,Hong Kong,Macau,Taiwan and Hainan provinces;south-west China,comprising Sichuan,Chongqing,Guizhou,Yunnan and Guangxi provinces;the Tibetan plateau,comprising Tibet and Qinghai provinces;northeast China,comprising Liaoning,Jilin and Heilongjiang provinces;and northwest China,comprising Xinjiang,Inner Mongolia,Ningxia and Gansu provinces. Data sources for plant foliar N from non-agricultural vegetation types.A total of981observations of plant foliar N content and859observations of foliar P were collected from666natural and semi-natural terrestrial plant species(including woody and herbaceous species,non-N-fixing and N-fixing species,and evergreen and deciduous species,according to various classification methods)between1980 and2010at245sites distributed across the whole of China(Supplementary Fig.1), on the basis of our field measurements and the literature(for details,see references in Supplementary Table3).Leaves were sampled mainly during the growing season (July to September).Leaf samples were oven-dried,ground and then measured for N concentrations using the Kjeldahl method.To avoid systematic deviation caused by chemical determination,N samples determined with C and N elemental analysers30(after the year2000)were not included in our analysis.For the few leaf samples lacking detailed time records,the sampling year was assumed to be two years before the associated paper was first submitted(for example,the sampling year was assumed to be2004if the paper was submitted in2006).Mean foliar N was calculated for each species at the same sites within the same sampling year. Data sources for crop N uptake from zero-N croplands.A total of278data points of crop N uptake were collected from non-N-fertilized(zero-N fertilizer input for at least five years)croplands(described as‘zero-N plots’hereafter)during the1980s and2000s across China,on the basis of our field experiments and published data22,31–37.Nitrogen uptake by rice,wheat and maize includes N accu-mulation in grain plus straw at harvest(normally from May to October)of the three main cereal crops on zero-N plots.Grain and straw samples were oven-dried, ground and measured for N concentrations using the Kjeldahl method when the harvest process was completed in the field.Nitrogen accumulation in grain or straw was calculated as N concentration multiplied by grain or straw dry matter; crop N uptake was then the sum of grain and straw N accumulation.For a few publications that did not provide crop N uptake data,we used conversion coefficients38of grain yield for estimating N uptake by rice,wheat and maize, respectively.Data sources for anthropogenic NH3and NO x emissions and their main con-tributors.NH3and NO x(sum of NO and NO2)emission inventories in China during1980and2010were obtained from all published data available2and updated to2010on the basis of data from the National Bureau of Statistics of China(/english/statisticaldata/yearlydata/)and the reported NH3and NO x emission factors39;if several emission values were available in one specific year only,an averaged emission value was used.Briefly,China’s national emission inventories for NH3and NO x were based on different emission sources and emission factors of specific N r pared with the NO x emission inventory(mainly point sources),the NH3emission inventory(mainly non-point-source emission)has a relatively large uncertainty2,21.The ratios of NH3-N to NO x-N emission were then calculated on the basis of averaged annual emission data over the period1980–2010.Data on N fertilizer use and domestic animal numbers(expressed as livestock units)were from Chinese Agriculture Statistics(1982–2010).The transforma-tion of domestic animal numbers to livestock units was based on some widely used conversion factors in Europe(http://epp.eurostat.ec.europa.eu/statistics_ explained/index.php/Glossary:LSU).Data on coal consumption(as standard coal) and motor vehicle numbers were from the National Bureau of Statistics of China (/english/statisticaldata/yearlydata/).Statistical analysis.Annual precipitation;N concentration in precipitation;bulk N deposition;ratios of NH4-N to NO3-N in bulk precipitation;foliar N,foliar P and crop N uptake from zero-N plots;NH3and NO x emissions and ratios of NH3-N to NO x-N emission;N fertilizer use;and numbers of domestic animals,numbers of motor vehicles and coal consumption in China were fitted(with year)by linear mixed models or nonlinear regression models for the interval1980–2010.We used mixed models40,41instead of simple linear regressions because of the large site-to-site variability.The selection of linear versus nonlinear regression depended on the distribution of the‘scatter diagram’(initially judging the temporal variation fol-lowed by a linear or nonlinear trend)and on the correlation coefficients(r)and P values in the linear or nonlinear regression equations41.Correlation coefficients were tested by a statistical model(SPSS13.0,SPSS Inc.).Differences between all of the above-mentioned parameters as measured in the1980s(1980–1989)and the 2000s(2000–2010)were compared statistically using an unpaired two-tail Student’s t-test.Significant difference is assumed when the P value is,0.05or as otherwise stated.31.Guo,L.P.Study on the Integrated Effects of Long-Term Fertilization under Wheat-CornRotation System at Fluvo-aquic Soil in Beijing Area63–65.PhD thesis,ChinaAgricultural Univ.(1998).32.Zhao,B.Q.et al.Long-term fertilizer experiment network in China:crop yields andsoil nutrient trends.Agron.J.102,216–230(2010).33.Miao,Y.X.,Stewart,B.A.&Zhang,F.S.Long-term experiments for sustainablenutrient management in China:a review.Agron.Sustain.Dev.31,397–414(2011).34.Fan,M.S.Integrated Plant Nutrient Management for Rice-upland Crop RotationSystem43–56.PhD thesis,China Agricultural Univ.(2005).35.Ye,Y.L.et al.Effect of long-term fertilizer application on yield,nitrogen uptake andsoil NO3-N accumulation in wheat/maize intercropping.J.Plant Nutr.Fertil.Sci.10, 113–119(2004).36.Fan,T.L.et al.Long-term fertilization on yield increase of winter wheat-maizerotation system in Loess Plateau dryland of Gansu.J.Plant Nutr.Fertil.Sci.10, 127–131(2004).37.Liao,Y.L.et al.Effects of long-term application of fertilizer and rice straw on soilfertility and sustainability of a reddish paddy soil productivity.Sci.Agric.Sin.42, 3541–3550(2009).38.Lu,R.K.et al.Nutrients cycle and balance in Chinese typical farm land biologicalsystem II.Index of nutrients income in farm land.Chin.J.Soil Sci.27,151–154 (1996).39.Olivier,J.G.J.,Bouwman,A.F.,Van der Hoek,K.W.&Berdowski,J.J.M.Global airemission inventories for anthropogenic sources of NO x,NH3and N2O in1990.Environ.Pollut.102,135–148(1998).40.Snijders,T.&Bosker,R.Multilevel Analysis:an Introduction to Basic and AdvancedModeling67–83(Sage,1999).41.Littell,R.C.,Milliken,G.A.,Stroup,W.W.&Wolfinger,R.D.SAS System for MixedModels525–566(SAS Institute Inc.,1996).LETTER。

不同浓度氮磷配比对丹参生长和活性成分积累的影响以一年生丹参种苗为试验材料，采用“3414”不完全随机区组设计，定期浇灌营养液进行盆栽试验。

于不同生长时期动态取样，测量丹参株高、地上鲜重、根鲜重、根干重及活性成分含量等指标。

研究氮磷元素对丹参生长、干物质积累及活性成分积累的影响，以期探寻兼顾产量和质量的氮磷配比及适宜施肥量。

结果表明：①高浓度氮肥有利于丹参地上干物质积累，低浓度氮肥促进丹参干物质积累向地下转移，N1P1配比使丹参干物质积累向地下转移的时间提前；②回归分析表明在丹参生长前期（7月初以前），将氮肥和磷肥分别按 1.521，0.355 g·L-1的浓度作为基肥施入可促进丹参生长，在丹参生长后期（8月中旬以后），氮肥和磷肥按2.281，0.710 g·L-1的质量浓度进行追肥可促进根干物质积累；③丹参的5种活性成分含量均随氮肥浓度升高而降低，随磷肥浓度升高而升高。

氮肥磷肥2∶3配施较适合丹参酚酸类成分的积累，按1∶2配施较适合丹参酮类成分的积累。

标签：氮肥；磷肥；氮磷互作效应；丹参生长；活性成分Effects of different concentrations of nitrogen and phosphorus on growth andactive components of Salvia miltiorrhizaXIA Guihui1，WANG Qiuling2，WANG Wenquan1，2，3*，HOU Junling1*，SONG Qingyan1，LUOlin1，ZHANG Doudou1，YANG Xiang1（1. School of Chinese Pharmacy，Beijing University of Chinese Medicine，Beijing 100102，China；2. Institute of Medicinal Plant Development，Chinese Academy of Medical Sciences and PekingUnion Medical College，Beijing 100193，China；3. Engineering Research Center of Good Agricultural Practice for Chinese Crude Drugs，Ministry of Education，Beijing 100102，China）[Abstract] With annual Salvia miltiorrhiza seedlings as experimental material，using “3414” optimal regression design recommended by the Ministry of Agriculture and regularly watered with nutrient solution，through the dynamic sampling of S. miltiorrhiza in different growing stages，and the growth index，dry weight of plant root and content of active components were measured. The potted experiments were applied to study the effects of different nitrogen and phosphorus ratios on the growth，dry matter accumulation and accumulation of active components of S. miltiorrhiza，in order to explore a compatible fertilization method of nitrogen and phosphorus ratio that are suitable for production and quality of S. miltiorrhiza. The results reported as follows：①High concentrations of nitrogen fertilizer was beneficial to dry matter accumulation of S. miltiorrhiza aerial parts，and low concentration of nitrogen fertilizer transferred the dry matter accumulation to underground，and N1P1 could make the transfer ahead of time；②Regression analysis showed that in the early growth stage （before early July），we could use the nitrogen and phosphorus as basic fertilizer at a concentration of 1.521，0.355 g·L-1 respectively to promote the growth of S. miltiorrhiza and at a concentration of 2.281，0.710 g·L-1 respectively to promote the dry matter accumulation of root （after midAugust）；③Five kinds of active components of S. miltiorrhiza decreased with the increase of nitrogen concentration，and increased with the increase of the concentration of phosphate fertilizer. Nitrogenous fertilizer，phosphate fertilizer in NP=2∶3 ratio was more suitable for the accumulation of salvianolic acids，in NP=1∶2 ratio was more suitable for the accumulation of tanshinone.[Key words] nitrogen fertilizer；phosphate fertilizer；interdependent effects；Salvia miltiorrhiza growth；active componentsdoi：10.4268/cjcmm20162215丹参Salvia miltiorrhiza Bge.为常用大宗药材，药用历史悠久，目前丹参栽培品已成为市场主流，在丹参栽培过程中施肥是一重要环节[1]。