藏东南森林穿透雨氮沉降通量变化特征及其影响因子

2012—2013年生长季在野外原位观测了青藏高原林芝地区森林穿透雨中不同形态氮湿沉降通量,并研究了氮沉降通量的变化特征及其影响因子。研究结果表明,2012、2013年可溶性总氮(TN)累积沉降通量分别为8.82kg·hm-2·a-1和6.91kg·hm~(-2)·a~(-1);其中,硝态氮(NO-3-N)、铵态氮(NH+4-N)、可溶性总有机氮(DON)沉降通量分别占总氮的16.98%、53.39%和29.63%,NH+4-N对湿沉降通量的贡献率最大。不同形态氮沉降通量呈现明显的季节性变化特征,一般在夏季达到最大值。随着降水量及温度的升高,不同形态氮沉降通量均有增加趋势;其中,总无机氮(TIN)与月平均气温呈显著相关关系(p0.05),TN、TIN均与月累积降水量呈极显著相关(p0.01)。月累计降水量和月平均气温可以共同解释森林穿透雨中TN沉降通量55.2%的变化。     

冻融交替对河岸缓冲带土壤无机氮和土壤微生物量氮的影响

全球气候变化引起的中高纬度地区积雪覆盖和降雪格局变化,造成该区域土壤冻融交替强度和频次变化,是土壤氮循环的重要影响因素。冻融温差和冻融循环次数影响微生物数量和群落的变化,进而影响土壤氮素生物地球化学循环。以大伙房水库实验林场小流域的河岸缓冲带生态系统为研究对象,通过分析冻融交替对河岸缓冲带土壤无机氮和土壤微生物量氮的影响,阐明冻融交替对土壤无机氮含量变化的影响机制,为评估小流域氮素流失风险提供依据。结果表明：随着冻融循环次数的增加,土壤无机氮含量呈增加趋势;不同温差的冻融循环处理对土壤无机氮影响不同,冻融条件为-5/+5℃和-20/+5℃时土壤无机氮含量在冻融循环10次之后分别为34.9±0.9 mg/kg和37.2±0.8 mg/kg,是处理前的1.21和1.41倍;冻融温差和冻融循环次数对土壤NH₄⁺–N含量有极显著影响(P<0.01),土壤冻融10次后土壤NH₄⁺–N含量是对照处理的4-10倍;冻融循环次数对土壤NO₃^－–N含量有显著影响(P<0.05),冻融温差对NO₃^－–N含量无显著影响(P>0.05);土壤微生物量氮含量对冻融循环的响应显著(P<0.01)。可见,冻融交替显著增加了土壤无机氮含量,由于早春季节植被对无机氮吸收较少,可能增大土壤氮素随冰雪融化的淋溶流失风险。     

南京郊区大气氮化物浓度和氮沉降通量的研究

为研究南京郊区的大气氮化物污染状况,进而估算其大气氮沉降通量,2005年6月-2006年5月在南京大学浦口校区气象园进行了大气、气溶胶和雨水样本的收集,同步进行近地面气象观测.在实验室分析大气氮化物NOx、NH3和有机氮浓度、总悬浮颗粒物(TSP)中硝酸盐、亚硝酸盐、铵盐和有机氮的质量浓度、雨水中NO-3、NO-2、NH+4离子和有机氮的质量浓度,利用气象资料和大叶阻力相似模型计算大气氮化物的干沉降速度,进而定量估算大气氮沉降通量.研究结果表明:南京郊区大气中有机氮浓度水平较高,无机氮(氨态氮和硝态氮)浓度水平较低.大气氮沉降量较大,且湿沉降和有机沉降贡献率占主导地位,这取决于本地区的下垫面和污染状况,同时也与气象条件有密切关系.     

盘锦湿地芦苇群落土壤碱解氮及溶解性有机碳季节动态

基于2005年4～10月盘锦湿地芦苇群落土壤不同土层土壤碱解氮及溶解性有机碳的观测资料,分析了盘锦湿地芦苇群落土壤碱解氮与溶解性有机碳(DOC)的季节动态。结果表明:不同土层碱解氮、溶解性有机碳的季节动态并不相同。0～10 cm土层碱解氮与DOC季节动态相似,6月土壤碱解氮与DOC含量均最高,分别为244.86 mg/kg和13.16 mg/L。8月碱解氮含量最低,为139.18 mg/kg;9月DOC含量最低。10～20 cm土层DOC的季节性动态变化与表土具有相似性,峰值均出现在6月,谷值出现在9月;10～20 cm土层碱解氮最低值出现在6月,与0～10 cm土层不同。20～30 cm土层内,4～7月DOC几乎无变化,8月DOC含量最低,9月增加;4～5月碱解氮波动较大,5月降到102 mg/kg,6月增加到151 mg/kg。研究表明,盘锦湿地芦苇群落土壤微生物活性与凋落物分解对DOC及碱解氮的季节动态有很大的影响,同时温度、降水量及冻融也影响着DOC及碱解氮的季节动态。     

紫金山不同海拔高度土壤的碳氮分布特征

有机碳氮是影响陆地生态系统的重要因子,保持并提高土壤碳氮储量,是稳定生态系统生产力的关键.以南京紫金山土壤为研究对象,依照海拔高度进行采样,对比分析了土壤有机碳氮的变化规律.研究结果表明:紫金山土壤有机碳氮受地表植被的影响比较大,混交林>林地>草地,土壤有机碳氮总量随海拔的升高呈现上升趋势,土壤碳氮比高达34~45,且随海拔升高呈下降趋势.相关分析表明,紫金山土壤有机碳与全氮质量分数呈显著正相关关系,由此说明氮素主要以有机氮的形式存在于有机质中.     

陕北丘陵区陡坡柠条林地与荒坡的土壤水分变化研究

通过定点土壤水分测定与对比分析,研究陕北丘陵区陡坡柠条林地与荒坡土壤水分亏缺状况、年际内动态变化规律、干燥化特征及其自然降水的补偿能力。结果表明：柠条林地0～10m土层贮水量仅相当于田间持水量的26．2％～41．2％。荒坡地0～10m土层贮水量相当于田间持水量的39．8％～41．2％。土壤贮水量的分布是阳坡〈半阳坡〈阴坡,上坡位〈下坡位。年际间土壤水分的变异程度随土壤深度的增加而减弱,土壤贮水量的变化主要发生在2m以上土层内。土壤贮水量具有明显的季节变化特征,但滞后于降雨量变化。生长季内,柠条地与荒坡土壤平均贮水量差异显著（P〈0．05）,土壤越深,其含水量变化越小。两种利用方式的土壤剖面都产生不同程度的干化层。柠条林地深层土壤干燥化强度明显大于荒坡地。丰水年柠条林雨水补偿的深度仅为1．0m,荒坡也仅为1．2m。柠条林丰水年的雨水补偿的深度比干旱年可增加60cm以上,5m土层贮水增量增加3倍以上。     

干旱和复水对羊草碳氮分配的影响

植物的碳氮营养及其相互关系是最重要的基本生物过程之一,阶段性干旱对植物碳氮分配的影响研究甚少。实验以中国北方草原的典型植物羊草为材料,研究不同干旱持续期复水对羊草碳氮含量、分配及其相互关系的影响。结果表明:短期和中期干旱使植株生物量、氮素水平和单株总氮量增加,但长期干旱使之降低。水分处理对碳含量的影响不显著。干旱后复水降低了各器官特别是绿叶的碳氮比。中度持续干旱的氮素利用率(NUE)最高、短期干旱最低。羊草各器官氮素绝对量占整株的百分比从大到小依次为:绿叶、根茎、根、枯叶和茎鞘,其中叶片的氮素总量占植株的一半以上;随着干旱持续期的增加,氮素对根部的投资亦加大。羊草受到适当干旱驯化后复水引发的超补偿作用可促进羊草植株生长、提高氮素水平,并在一定程度上通过碳氮分配的调节作用来适应于阶段性的干旱胁迫。     

温带森林土壤溶液溶解性N2O和CO2含量特征及其影响机制

利用陶瓷头土壤溶液收集器采集2006年7月～2007年8月问长白山阔叶红松天然林不同深度(15cm和60 cm)土壤溶液,探讨应用气液萃取平衡-气相色谱法测定森林土壤溶液中溶解性气体N_2O和CO_2浓度的可行性,并利用此方法研究林地不同深度土壤溶液中两种气体含量特征及其影响机理.研究结果显示观测期内林地15 cm和60 cm深度土壤溶液中溶解性CO_2浓度的变化范围分别为5.26～10.71μg·mL~(-1)(C)和3.13～6.16 μg·mL~(-1)(C),溶解性N_2O浓度的变化范围分别为2.44～13.40 ng·mL~(-1)(N)和3.23～27.98 ng·mL~(-1)(N).阔叶红松天然林土壤溶液中溶解性CO_2和N_2O浓度均呈现出明显的季节性变化.春融后的降水促进了土壤溶液中溶解性N_2O产生,尤其在60 cm深度.与60 cm深度相比,林地15 cm深度溶液中溶解性CO_2浓度的季节性变化更明显,尤其在植物生长旺季.逐步回归分析显示,水溶性有机碳含量可以解释林地不同深度溶液中溶解性CO_2浓度变化的29%;水溶性有机氮含量可以解释林地60 cm深度溶解性N_2O浓度变化的34%.因此,水溶性有机碳和有机氮分别是长白山阔叶红松林土壤溶液溶解性CO_2和N_2O形成的重要因子.同时研究结果表明本文实验方法对于测定林地不同深度土壤溶液中溶解性N_2O和CO_2含量均有较好的适用性,连续三次萃取后所获得的气体浓度可有效反映溶液中的实际气体浓度.     

黄河源区降雪对不同冻融阶段土壤温湿变化的影响北大核心CSCD

利用2013年10月1日至2014年5月31日黄河源区鄂陵湖流域的土壤温度资料首先划分土壤不同冻融阶段,然后在每个阶段各选取一次降雪过程,分析了降雪对土壤温湿变化的影响。结果表明:在土壤冻结阶段,雪后晴天(有雪覆盖)土壤净输出的热量减少,5 cm和10 cm土壤日最低温度明显升高,20 cm土壤日最低温度升至0℃以上,导致20 cm土壤达到完全冻结的时间延长;在土壤消融阶段,降雪当天土壤净输入的热量减少,5 cm和10 cm土壤日最高温度突降至0℃以下,导致5 cm和10cm土壤达到完全消融的时间增加。在以上两个阶段的降雪过程中,积雪不仅可通过自身的消融增加浅层土壤湿度,还可通过改变浅层土壤温度间接影响浅层土壤湿度,而在土壤完全冻结阶段,积雪对土壤温度虽有影响,但对土壤湿度的直接和间接影响都较小。在整个土壤冻融阶段,与由土壤冻结和消融引起的土壤湿度变化相比,降雪引起的土壤湿度变化较小。     

冬小麦土壤深松保墒增产效应试验研究

采用土壤深松 45cm、30 cm处理打破犁底层 ,1 996～ 1 998年连续进行 2个年度的冬小麦保墒、增产效应田间试验 .试验结果表明 :土壤深松处理后可减少冬小麦全生育期 0～ 1 0 0 cm的作物耗水量 ,促进根系对 1 0 0～ 2 0 0 cm土层土壤水分的利用 ,提高冬小麦的产量耗水比 .土壤深松处理能明显增加 0～ 30 cm土层的土壤湿度和含水量 ,降低 0～ 50 cm土层的土壤容重 .有利于冬小麦根系、茎、叶的生长发育和总生物量的累积 .土壤深松 45cm处理 2年平均冬小麦增产 7.0 % ,土壤深松 30 cm处理第一年增产 7.7% .冬小麦土壤深松保墒增产效应的适宜深松深度为 30 cm.     

Synergistic Effects of Nitrogen Amendments and Ethylene on Atmospheric Methane Uptake under a Temperate Old-growth Forest

An increase in atmospheric nitrogen (N) deposition can promote soil acidification, which may increase the release of ethylene (C2H4) under forest floors. Unfortunately, knowledge of whether increasing N deposition and C2H4 releases have synergistic effects on soil methane (CH4) uptake is limited and certainly deserves to be examined. We conducted some field measurements and laboratory experiments to examine this issue. The addition of (NH4)2SO4 or NH4Cl at a rate of 45 kg N ha-1 yr-1 reduced the soil CH4 uptake under a temperate old-growth forest in northeast China, and there were synergistic effects of N amendments in the presence of C2H4 concentrations equal to atmospheric CH4 concentration on the soil CH4 uptake, particularly in the NH4Cl-treated plots. Effective concentrations of added C2H4 on the soil CH4 uptake were smaller in NH+4 -treated plots than in KNO3-treated plots. The concentration of ca 0.3 μl C2H4 L-1 in the headspace gases reduced by 20% soil atmospheric CH4 uptake in the NH4Cl-treated plots, and this concentration was easily produced in temperate forest topsoils under short-term anoxic conditions. Together with short-term stimulating effects of N amendments and soil acidification on C2H4 production from forest soils, our observations suggest that knowledge of synergistic effects of NH+4 , rather than NO3- , amendments and C2H4 on the in situ soil CH4 uptake is critical for understanding the role of atmospheric N deposition and cycling of C2H4 under forest floors in reducing global atmospheric CH4 uptake by forests. Synergistic functions of NH4+ -N deposition and C2H4 release due to soil acidification in reducing atmospheric CH4 uptake by forests are discussed.     

Aspects of the cycle of inorganic nitrogen compounds in the tropical rain forest of the Ivory Coast

A partial balance of mineral N is given for the basins of two coastal rivers in a forest zone in the Ivory Coast. The dry and wet depositions on the basin surfaces is given for particulate matter (NO₃ ^–, NH₄ ⁺). The quantity of mineral N washed away in the rivers is evaluated. The losses from leaching of the soils by rainwater are about 0.33 to 1.0% of the atmospheric depositions for NH₄ ⁺–N and 2.2 to 5.8% for NO₃ ^––N. The yearly atmospheric input of N compounds to the ecosystem, about 1.4 g N m^–2 y^–1, is at least 14% of mineral N formed in the soils and is therefore quite significant.     

Field measurements of emission of nitric oxide from fertilized and unfertilized forest soils in Sweden

Application of nitrate fertilizers on two types of forest soils led to a marked increase in the NO emission rate indicating a large potential for NO production in these soils. The largest fluxes on the fertilized plots were up to 60 ng NO–N m^–2 s^–1. About 0.35% of the applied nitrogen was lost as NO within about 14 days after fertilization. The fluxes from the unfertilized forest soils were in the range 0.1 to 0.8 ng NO–N m^–2 s^–1 with a median value of 0.3 ng NO–N m^–2 s^–1. If this value, obtained during June and August to September, is representative for the growing season (150 days), it corresponds to an annual emission of 0.04 kg NO–N ha^–1. This is about 30% of the value obtained for an unfertilized agricultural soil. Because of the large areas occupied by forests in Sweden the flux of NO from forest soils represents a significant contribution to the total flux of NO from soils in Sweden.Earlier observations of equilibrium concentrations for NO have been verified. These were found to range from 0.2 to 2 ppbv for an unfertilized forest soil and up to 170 ppbv for a fertilized soil. At the rural site in Sweden where these measurements were performed the ambient concentrations where found to be less than this equilibrium concentration, and consequently there was generally a net emission of NO.There are still large uncertainties about the global flux of NO from soils. Using direct measurements on three different types of ecosystems and estimates based on a qualitative discussion for the remaining land areas, a global natural source for NO of the order of 1 Tg N a^–1 was obtained. If 0.35% of the total annual production of fertilizer nitrogen is lost as NO, fertilization of soils may contribute with 20% to the natural flux from soils.     

Wet deposition of atmospheric inorganic reactive nitrogen (Nr) across an urban-industrial-rural transect of Nr emission hotspot (India)

The present study comprehensively reports the simultaneous measurement of wet deposition of total inorganic nitrogen (TIN; which is the sum of the NH₄⁺-N and NO₃^?-N) at three different sites in Nr emission hotspot of Indo-Gangetic plain (IGP) over a year-long temporal scale from October 2017 to September 2018. At rural Meetli (MTL) site, urban Baraut (BRT) site and industrial Loni (LNI) site, the annual wet deposition of NH₄⁺-N was estimated as 21.87, 19.48 and 7.43 kg N ha^?1 yr^?1, respectively; the annual wet deposition NO₃^?-N was estimated as 12.96, 12.17 and 4.44 kg N ha^?1 yr^?1, respectively; and the annual wet deposition of TIN was estimated as 34.83, 31.64 and 11.87 kg N ha^?1 yr^?1, respectively. NH₄⁺-N was dominantly contributing species in annual, monsoon and non-monsoon-time wet deposition of TIN at all sites. The spatial gradient (variability) in percent contribution of NH₄⁺ to total annual volume-weighted mean (VWM) concentration of all analyte ions was observed as MTL (43.23%)?>?BRT (37.90%)?>?LNI (30%). On the other hand, the spatial gradient in percent contribution of NO₃^? to total annual VWM concentration of all analyte ions was observed as MTL (7.45%)?>?BRT (6.89%)?>?LNI (5.32%). The extremely narrow range of NH₄⁺-N/NO₃^?-N ratios (ranging from 1.60 at BRT site to 1.69 at LNI site) showed the approximately equal relative abundance of oxidized and reduced nitrogen (N) deposition across all sites. Inferences from enrichment factor analysis, principal component analysis and Pearson’s correlation coefficient analysis suggested that across all sites, virtually all NH₄⁺-N and NO₃^?-N depositions were originated anthropogenically. The annual wet deposition of TIN measured in this study showed?≥?6865%,?≥?6228% and?≥?2274% increment than the natural N deposition rate at MTL, BRT and LNI site, respectively. These empirically measured annual wet depositions of TIN also emanated theoretical transgression of critical N load threshold across all sites therefore signifying probable undermining of long-term elastic stability and resilience of ecosystems against stressor in the study domain.

     

An Investigation into the Ionic Chemical Composition and Mixing State of Biomass Burning Particles Recorded During TRACE-P P3B Flight#10

In this study bulk airborne aerosol composition measured by the PILS-IC (integration time of 3 min 24 s) during TRACE-P P3B Flight 10 are used to investigate the ionic chemical composition and mixing state of biomass burning particles. A biomass burning plume, roughly 3–4 days old, moderately influenced by urban pollution aerosols recorded in the Philippine Sea is investigated. Focusing on the fine particle NO₃⁻, SO₄²⁻, K⁺, NH₄⁺, and water-soluble organics, the observed correlations and nearly 1-to-1 molar ratios between K⁺ and NO₃⁻ and between NH₄⁺ and (SO₄²⁻+ inferred Organics) suggest the presence of fine-mode KNO₃, (NH₄)₂SO₄, and NH₄(Organics) aerosols. Under the assumption that these ion pairs existed, and because KNO₃ is thermodynamically less favored than K₂SO₄ in a mixture of NO₃⁻, SO₄²⁻, K⁺, NH₄⁺, and Organic anions, the measurements suggest that aerosols could be composed of biomass burning particles (KNO₃) mixed to a large degree externally with the (NH₄)₂SO₄ aerosols. A “closed-mode” thermodynamic aerosol simulation predicts that a degree of external mixing (by SO₄²⁻ mass) of 60 to 100% is necessary to achieve the observed ionic associations in terms of the existence of KNO₃. However, the degree of external mixing is most likely larger than 90%, based on both the presence of KNO₃ and the amounts of NH₄NO₃. Calculations are also shown that the aerosol mixing state significantly impacts particle growth by water condensation/evaporation. In the case of P3B Flight #10, the internal mixture is generally more hygroscopic than the external mixture. This method for estimating particle mixing state from bulk aerosol data is less definitive than single particle analysis, but because the data are quantitative, it may provide a complementary method to single particle chemical analysis.     

Factors influencing ammonia volatilization from urea in soils of the shortgrass steppe

The effects of soil moisture, temperature, and humidity treatments on urea hydrolysis and NH₃ volatilization were assessed in the laboratory. Field studies were conducted to determine seasonal NH₃ losses from simulated urine patches applied to contrasting soils of a representative hillslope of the shortgrass steppe region in the North American Great Plains.Losses of NH₃–N were most influenced by soil moisture. The effects of temperature and humidity on total, or temporal, losses of NH₃ were dependent on soil moisture. Losses ranged from 18.5% under conditions of low-temperature/high-humidity/wet soil to 7.7% under conditions of high-temperature/low-humidity/dry soil. In contrast, urea hydrolysis was not affected by soil moisture.Losses of NH₃–N from simulated urine applied to field plots ranged from 1.5% on footslope soils in summer to 14.1% on backslope (midslope) soils in summer, whereas losses were 8.1% on back-slope soils in winter. Factors such as soil texture, microbial activity, and plant productivity along a toposequence had larger effects than climatic variables on variation in the volatile losses of NH₃–N from this grassland.This paper is a report on the work presented at the international symposium Influence of marine and terrestrial biosphere on the chemical composition of the atmosphere, held in Mainz, F.R.G., on 16–22 March 1986.     

A global model of changing N2O emissions from natural and perturbed soils

A high resolution global model of the terrestrial biosphere is developed to estimate changes in nitrous oxide (N₂O) emissions from 1860–1990. The model is driven by four anthropogenic perturbations, including land use change and nitrogen inputs from fertilizer, livestock manure, and atmospheric deposition of fossil fuel NO _x . Global soil nitrogen mineralization, volatilization, and leaching fluxes are estimated by the model and converted to N₂O emissions based on broad assumptions about their associated N₂O yields. From 1860–1990, global N₂O emissions associated with soil nitrogen mineralization are estimated to have decreased slightly from 5.9 to 5.7 Tg N/yr, due mainly to land clearing, while N₂O emissions associated with volatilization and leaching of excess mineral nitrogen are estimated to have increased sharply from 0.45 to 3.3 Tg N/yr, due to all four anthropogenic perturbations. Taking into account the impact of each perturbation on soil nitrogen mineralization and on volatilization and leaching of excess mineral nitrogen, global 1990 N₂O emissions of 1.4, 0.7, 0.4 and 0.08 Tg N/yr are attributed to fertilizer, livestock manure, land clearing and atmospheric deposition of fossil fuel NO _x , respectively. Consideration of both the short and long-term fates of fertilizer nitrogen indicates that the N₂O/fertilizer-N yield may be 2% or more.C. NBM Definitions AET _mon (cm H₂O) = monthly actual evapotranspiration - AET _ann (cm H₂O) = annual actual evapotranspiration - age _h (years) = stand age of herbaceous biomass - age _w (years) = stand age of woody biomass - atmblc (gC/m²/month) = net flux of CO₂ from grid - biotoc (gC/g biomass) = 0.50 = convert g biomass to g C - beff _h = 0.8 = fraction of cleared herbaceous litter that is burned - beff _w = 0.4 = fraction of cleared woody litter that is burned - bfmin = 0.5 = fraction of burned N litter that is mineralized or converted to reactive gases which rapidly redeposit. Remainder assumed pyrodenitrified to N₂. + N₂O - bprob = probability that burned litter will be burned - burn _h (gC/m²/month) = herbaceous litter burned after land clearing - burn _w (gC/m²/month) = woody litter burned after land clearing - cbiomsh (gC/m²) = C herbaceous biomass pool - cbiomsw (gC/m²) = C woody biomass pool - clear (gC/m²/month) = woody litter C removed by land clearing - clearn (gN/m²/month) = woody litter N removed by land clearing - cldh (month^–1) = herbaceous litter decomposition coefficient - cldw (month^–1) = woody litter decomposition coefficient - clittrh (gC/m²) = C herbaceous litter pool - clittrw (gC/m²) = C woody litter pool - clph (month^–1) = herbaceous litter production coefficient - clpw (month^–1) = woody litter production coefficient - cnrath (gC/gN) = C/N ratio in herbaceous phytomass - cnrats (gC/gN) = C/N ratio in soil organic matter - cnratt (gC/gN) = average C/N ratio in total phytomass - cnratw (gC/gN) = C/N ratio in woody phytomass - crod (month^–1) = forest clearing coefficient - csocd (month^–1) = actual soil organic matter decompostion coefficient - decmult decomposition coefficient multiplier; natural =1.0; agricultural =1.0 (1.2 in sensitivity test) - fertmin (gN/m²/month) = inorganic fertilizer input - fleach fraction of excess inorganic N that is leached - fligh (g Lignin/ g C) = lignin fraction of herbaceous litter C - fligw (g Lignin/ g C) = 0.3 = lignin fraction of woody litter C - fln2o = .01–.02 = fraction of leached N emitted as N₂O - fnav = 0.95 = fraction of mineral N available to plants - fosdep (gN/m²/month) = wet and dry atmospheric deposition of fossil fuel NO _x - fresph = 0.5 = fraction of herbaceous litter decomposition that goes to CO₂ respiration - fresps = 0.51 + .068 ^* sand = fraction of soil organic matter decomposition that goes to CO₂ respiration - frespw = 0.3 ^* (^* see comments in Section 2.3 under decomposition) = fraction of woody litter decomposition that goes to CO₂ respiration - fsoil = ratio of NPP measured on given FAO soil type to NPF_miami - fstruct = 0.15 + 0.018 ^* ligton = fraction of herbaceous litter going to structural/woody pool - fvn2o = .05–.10 = fraction of excess volatilized mineral N emitted as N₂O - fvol = .02 = fraction of gross mineralization flux and excess mineral N volatilized - fyield ratio of total agricultural NPP in a given country in 1980 to total NPP_miami of all displaced natural grids in that country - gimmob _h (gN/m²/month) = gross immobilization of inorganic N into microbial biomass due to decomposition of herbaceous litter - gimmob _s (gN/m²/month) = gross immobilization of inorganic N into microbial biomass due to decomposition of soil organic matter - gimmob _w (gN/m²/month) = gross immobilization of inorganic N into microbial biomass due to decomposition of woody litter - graze (gC/m²/month) = C herbaceous biomass grazed by livestock - grazen (gN/m²/month) = N herbaceous biomass grazed by livestock - growth _h (gC/m²/month) = herbaceous litter incorporated into microbial biomass - growth _w (gC/m²/month) = woody litter incorporated into microbial biomass - gromin _h (gN/m²/month) = gross N mineralization due to decomposition and burning of herbaceous litter - gromin _s (gN/m²/month) = gross N mineralization due to decomposition of soil organic matter - gromin _w (gN/m²/month) = gross N mineralization due to decomposition and burning of woody litter - herb herbaceous fraction by weight of total biomass - leach (gN/m²/month) = leaching (& volatilization) losses of excess inorganic N - ligton (g lignin-C/gN) = lignin/N ratio in fresh herbaceous litter - LP _h (gC/m²/month)= C herbaceous litter production - LP (gC/m²/month) = C woody litter production - LPN _h (gN/m²/month) = N herbaceous litter production - LPN _W (gN/m²/month) = N woody litter production - manco2 (gC/m²/month) = grazed C respired by livestock - manlit (gC/m²/month) = C manure input (feces + urine) - n2oint (gN/m²/month) = intercept of N₂O flux vs gromin regression - n2oleach (gN/m²/month) = N₂O flux associated with leaching and volatilization of excess inorganic N - n2onat (gN/m²/month) = natural N₂O flux from soils - n2oslope slope of N₂O flux vs gromin regression - nbiomsh (gN/m²) = N herbaceous biomass pool - nbiomsw (gN/m²) = N woody biomass pool - nfix (gN/m²/month) = N₂ fixation + natural atmospheric deposition - nlittrh (gN/m²) = N herbaceous litter pool - nlittrw (gN/m²) = N woody litter pool - nmanlit (gN/m²/month) = organic N manure input (feces) - nmanmin (gN/m²/month) = inorganic N manure input (urine) - nmin (gN/m²) = inorganic N pool - NPP _acth (gC/m²/month)= actual herbaceous net primary productivity - NPP _actw (gC/m²/month) = actual woody net primary productivity - nvol (gN/m²/month) = volatilization losses from inorganic N pool - plntnav (gN/m²/month)= mineral N available to plants - plntup _h (gN/m²/month) = inorganic N incorporated into herbaceous biomass - plntup _w (gN/m²/month) = inorganic N incorporated into woody biomass - precip _ann (mm) = mean annual precipitation - precip _mon (mm) = mean monthly precipitation - pyroden _h (gN/m²/month) = burned herbaceous litter N that is pyrodenitrified to N₂ - pyroden _w (gN/m²/month) = burned woody litter N that is pyrodenitrified to N₂ - recyc fraction of N that is retranslocated before senescence - resp _h (gC/m²/month) = herbaceous litter CO₂ respiration - resp _s (gC/m²/month) = soil organic carbon CO₂ respiration - resp _w (gC/m²/month) = woody litter CO₂ respiration - sand sand fraction of soil - satrat ratio of maximum NPP to N-limited NPP - soiloc (gC/m²) = soil organic C pool - soilon (gN/m²) = soil organic N pool - temp _ann (°C) = mean annual temperature - temp _mon (°C) = mean monthly temperature Now at the NOAA Aeronomy Laboratory, Boulder, Colorado.     

Field measurements of NO and NO2 emissions from fertilized and unfertilized soils

Field measurements of NO and NO₂ emissions from soils have been performed in Finthen near Mainz (F.R.G.) and in Utrera near Seville (Spain). The applied method employed a flow box coupled with a chemiluminescent NO _x detector allowing the determination of minimum flux rates of 2 g N m^-2 h^-1 for NO and 3 g m^-2 h^-1 for NO₂.The NO and NO₂ flux rates were found to be strongly dependent on soil surface temperatures and showed strong daily variations with maximum values during the early afternoon and minimum values during the early morning. Between the daily variation patterns of NO and NO₂, there was a time lag of about 2 h which seem to be due to the different physico-chemical properties of NO and NO₂. The apparent activation energy of NO emission calculated from the Arrhenius equation ranged between 44 and 103 kJ per mole. The NO and NO₂ emission rates were positively correlated with soil moisture in the upper soil layer.The measurements carried out in August in Finthen clearly indicate the establishment of NO and NO₂ equilibrium mixing ratios which appeared to be on the order of 20 ppbv for NO and 10 ppbv for NO₂. The soil acted as a net sink for ambient air NO and NO₂ mixing ratios higher than the equilibrium values and a net source for NO and NO₂ mixing ratios lower than the equilibrium values. This behaviour as well as the observation of equilibrium mixing ratios clearly indicate that NO and NO₂ are formed and destroyed concurrently in the soil.Average flux rates measured on bare unfertilized soils were about 10 g N m^-2 h^-1 for NO₂ and 8 g N m^-2 h^-1 for NO. The NO and NO₂ flux rates were significantly reduced on plant covered soil plots. In some cases, the flux rates of both gases became negative indicating that the vegetation may act as a sink for atmospheric NO and NO₂.Application of mineral fertilizers increased the NO and NO₂ emission rates. Highest emission rates were observed for urea followed by NH₄Cl, NH₄NO₃ and NaNO₃. The fertilizer loss rates ranged from 0.1% for NaNO₃ to 5.4% for urea. Vegetation cover substantially reduced the fertilizer loss rate.The total NO _x emission from soil is estimated to be 11 Tg N yr^-1. This figure is an upper limit and includes the emission of 7 Tg N yr^-1 from natural unfertilized soils, 2 Tg N yr^-1 from fertilized soils as well as 2 Tg N yr^-1 from animal excreta. Despite its speculative character, this estimation indicates that NO _x emission by soil is important for tropospheric chemistry especially in remote areas where the NO _x production by other sources is comparatively small.     

青藏高原湿地土壤冻结、融化期间的陆面过程特征

利用青藏高原中部玉树隆宝湿地2015年7月-2016年7月的观测资料,分析了土壤冻结、融化前后土壤温、湿度和地表能量收支特征,结果表明：冻土持续时期为12月至次年4月,深层土壤的冻结较浅层土壤滞后,融化过程快于冻结过程,5-40 cm土壤全部冻结历时51 d,全部融化历时19 d。土壤体积含水量年变化幅度达0.6 m³/m³。冻结过程5-40 cm土壤体积含水量下降,融化过程5-10 cm土壤体积含水量升高。土壤冻结之后,感热通量白天的值升高,潜热通量白天的值降低,净辐射和土壤热通量均降低,土壤热通量日变化幅度增大。土壤融化之后,潜热通量、净辐射和土壤热通量白天的值升高。地表反照率、鲍恩比、土壤热导率和土壤热扩散率冻结后增大融化后减小,土壤热容量冻结后减小融化后增大。     

典型温带针阔叶混交林碳收支对温度的响应特征

森林生态系统是一个庞大的碳储备系统,在当前气候变暖条件下,温度变化会对森林生态系统的碳收支过程产生重要影响。该文选择长白山温带针阔混交林森林生态系统（CBS）作为研究对象,利用多年通量及小气候观测资料分析该生态系统碳收支过程对温度的响应特征,结果显示该温带森林碳交换的季节变化特征十分明显。生态系统总初级生产力GPP、生态系统呼吸R_e和净生态系统碳交换NEE在2003—2008年的月平均变化显示,碳收支3个组分最大值均出现在夏季,GPP最大值出现在7月,R_e最大值主要出现在8月,NEE负方向的最大值主要出现在6月或7月,表现为碳吸收。在日尺度和月尺度对温度的响应上,GPP和R_e都是随温度（气温和5 cm土壤温度）呈显著的指数升高形式。在日尺度上和月尺度上, NEE对气温的响应皆是分段线性形式,先是随气温的上升而正向增大,表现为碳排放;当超过临界温度,随气温的继续上升而负值增大,表现为碳吸收。根据温度、GPP、R_e以及NEE的季节的变化,每年达到最大的GPP、R_e以及NEE的最适温度均不同,这表明了在气温变化的背景下,生态系统的最适温度也在随之改变,也表明了不考虑其它因素的影响,在气候变暖的背景下,长白山针阔混交林森林生态系统的GPP、R_e随气温的升高增大,而NEE随气温的升高而减小。