Soil Contributions to Blasting Effects from Case Histories
AnEmpiricalSoilLossEquation-tucson.ars.ag.gov

An Empirical Soil Loss EquationLiu Baoyuan, Zhang Keli and Xie YunDepartment of Resources and Environmental Sciences, Beijing Normal University, Key Laboratory of Environmental Change and Natural Disaster, the Ministry of Education of China,Beijing 100875, PR ChinaAbstract: A model was developed for estimating average annual soil loss by water on hillslope for cropland, which is called Chines Soil Loss Equation (CSLE). Six factors causing soil loss were evaluated based on soil loss data collected from experiment stations covering most regions of China and modified to the scale of Chinese unit plot defined. The model uses an empirical multiplicative equation, A=RKLSBET, for predicting interrill erosion from farmland under different soil conservation practices. Rainfall erosivity (R) was the product of rainfall amount and maximum intensity of 10min, and also was estimated by using daily rainfall data. The value of soil erodibility (K), the average soil loss of unit plot per rainfall erosivity, for 6 main soil types was calculated based on the data measured from unit plots and other data modified to the unit plot level. The method of calculating Kfrom soil survey data for regions without measured data was given. The slope length and steepness factors was calculated by using the equations in USLE if slope steepness is less than 11 degree, otherwise the steepness factor was evaluated by using a new seep slope equation based on the analysis of measured soil loss data from steep slope plots within China.According to the soil and water conservation practices in China, the values of bio-control, engineering-control, and tillage factors were estimated.Keywords: Chines soil loss equation, soil loss, unit plot1 IntroductionSoil loss equation is to predict soil loss by using mathematical methods to evaluate factors causing soil erosion. It is an effective tool for assessing soil conservation measures and making land use plans. Universal soil loss equation is an empirical equation developed during 1950’s that had been applied for natural resources inventory successfully in the US and revised in 1990’s. From 1980’s the process-based models for prediction of soil loss have been studied though the world, such as WEPP (Water Erosion Predict Project, Nearing et al., 1989), GUEST (Griffith University Erosion System Template, Misra and Rose, 1996), EUROSEM (the European Soil Erosion Model Morgan etal., 1998) and LISEM (Limburg Soil Erosion Model, De Roo and Wesseling, 1996). There have been many studies on soil erosion models and related experiments since 1940's, but the models were limited in local levels and difficult to expand to broad regions due to data collected without universal standard. So far there is not any soil loss equations that could be applied through China with minor errors. The objective of this study is to develop a soil loss equation used within China based on measured data from Chinese unit plots and data from many plots modified to Chinese unit plot, which is called Chinese soil loss equation (CSLE).2 Model descriptionSoil loss is a process of soil particle detachment by raindrops and then transported by runoff from the rainfall. Many factors like soil physical characteristics slope features, land surface cover etc. will influence soil loss amount, but they have interactions. It is necessary to distinct their effects on soil loss mathematically and to evaluate them on the same scale in order to improve the accuracy of the model. Unit plot is such a good method to solve the problem. The normalized data covering the China by modified to unit plot supported the development of Chines soil loss equation. In addition,22 two features of soil erosion in China are distinctive and should be considered in the equation. One issoil erosion with steep slope, and the other is the systematical practices for soil conservation during thelong history of combating soil erosion, which could be classified as biological-control, engineering-control and tillage measures. So the Chinese soil loss equation was express as followsafter the analysis of data collected from most regions of ChinaA = RKSLBET (1)where A is annual average soil loss (t/ha), R is rainfall erosivity (MJ mm/(h ha y)), K is soilerosibility (t ha h/(ha MJ mm y)), S and L are dimensionless slope steepness and slope lengthfactors, B , E , and T are dimensionless factors of biological-control, engineering-control, and tillagepractices respectively. The dimensionless factors of slope and soil conservation measures were defined as the ratio of soil loss from unit plot to actual plot with aimed factor changed but the samesizes of other factors as unit plot. Chinese soil loss equation is to predict annual average soil lossfrom slope cropland under different soil conservation practices.To evaluated factors in the equation, about 1841 plot-year data were analyzed. Of these, 214plot-year data from 12 plots and 1143 rainfall events from 14 weather stations were used to evaluaterainfall erosivity. The Chinese unit plot was determined by analyzing 384 plot size data, and about200 plot-year data from 12 plots modified to unit plot were used to evaluate erodibility for 6 types ofsoil. About 30 plot-year data from steep plots modified to unit plot was used to establish the steepslope factor equation. Other plot data was used to calculate the values of biological-control, engineering-control and tillage factors.3 Factor calculations for the equation3.1 Rainfall erosivity (R )A threshold for erosive rainfall of 12mm was estimated, close to that suggested by Wischmeierand Smith (1978), 12.7mm. After comprehensive considering the accuracy of rainfall erosivity, thedata availability and calculation simplicity, the rainfall index of a rainfall event for Chinese soil losserosion was defined. It is the product of rainfall amount (P ) and its maximum 10-min intensity (I 10),and the relationship between PI 10 and the universal rainfall index EI 30 was also estimated as follows:EI300.1773PI 10 R 20.902 (2)where E is the total energy for a rainfall event (MJ/ha), I 30 and I 10 are the rainfall maximum 30min and10min intensities respectively (mm/hr), P is the rainfall amount (mm). The annual rainfall erosivityis the sum of PI 10 for total rainfalls through the year. Actually, it is also difficult to get the rainfallevent data. To apply the weather data from weather stations covering the China, an equation functionfor estimating half-month rainfall erosivity by using daily rainfall data was developed.1010.184(n hm d d i i R P ==∑)IR 20.973 (3)where R hm is the rainfall erosivity for half-month (MJ mm/h ha), P d is the daily rainfall amount (mm)and I 10d is the daily maximum 10min rainfall intensivity (mm/h). I =1, …, n is the rainfall days withina half-month. If there is no I 10d available, R hm was also calculated by using only daily rainfall amount.1()n hm d i i R P βα==∑ (4)where α and β are fitted coefficients and other variables had the same meaning as above.Seasonal rainfall erosivity distribution could be estimated by the sum of R hm . To plot Chineseisoerodent map for estimation or interpolation of local values of average annual rainfall erosivity in23 any place, the empirical relationships by using different rainfall available data were estimated (not listed). Users can choose different equations to calculate average annual rainfall erosivity according to the data availability.3.2 Soil erodibility (K)Soil erodibility is defined as soil loss from unit plot with 22.1m long and 9% slope degree per rainfall erosion index unit (Olson and Wischmeier, 1963). Different from the US, much of soil loss was from steep slope in China. So the Chinese unit plot was defined as a 20m long, 5m wide and 15°degree slope plot with continuously in a clean-tilled fallow condition and tillage performed upslope and downslope. The suggestion of Chinese unit plot made data measured be used to evaluate K values as much as possible without large errors. Because 15° is the middle values for most plots in China. Modified data measured from both plots of less than 15° and larger than 15° to a unit plot had the relative minimum errors.Based on the K defination and Chines unit plot, soil erodibility for 6 main soil types in China was estimated. For example, the values of K for loess were 0.61, 0.33, and 0.44 t ha h/(ha MJ mm) in Zizhou, Ansai, and Lishi in Loess Plateau of China.3.3 Slope length (L) and slope steepness (S) factorsTopography is an important factor affecting soil erosion. It is significant to quantitatively evaluate the effects of topography on erosion for predicting soil loss. The effects of topography on erosion includes slope length and steepness in terms of soil-loss estimation. In soil loss equation, factors of slope length and steepenss were cited with dimensionless values. They are values of the ratio of the soil loss from the plot with actual slope steepness or slope length to that from the unit plot.The relationship between slope length and soil loss has been studied from field or lab data for a long time. Many studies showed that the soil loss per area is proportional to some power of slope length except that the values of the exponent are slightly different. For example, Zingg (1940) derived a value of 0.6 for the slope-length exponent. Musgrave (1947) used 0.35. USLE (Universal Soil Loss Equation ) published in 1965 suggested the values of 0.6 and 0.3 respectively for slopes steeper than 10% and very long slopes, and 0.5 for other conditions. In 1978, the USLE (Wischmeier and Smith, 1978) adjusted the exponent values for different cases, 0.5 for 5% slope or more, 0.4 for slopes between 3.5% and 4.5%, 0.3 for slopes between 1% and 3%, and 0.2 for slopes less than 1%. Revised USLE (RUSLE) published in 1997 used a continuous function of slope gradient for calculating slope-length exponent.Soil erosion from the steep slope is serious in China. How slope length influences soil loss on steep slopes needs further studies. For this end, the relationship between slope length and soil loss on steep slopes was examined based on the plot data obtained at Suide, Ansai, and Zizhou on the loess plateau of China and modified to the unit plot. The results indicated that the slope-length equation in the RUSLE could not be used for soil loss prediction under the steep slope conditions. The equation for calculating soil length factor in the USLE published in 1978 could be applied into China:22.13mLλ=(5)where λ is slope-length (m), m is the slope length exponent.Slope gradient is another topographical factor affecting soil erosion. Most studies have shown that the relation of soil loss to gradient may be expressed as some exponential function or quadratic polynomial. Zingg (1940) concluded that soil loss varies as the 1.4 power of percent slope, and Musgrave (1947) recommended the use of 1.35. Based on a substantial number of field data, Wischmeier and Smith (1965) derived a slope-gradient equation expressed as quadratic polynomial function of gradient percent. Having analyzed the data assembled from plots under natural and simulated rainfall, McCool et al., (1987) found that soil loss increased more rapidly from the slopes24 steeper than 5° than that from slopes less than 5°, and he recommended two different slope steepnessfactor equations for different ranges of slopes:S =10.8sin θ + 0.03 θ 5° (6-1)S =16.8 sin θ – 0.5 θ > 5°(6-2) These equations were established based on soil loss data from gentle slopes, and have not beentested for steep slope conditions. We used soil loss plot data from Suide, Ansai, and Tianshui on theloess plateau of China to test the equations. The results showed that great errors were produced whenusing equations suggested by McCool et al ., (1987) for predict soil loss from slopes steeper than 10°. After the slope degree was larger than 10°, soil loss from steep slopes increased ripedly. Based theregression analysis of our data, am equation to calculate slope steepness factor for seep slopes wasdeveloped:S =21.91 sin θ – 0.96 θ10°(6-3)So in Chinese soil loss equation, slope steepness factor could be estimated by using equation (6-1)to (6-3) under different slope conditions3.4 Bilogical-control (B ), engineering-control (E ), and tillage (T ) factorsDuring the development of the historical agriculture traditions in China, the systematical practicesfor soil and water conservation formed. They could be divided into three categories: biological-control, Engineering-control and tillage measures. Biological-control practices include theforest or grass plantation for reducing runoff and soil loss. Engineering-control practices refer to thechanges of topography to reduce runoff and soil loss by engineering construction like terrace, check-dams. Tillage practices are the measures taken by farmland equipment. The difference between engineering and tillage is that the latter does not change the topography and is only applied onthe farmland.Table 1 Estimated values of biological-control factor for cropsSeedbed Establishment Development Maturing crop Growing season Annual averageBuckwheat 0.71 0.54 0.19 0.21 0.74 0.74 Potato 1.00 0.53 0.47 0.30 0.47 0.50 Millet 1.00 0.57 0.52 0.52 0.53 0.55 Soybean 1.00 0.92 0.56 0.46 0.51 0.53 Winter wheat 1.00 0.17 0.23Maize intercropping with soybean1.00 0.40 0.26 0.03 0.28 Hyacinth Dolichos 1.00 0.70 0.46 0.57Table 2 Estimated values for factors of woodland and grassland vegetationSophora Korshinsk Peashrub Seabuckthorn Seabuckthorn & PoplarSeabuckthorn & Chinese Pine Erect Milkvetch Sainfoin Alfalfa First year Sweetclover Second year Sweetclover0.004 0.054 0.083 0.144 0.164 0.067 0.160 0.256 0.377 0.08325Many studies gave the B values for different biologic measures in China, but they were not from the universal calculated methods and could not be used directly in soil loss equation. Based on the defination of B values, the ratio of soil loss from plots with some biological-control practice to that from unit plot, we calculated B values for some types of biological-control practices (Table 1). Some values for typical engineering-control and tillage measures in China were summarized (not listed).References[1] Nearing, M.A., G.R. Foster, L.J. Lane, and S.C. Finkner. A process-based soil erosion modelfor USDA-water erosion prediction project technology. Transactions of The ASAE, 1989, 32(5):1587-1593.[2] Misra R K, Rose C W. Application and sensitivity analysis of process -based erosionmodel—GUEST[J]. European Journal Soil Science. 1996,10:593-604.[3] Morgan R P C, Quinton J N, Smith R E, et al., The European soil erosion model (EUROSEM): Adynamic approach for predicting sediment transport from fields and small catchments[J]. Earth Surface Processes and Landforms, 1998,23:527-544.[4] De Roo A P J. The LISEM project: an introduction. Hydrological Processes. 1996, vol.10:1021-1025.[5] Wischmeier W H, Smith D D. Predicting rainfall erosion losses[R]. USDA AgriculturalHandbook No.537. 1978.[6] Olson,T.C., and Wischmeier,W.H. 1963. Soil erodibility evaluations for soils on the runoff anderosion stations. Soil Science Society of American Proceedings 27(5):590-592.[7] Zingg A W. Degree and length of land slope as it affects soil loss in runoff[J]. AgriculturalEngineering, 1940,21: 59-64.[8] Musgrave G W. The quantitative evaluation of factors in water erosion A first approximation[J].Journal Soil and Water Cons, 1947, 2:133-138.[9] Renard K G,Foster G R,Weesies G A et al., RUSLE―A guide to conservation planning with therevised universal soil loss equation[R]. USDA Agricultural Handbook No.703. 1997.[10] McCool, D. K. Brown, L.C., Foster, G. R., et al., Revised slope steepness factor for theuniversal soil loss equation. TRANSACTIONS of the ASAE, 1987, 30(5): 1387-1396.。
土壤侵蚀敏感度计算

土壤侵蚀敏感度计算英文回答:Soil erosion sensitivity is a measure of the susceptibility of a soil to erosion. It is determined by a number of factors, including the soil's texture, structure, organic matter content, and slope. Soils with a high erosion sensitivity are more likely to be eroded by wind and water, while soils with a low erosion sensitivity are less likely to be eroded.There are a number of different methods for calculating soil erosion sensitivity. One common method is the Revised Universal Soil Loss Equation (RUSLE), which is used to estimate the average annual soil loss from a given area of land. RUSLE takes into account the soil's texture, structure, organic matter content, slope, and rainfall erosivity.Another common method for calculating soil erosionsensitivity is the Soil Erosion Potential (SEP) index, which is used to estimate the potential for soil erosion on a given area of land. SEP takes into account the soil's texture, structure, organic matter content, slope, and land use.Soil erosion sensitivity is an important factor to consider when planning land use activities. Areas with a high erosion sensitivity should be managed carefully to prevent soil erosion. This can be done by using conservation practices such as terraces, contour farming, and cover crops.中文回答:土壤侵蚀敏感性是指土壤对侵蚀的敏感程度。
Soil Contamination EP博士讲座

The case for China - Overall
• Soil pollution comes mainly from mining and industrial activity. China’s 30 years of rapid economic growth have inevitably caused many environmental problems. Europe and the US saw the same thing during their periods of quick growth.
• B-horizon /(subsoil): less organic material & fewer organisms than A- horizon.
• C-horizon: consists of broken-up bedrock, does not contain any organic materials. Chemical composition helps to determine pH of soil & also influences soil’s rate of water absorption & retention.
The contaminated soil reached about 10.500.000 hectares(公顷). The soil contaminated resulting from sewage irrigation was 2.275.000 hectares, and the soil stockpiled and ruined by solid waste was 140.000 hectares. These covered 10% of the total cultivated area. As different kinds of industrial wastewater, exhaust gas, livestock manures, sewage irrigation and sludge farm application have all become the sources of heavy metals.
市政垃圾堆肥对巴西土壤的化学效应

Bioresource Technology 98 (2007) 525–5330960-8524/$ - see front matter © 2006 Elsevier Ltd. All rights reserved.doi:10.1016/j.biortech.2006.02.025Composted municipal waste e V ects on chemical propertiesof a Brazilian soilD.V. Pérez a,¤, S. Alcantara b , C.C. Ribeiro b , R.E. Pereira b , G.C. Fontes b , M.A. Wasserman c ,T.C. Venezuela d , N.A. Meneguelli a , J.R. de Macedo a , C.A.A. Barradas eaEmbrapa-Solos, R. Jardim Botânico, 1024, Rio de Janeiro (RJ), BrazilbInstituto de Química, UFRJ, Av. Brig. Trompovsky, s/no, Cidade Universitária, Rio de Janeiro (RJ), Brazil cInstituto de Radioproteção e Dosimetria/CNEN. Av. Salvador Allende s/no, Recreio, Rio de Janeiro (RJ), BrazildFiocruz/ENSP, R. Leopoldo Bulhões, 1480, Rio de Janeiro (RJ), 21041-210, Brazil ePESAGRO-RIO, R. Euclydes Solon Pontes no 30, Nova Friburgo (RJ), 28.625-020, BrazilReceived 4 January 2004; received in revised form 12 January 2006; accepted 7 February 2006Available online 31 March 2006AbstractThe spread of composted municipal waste (CMW) on land can be used for sustainable crop production. Nevertheless, heavy metals availability may be a problem. Therefore, the main objective of this study was to assess the impact of CMW disposal on heavy metal accu-mulation in soil and plants. The treatments consisted of an untreated plot (control) and four rates of CMW application. All plots were cultivated in succession of carrot, cauli X ower, sweet corn, and radish. Cu and Pb signi W cantly accumulated in the topsoil (0–5cm) with a similar pattern in the depths of 5–10cm and 10–20cm. Cauli X ower, for Fe and Cu, and radish, for Pb and Cu, had their tissue analysis sig-ni W cantly a V ected due to the increasing rates of application of CMW. Nevertheless, the levels of accumulation in both, soil and plant, are within permissible limits. The evidences provided by this experiment indicated that heavy metals are less likely to cause problems for the estimation of CMW loadings to Brazilian agricultural land.© 2006 Elsevier Ltd. All rights reserved.Keywords:Municipal waste; Biosolid; Heavy metals; Soil properties1. IntroductionMunicipal solid waste has been a serious environmental problem for many cities in developing countries (Abdel-Sabour and Abo El-Seoud, 1996; Soumaré et al., 2003). For instance, Rio de Janeiro, the second largest city in Brazil,has shown over the last years a signi W cant increase of solid waste handling. From 1995 to 2002, the total waste col-lected and the average waste collected per day increased from 2.6 to 3.6 million tons and 7.0 to 9.9 thousand tons,respectively.In spite of the fact that there are many kinds of W nal disposal available, the agricultural practice of amending soils with composted municipal waste (CMW) has received worldwide attention. This compost is rich in organic matter and its use may improve soil fertility and physical proper-ties (He et al., 1992; Oshins, 1995; Anikwe and Nwobodo,2002). However, repeated compost application can lead to accumulation of trace metals in soils that could eventually contaminate human and other animal food chains (Garcia et al., 1992; Pinamonti et al., 1997; National Research Council, 2003).There are currently no standards to evaluate compost quality in Brazil. Only Paraná and São Paulo states have set up guidelines based on the criteria for sludge (Sanepar,1997; CE TE SB, 2001). Hence, there is a need to develop*Corresponding author.E-mail address: daniel@cnps.embrapa.br (D.V. Pérez).526 D.V. Pérez et al. / Bioresource Technology 98 (2007) 525–533general standards for land application of urban waste. Our objectives were to determine: (i) the e V ect of CMW applica-tion on the heavy metal composition of four vegetable crops and (ii) the residual e V ects of this soil amendment on chemical properties of a Brazilian soil.2. MethodsAll the composted municipal waste used during this study was taken from the largest treatment plant (Caju) of Rio de Janeiro State, and it was applied from 1995 to 1997to a soil (Dystrochrept) located in Nova Friburgo County (22°15ЈS and 42°45ЈW), a representative mountain area of intensive vegetable production. The Köppen climate classi-W cation is Cwb with mean annual temperature of 18°C and mean annual precipitation of 1431mm. In Caju plant, recy-clable materials such as paper, glass and aluminum cans are manually removed early in the composting process. The remaining material is ground and the ferrous materials are separated using an electromagnet. The remaining organic waste is sieved and arranged into rows of long piles, and aerated by turning the pile periodically with mechanical means. Generally, 77–90 days are necessary to complete the composting.Some characteristics of the soil used in this study are presented in Table 1. The experimental W eld design was a randomized complete block, consisting of an untreated plot (control) and four rates of CMW surface application (12.5,25, 50, 100t ha ¡1, wet basis) and four blocks. No inorganic fertilizer was applied. Irrigation was also applied so as to keep soil moisture in the range of W eld capacity. Each plot had a total area of 4.0£2.4m 2 separated in all directions by a border of 1m. All plots were cultivated with the following crop succession: carrot, planted on November 22nd 1995and harvested on April 2nd 1996; cauli X ower, planted on May 23rd 1996 and harvested on September 5th 1996;sweet corn, planted on December 10th 1996 and harvested on April 10th 1997; and radish, planted on August 20th 1997 and harvested on October 21st 1997. These species were selected due to the fact that they present di V erent edi-ble plant parts (root, X ower, seed) and, consequently, di V er-ent nutrient uptake paths (Farago, 1994). They are also sensitive crops for di V erent metal toxicities (Alloway, 1990;Fergusson, 1990; Kabata-Pendias and Pendias, 1992).Rotary tilling was used in order to prepare the soil since it mixes the upper layers of soil rather than completely turn-ing the soil over. In the present study, tillage went to the W rst 15cm of the soil. Moreover, the direction of the rotary tilling was inverted after each cultivation so as to avoidplot-to-plot contamination. The compost treatments were super W cially applied in the same day of planting. Hence, a total amount of 50, 100, 200, and 400t ha ¡1 CMW was applied during the experiment. After the W rst year of the last CMW spread (1998), soil samples were collected from four depths (0–5, 5–10, 10–20, 20–40cm). The samples were dried in a forced air oven at 40°C, passed thorough a 2-mm sieve and stored in a polyethylene bag. Vegetable edible parts were rinsed with distilled water, after that they were dried at 70°C and ground in a stainless steel Wiley mill in order to pass a 1mm sieve. Ground samples were stored at room temperature in acid-washed polyethylene containers.Aqua regia (HCl/HNO 3, 3:1) extraction is used in order to evaluate anthropogenic inputs of heavy metals and it is rather e Y cient (Hani, 1996; Walter and Cuevas, 1999;Scancar et al., 2000). Hence, this method was applied for soil and compost evaluation of Fe, Mn, Zn, Cu, Cd, Cr, Pb,and Ni. Therefore, considering the accumulation of some metals observed in the 0–5cm, a sequential extraction method (Wasserman et al., 2005; Table 2) was used in order to specify the types of metal associations in soil.Dried plant samples were digested with a nitric/perchloric acid mixture. The content of the selected metals was ana-lyzed by ICP-OE S (Perkin–E lmer OPTIMA 3000, Nor-walk, CT, USA). Duplicate analyses of each soil and plant extractions were performed throughout the work as well.The humic fractions of the soil were sequentially extracted according to Kononova and Bel’Chikova (Sastri-ques, 1982). In short, the free fulvic acids (not bound) were obtained by shaking 20–40g of soil (air dried, 2mm-sieved)Table 1Some physical and chemical characteristics a of the soil used in the experimentaDetermined according to the procedures of EMBRAPA (1997).Horizon Depth (cm)Clay (g/kg)pH (H 2O)Ca 2++Mg 2+ (cmol c /kg)K + (cmol c /kg)Al 3+ (cmol c /kg)CEC (cmol c /kg)P (mg kg ¡1) C (g/kg)N (g/kg)Ap 0–20330 6.0 3.6 1.10.840.011.125114.80.22Bi120–45390 5.20.80.120.612.03418.00.25Bi245–70380 5.10.70.070.69.03418.40.25Table 2Procedure of the sequential extraction scheme used to fractionate heavy metals in soil samples FractionSequence of extraction(F1)HAc (2M)+NaAc (2M) 1:1; pH 4.7Exchangeable +carbonate bound Room temperature/16h(F2)NH 2OH ·HCl (0,1M); pH 2 (HNO 3)Fe & Mn oxide bound Room temperature/16h (F3)H 2O 2 (30%)+HNO 3(0.02M)+NH 4Ac (1M)Room temperature/16h Organically bound (F4)NaOH (0.1M); pH 12Al oxide +strong Fe &Mn oxide bound Room temperature/16h (F5)Aqua regia (HNO 3/HCl; 1:3)Residual50°C/30minD.V. Pérez et al. / Bioresource Technology 98 (2007) 525–533527with 200mL H 3PO 4 2M for 30min. After that, the sample was centrifuged at 1000rpm for 30min and it was also W ltered. This procedure was repeated 3 times. The residual soil was washed 3 times with demineralized water and it was shaken with 200mL Na 4P 2O 7 0.1M +NaOH 0.1M for 4 hours. Following centrifugation (3000rpm/30min) the supernatant solution (humic +fulvic acids) was separated.This procedure was repeated 3 times as well. The residual soil was used so as to determine the C content of the humin fraction. An aliquot of the supernatant was acidi W ed with H 2SO 4 to pH 1.0 and, then, centrifuged (1500rpm/5min)in order to separate the precipitated humic acid from the supernatant fulvic acid. The carbon content of each frac-tion was determined by dichromate oxidation.Suprapur acids (Merck, Darmstadt, Germany) and ultrapure water (Barnstead Ultrapure Water System,Dubuque, IA, USA) were used in all laboratory procedures.All containers were soaked in 10% HNO 3 and thoroughly rinsed in demineralized water before being used.An analysis of variance was used in order to test sig-ni W cance (P <0.05) of treatment e V ects and Tukey’s test (P <0.05) was used so as to compare the means. All stat-istical analyses were performed using Statistical Analysis System (SAS, 1999).3. Results and discussion3.1. Chemical composition of the CMWIn spite of the fact that there are currently no Brazilian standards in order to evaluate compost quality, the results (Table 3) agree well with the scarce data of chemical analy-sis of Brazilian CMW. Grossi (1993), during 1990 and 1991,analyzed 61 samples of CMW from 16 Brazilian cities. She found a large range of heavy metal concentrations varying with the maturity degree of the compost (Table 4). Based on it, our results match most of the ranges in heavy metals which were related to the mature compost that we used (Tables 3 and 4). Our results also match the ranges of heavy metals found by Cravo et al. (1998) during their study of the compost produced by six Brazilian waste plant treat-ments (Tables 3 and 4). Considering the main international legislation on the disposal of biosolids in agriculture (USE PA 40 CFR Part 503 and Council Directive 86/278/EEC), we realized that, all the metal contents determined in the present study were under the regulation limits (Tables 3and 4). Notwithstanding, some countries in E urope have more restricted laws (Table 4). In that case, the CMW employed in the present work failed to match the limitTable 3Some chemical analyses of the CMW used as amendment for the cultivation of the four vegetables in BrazilaWet basis. Relative standard deviation lower than 10% for all analyses.Vegetable crop pH Moisture (g kg ¡1)a C(g kg ¡1)N (g kg ¡1)C:N Fe (£103)(mg kg ¡1)Mn (mg kg ¡1)Cu (mg kg ¡1)Cd (mg kg ¡1)Co (mg kg ¡1)Cr (mg kg ¡1)Ni (mg kg ¡1)Pb (mg kg ¡1)Carrot7.7407.2158.715.21012.6240.2384.4 2.0 2.064.128.8189.0Cauli X ower 7.7484.6162.015.4119.3198.2170.5 1.4 1.656.217.1151.0Sweet corn 7.8440.8130.916.289.6203.0248.0 1.5 1.854.029.1153.0Radish7.7173.8154.717.8921.6336.2119.8 1.7 2.541.020.384.0Table 4Some chemical analyses of the CMW produced in Brazilian cities compared with various international regulation limits for biosolids disposal in agricul-ture a Cravo et al. (1998), mean and standard deviation, in parenthesis.b Grossi (1993) for mature compost.c Grossi (1993) for semi-mature compost.d Grossi (1993) for raw compost.e USEPA (1994) for Exceptional Quality biosolid.f Long (2001) for grade B biosolid.gEuropa (2005).Source Fe (£103) (mg kg ¡1dry-matter)Mn (mg kg ¡1dry-matter)Cu (mg kg ¡1dry-matter)Cd (mg kg ¡1dry-matter)Co (mg kg ¡1dry-matter)Cr (mg kg ¡1dry-matter)Ni (mg kg ¡1dry-matter)Pb (mg kg ¡1dry-matter)Brazil a23.3304229 2.810.889.832238.9(13.7)(132)(266)(1.7)(4.9)(45.1)(27)(166.4)Brazil b 11–23–61–2330.1–0.576–10420–3144–342Brazil c 103–572–72–29910.3–12.860–27819–7857–1272Brazil d 88–252–64–19700.7–4.533–13317–3844–274USA e––150039–1200420300Australia f ––250020500–3000270420EuropeanCommunity g ––1000–175020–40––300–400750–1200France g ––1000151000200800Germany g ––80010900200900Netherlands g ––75 1.257530100Sweden g600210050100528 D.V. Pérez et al. / Bioresource Technology 98 (2007) 525–533concentrations of Cu, Cd and Pb related to The Nether-lands and Pb to Sweden laws. Concerning only the four applications of the CMW used in the experiment, we have observed that there were some variations of trace metals content (Table 3). However, they were probably related to seasonal variations in raw input of the collected municipal waste.The contents of trace metals found in the compost were much higher than in the agricultural soil used (Table 5) for Cu, Cr, and Pb. However, the concentrations of Fe, Mn,Cd, and Co were higher in the soil and the results for Ni varied. The outcomes concerning heavy metal accumula-tion in soil will be discussed in a coming section.No negative e V ect was observed due to the increasing application of compost rates in the yield of the four culti-vated vegetables (Fig.1). Hence, the CMW used seemed to have no phytotoxicity e V ect.3.2. Plant analysisNo Cd was detected in the analyzed tissues (Table 6).Depending upon the tissue, there were some other elements,among those determined, which were below limit detection.In that case, they were not shown (Table 6). The e V ect of the compost on the uptake of trace metals analyzed is apparently insigni W cant for carrot and sweet corn. For cau-li X ower, Fe and Cu uptakes decreased after the application of higher rates of CMW. However, Cu and Pb uptakes for radish have increased, although, in the case of Cu, it occurred only with the highest amount of compost applica-tion (Table 6).When compared to other studies dealing with metal absorption from crops amended with CMW, our resultsshow a di V erent trend. Fritz and Venter (1988) studied, in a greenhouse experiment, the heavy metal uptake behavior of lettuce, spinach, carrot, radish, bush bean, and tomato, all of them were grown successively. Their results of leaf analy-sis, averaged over all species, indicated that Zn, Cu, and Pb increased signi W cantly due to the higher compost rates used.Cd, Cr, and Ni did not show any signi W cant variation. Root crops had shown a signi W cant increase of Zn. However,only carrot roots exhibited a considerable increase of Pb and Cr contents. Fruit crops have shown signi W cant di V er-ences for Zn, Ni, Cd, and Cr, but only for the intermediate CMW doses. Costa et al. (1994) observed, in a greenhouse experiment with lettuce, increased Zn, Cu, Cd, and Pb leaf contents with increasing compost rates. Abdel-Sabour and Abo El-Seoud (1996) observed, in sesame seeds, an increase of Pb and Cd concentrations with CMW treatments in rela-tion to the control. Pinamonti et al. (1997) found a signi W -cant increase in Ni and Cr in the leaves and fruits of an apple orchard, but only for the highest doses of CMW.Costa et al. (1997) observed in a greenhouse experiment that compost application had enhanced Zn, Cu, and Cd accumulation on dry-matter of carrot leaves and roots.The marked heterogeneity among the studies cited above and also to those found in the present work is probably related to the fact that they were dealing with di V erent plant species under di V erent and speci W c soil conditions (Fritz and Venter, 1988; Kabata-Pendias and Pendias,1992; Pais and Jones, 1997).Based on data given in Table 6 and according to Kabata-Pendias and Pendias (1992), it is possible to a Y rm that there was no metal concentration above the level considered critical for plant tissues in general. However,our results must be viewed cautiously. The experiment with composted waste endured two years only, and in some treatments a very high rate of CMW (400t ha ¡1) was employed. Consequently, we are not able to state whether any drawback would come out if CMW was used for more than two years, especially when it comes to such high rates of CMW.3.3. Soil analysis3.3.1. “Total” metal concentrationSoil contents and variabilities (Table 7) were within the range considered normal in soils (Kabata-Pendias and Pen-dias, 1992; Pais and Jones, 1997), corroborating the fact that no phytotoxicity e V ect was found by the application ofTable 5Metal concentrations of the soil at the experimental site in Nova Friburgo county (Brazil) before the application of compost waste treatments Relative standard deviation lower than 10% for all analysis.Depth (cm)Mn (mg kg ¡1dry-matter)Fe (£103) (mg kg ¡1dry-matter)Cd (mg kg ¡1dry-matter)Co (mg kg ¡1dry-matter)Cr (mg kg ¡1dry-matter)Cu (mg kg ¡1dry-matter)Ni (mg kg ¡1dry-matter)Pb (mg kg ¡1dry-matter)0–5401.040.7 2.418.323.517.820.323.95–10388.639.7 2.319.022.017.721.722.710–20396.641.1 2.121.122.917.221.923.520–40388.530.82.522.122.814.120.314.7D.V. Pérez et al. / Bioresource Technology 98 (2007) 525–533529CMW (Fig.1). The e V ect obtained with the studied treat-ments on the aqua regia (“Total”) heavy metal content,concerning the soil upper layer (0–5cm) can be related to the amounts of each element introduced by the CMW.Hence, the applied composts have led to a great input of Cu, Cr, and Pb in the original soil (Tables 4 and 5), which caused an important increase in the “Total” concentration of these elements in the soil (Table 7). The “Total” Co con-tent has consistently decreased in virtue of an increase in the amount of CMW (Table 7), due to the fact that the Co content of CMW was lower than the soil Co concentration (Tables 4 and 5). In the case of Fe and Mn, although the same pattern of di V erence between soil and CMW concen-trations occurred, similar to the Co, the soil content is in an order of magnitude higher where the dilution by the CMW application is insigni W cant. The concentration of Ni in both the soil and in the CMW did not di V er signi W cantly.As a consequence, there was no signi W cant variation due to CMW application. Cabrera et al. (1989) and Pinamonti et al. (1997) observed that relationship between the soil and CMW heavy metal concentration so as to predict the soil accumulation of these elements.Data for “Total” contents of all studied metals with depth were similar to the corresponding 0–5cm layer, with the exception of the layer below 20cm. That is, Pb and Cu concentrations have increased signi W cantly after CMW application and the levels of the other metals have shownno signi W cant variation. The exception was Cr, since there was no signi W cant di V erence of its content between the 5–10and the 10–20cm layers. However, it is possible to say that numerically, the Cr content increased when higher levels of CMW were applied. Hence, the increase of Pb and Cu concentrations, associated with the higher rates of CMW application, in the layers 0–5cm, 5–10cm and 10–20cm probably resulted from the e V ect of mixing caused by roto-tilling the soil to a depth of 15cm. Data from Co seems to corroborate this. The dilution observed in the 0–5cm depth,caused by the lower concentration of Co present in CMW than in the soil, occurred also in the 5–10cm depth. At the depth of 20–40cm, except for Cr and Ni, most of the metal contents were una V ected by the treatments. The signi W cant di V erence found for Cr at the depth of 20–40cm was consis-tent with the trend observed for 5–10, and 10–20cm layers,although, in that case, it was not statistically signi W cant.The results for Ni showed a slightly low value for the 50t ha ¡1 CMW application, which a V ected the statistical mean test.3.3.2. Sequential extractionBesides soil-to-plant transfer of heavy metals, direct ingestion of soil by humans and animals are important pol-lutant transport pathways to be considered for land appli-cation of biosolids (Ryan and Chaney, 1994; Iskandar and Kirkham, 2001; National Research Council, 2003). SinceTable 6Concentration of trace metals in the tissue of four vegetables grown at di V erent rates of composted municipal waste (CMW) application Values in the same line for the same sample followed by the same letter are not signi W cantly di V erent as determined by Tukey’s test (P <0.05).aDry matter basis.bCoe Y cient of variation from the analysis of variance.mg/kg ¡1a CMW rate (t ha ¡1)CV b (%)0.012.525.050.0100.0Carrot (root)Fe 269.05a 219.38a 257.35a 259.95a 251.65a 32Mn 14.13a 16.01a 14.01a 11.67a 14.08a 36Cu 7.50a 6.96a 8.21a 7.42a 8.81a 19Cr0.37a 0.31a 0.38a 0.38a 0.39a 20Cauli X ower (X ower)Fe 101.80a 81.20ab 58.55bc 47.40c 53.23bc 26Mn 14.23a 14.50a 12.50a 12.22a 11.52a 11Cu 2.77a 2.25b 2.02b 2.08b 2.08b 10Co0.63a 0.63a 0.62a 0.68a 0.64a 17Sweet corn (seed)Fe 30.12a 26.34a 29.78a 29.32a 28.72a 31Mn 7.38a 8.96a 6.62a 6.36a 8.70a 22Cu 1.75a 1.93a 1.60a 1.78a 1.45a 14Cr 0.12a 0.14a 0.12a 0.14a 0.15a 26Ni 0.59a 0.37a 0.52a 0.57a 0.49a 75Pb0.37a 0.92a 0.50a 0.55a 0.81a 70Radish (root)Fe 2776.25a 2334.96a 3070.42a 2105.42a 3583.75a 47Mn 30.06a 28.94a 38.04a 24.72a 42.91a 39Cu 3.14b 5.20b 6.68b 5.53b 14.58a 50Ni 3.55a 2.11a 2.41a 2.25a 4.33a 57Co 3.40a 1.65a 2.41a 2.14a 2.84a 51Pb1.14b1.65ab3.39ab2.48ab7.24a79530 D.V. Pérez et al. / Bioresource Technology 98 (2007) 525–533most of the above processes occur in the upper layer of soil,only the results for the 0–5cm layer will be discussed here.It has been shown that contrary to the determination of the total content of any heavy metal in soil, chemical frac-tionation may provide more useful information concerning the mobility and bioavailability of heavy metals in soil (Tack and Verloo, 1995; Quevauviller, 1998). Sequential extraction procedures allow this fractionation by assuming that di V er-ent extracting solutions, applied in a speci W c sequence, will act on di V erent species or binding forms in the soil (Verloo and Eeckhout, 1990; López-Sánchez et al., 2002). The bind-ing form in the solid phase of the soil is related to the inten-sity of metal release to the liquid phase and hence likelihood of mobilization and bioavailability (Tack and Verloo, 1995).In the fractionation scheme used in this work (Table 2),fractions 1–3 are more likely to represent the equilibrium between the liquid and solid phases than fractions 4 and 5which are presumed to be the more structurally bound ele-ments occluded in Fe and Mn oxides, strongly adsorbed to Al oxides or residual forms of silicates.The concentrations of Fe, Mn, Cu, Cd, Ni, and Pb in the W ve fractions resultant from all treatments are presented in Fig.2. E xcept for Cu, most of the extracted metals were associated with the residual fraction (F5). The distribution of Cu was di V erent from that of other heavy metals. The organically bound fraction (F3) concentrated most of theCu analyzed in all treatments and the amount of Cu in F3has increased signi W cantly with increasing rates of CMW application. Although the other fractions were extracted in lower proportions, a signi W cant increase in the carbonate/exchangeable and the Al oxide +strong Fe/Mn oxide-bound fractions (F1 and F4, respectively) was observed towards the higher CMW applications. As it can be seen in Fig.2, despite the large amount of the residual fraction,Mn, Pb, and Cd also showed a signi W cant increase in the carbonate/exchangeable fraction (F1) with increasing CMW rates. The organically bound fraction (F3) has sig-ni W cantly increased for Pb and Cd as well.3.3.3. Humic fractionsRototilling the soil with no amendment application (0t ha ¡1) changed the humus composition signi W cantly com-pared to the soil before the experiment started (Table 8). The non-humic fraction (NHC) decreased, because the minerali-zation of the organic matter increased. The lowering of the total organic carbon (TOC) content corroborates this obser-vation (Table 8). The concentration of fulvic acids (FA)slightly increased as a consequence of this process of miner-alization. With the application of higher rates of CMW, the NHC content decreased, and, in the case of the 50t ha ¡1application, it was almost not detected. These results corrob-orate the W ndings of Kononova (1984) that soil cultivationTable 7Trace metal concentration of the soil one year after the growth of the four vegetables amended with composted municipal waste (CMW)Values in the same line for the same sample followed by the same letter are not signi W cantly di V erent as determined by Tukey’s test (P <0.05).aCoe Y cient of variation from the analysis of variance.CMW rate (t ha ¡1)Fe (£103) (mg kg ¡1)Mn (mg kg ¡1)Cu (mg kg ¡1)Cd (mg kg ¡1)Co (mg kg ¡1)Cr (mg kg ¡1)Ni (mg kg ¡1)Pb (mg kg ¡1)0–5cm 0.032.6290.711.4d 1.917.2ab 15.7b 17.519.2c 12.536.9314.220.7c 2.418.5a 21.6ab 21.226.9c 25.032.7299.724.6c 1.916.2ab 20.9ab 18.628.5c 50.035.6343.942.1b 2.416.5ab 27.1a 22.146.7b 100.033.9298.860.9a 2.512.5b 29.1a 21.260.2a CV (%)a129182131614145–10cm 0.035.2297.215.7c 1.816.5ab 17.717.423.0b 12.536.2300.017.6bc 2.416.8ab 19.419.924.9b 25.033.1317.416.0c 1.817.2a 18.318.029.8ab 50.036.4328.533.2ab 2.416.5ab 29.521.437.8ab 100.033.1290.546.4a 2.213.1b 26.018.147.4a CV (%)101128231123232510–20cm0.034.5313.216.0b 1.817.119.419.425.6ab 12.537.8304.116.7b 2.517.019.218.622.7b 25.028.6278.513.1b 2.415.816.018.118.9b 50.036.0326.027.5ab 2.218.322.619.533.5ab 100.032.9292.235.0a 2.116.121.918.137.6a CV (%)141630201720202420–40cm0.030.4308.210.6 1.617.415.3ab 18.2a 14.912.533.127712.1 2.416.015.8ab 15.4ab 15.925.032.2318.111.0 1.817.215.7ab 15.9ab 20.050.030.4273.09.9 1.816.613.3b 12.0b 15.5100.031.4278.914.8 1.816.819.1a 15.1b 20.2CV (%)14827228141132D.V. Pérez et al. / Bioresource Technology 98 (2007) 525–533531decreased the non-humic content of soil organic matter. In that case a slight increase of the humic acid fraction (HA)occurred, and, as a consequence, the fulvic acid content diminished. However, the most important e V ect observed was the increase of the humin fraction over the sum of the humic and fulvic acid fractions. This pattern was reportedTable 8Humic fractions extracted from the soil one year after the growth of the four vegetables amended with composted municipal waste (CMW)In parenthesis, results in percentage of the total organic carbon (TOC).aBefore cultivation, at the start of the experiment.CMW (t ha ¡1)Organic C in the humic fractionsTOC (g kg ¡1)FA free (g kg ¡1)FA bound (g kg ¡1)FA total (g kg ¡1)HA (g kg ¡1)Humin (g kg ¡1)FA +HA +humin (g kg ¡1)0.025.00.20 (8.0)0.19 (7.6)0.39 (15.6)0.12 (4.8) 1.78 (71.2) 2.29 (91.6)12.529.50.21 (7.1)0.20 (6.8)0.41 (13.9)0.15 (5.1) 2.12 (71.9) 2.68 (90.8)25.026.40.22 (8.3)0.10 (3.8)0.32 (12.1)0.16 (6.1) 1.93 (73.1) 2.41 (91.3)50.032.10.21 (6.5)0.15 (4.7)0.36 (11.2)0.21 (6.5) 2.63 (81.9) 3.20 (99.7)100.036.70.22 (6.0)0.16 (4.4)0.38 (10.4)0.23 (6.3) 2.92 (79.6) 3.53 (96.2)Control a35.20.28 (8.0)0.15 (4.3)0.43 (12.2)0.23 (6.5)1.80 (51.1)2.46 (69.9)。
宿州市耕地土壤养分时空变化特征分析

Temporal and spatial characteristics of soil nutrients in cultivated land in Suzhou CityDING Qixun 1,ZHAN Xuejie 1,ZHANG Tian′en 1,XU Nuo 2,MA Xiuting 3,ZHANG Changkun 3,MA Youhua 1*(1.Key Laboratory of Farmland Ecological Conservation and Pollution Control of Anhui Province,College of Resources and Environment,Anhui Agricultural University,Hefei 230036,China;2.Suzhou Agriculture and Rural Affairs Bureau,Suzhou 234000,China;3.Anhui Huacheng Seed Co.,Ltd.,Suzhou 234000,China )Abstract :Analyzing the temporal and spatial evolution of soil nutrients is a prerequisite for implementing precision agriculture and sustainable soil management.The spatial and temporal variation characteristics of soil organic matter,total N,available P,and available K in arable soil in Suzhou City in 2010and 2019were analyzed by inverse distance weighted spatial interpolation analysis method.The results showed that the soil nutrients of arable soil in Suzhou increased slightly in 2019compared with 2010.The soil organic matter of arable soil was relatively scarce in Dangshan County,Xiaoxian County,and Sixian County,and abundant in the middle towns of YongqiaoDistrict,with an average value of 17.95g·kg -1,an increase of 6.15%.The area with intermediate soil organic matter content accounted for76.00%of the total cultivated land area;the soil total N content was the same,with an average value of 1.06g·kg -1.The area with medium宿州市耕地土壤养分时空变化特征分析丁琪洵1,詹雪洁1,张天恩1,许诺2,马秀婷3,张长坤3,马友华1*(1.农田生态保育与污染防控安徽省重点实验室,安徽农业大学资源与环境学院,合肥230036;2.宿州市农业农村局,安徽宿州234000;3.安徽华成种业股份有限公司,安徽宿州234000)收稿日期:2021-11-26录用日期:2022-03-02作者简介:丁琪洵(1997—),女,江苏泰州人,硕士研究生,主要从事耕地质量评价与提升研究。
广东鹤山火烧迹地植被恢复后土壤养分含量变化

广东鹤山火烧迹地植被恢复后土壤养分含量变化*孙毓鑫1,2吴建平1,2周丽霞1林永标1傅声雷1**(1中国科学院华南植物园,广州510650;2中国科学院研究生院,北京100049)摘 要 采用对比分析方法,研究了广东鹤山桉林和灌草坡火烧迹地植被恢复后土壤养分含量的变化.结果表明:火烧3年后,桉林土壤有机碳、全氮、速效钾和pH 含量明显降低,土壤有效磷、交换性镁、土壤净氮矿化速率和氨化速率降低,但不显著;火烧灌草坡除土壤交换性钙明显增加外,其他土壤养分均无显著变化.火烧桉林氮矿化速率较低的主要原因是其可利用基质的减少和桉树快速生长吸收大量养分所致,火烧灌草坡土壤养分的恢复速度较快.关键词 土壤养分 火烧迹地 植被恢复 鹤山文章编号 1001-9332(2009)03-0513-05 中图分类号 Q948.1;S153.6 文献标识码 A Changes of soil nutrient contents after prescr i b ed burni n g of forestland in H eshan C it y ,Guangdong P rovince SUN Yu x i n 1,2,WU Jian p i n g 1,2,Z H OU L i x ia 1,LI N Yong biao 1,FUSheng le i 1(1South China Botan ical Garden,Chinese Acade m y of Sciences ,Guangzhou 510650,China;2Graduate University of Chinese A cade my of Sciences ,B eijing 100049,Ch i n a). Chin.J.App l .E col .,2009,20(3):513-517.A bstract :A co m parative study w as conducted to analyze the changes of so il nutrient con tents i n Eucal y p t u s fo restland and in shrubland after three years o f prescr i b ed burn i n g .In Eucalyp tus forest land ,so il organic carbon ,to tal n itr ogen ,ava il a ble potassi u m conten ts and so il pH decreased si g nif icantly ;so il availab l e phosphorus and exchangeable m agnesi u m contents ,net n itrogen m i n era liza tion rate and a mm onificati o n rate a lso decreased but sho w ed no sign ificant d ifference .I n shr ub land ,so il ex changeab le ca lci u m content i n creased si g nificantly ,but the contents o f o t h er nutrients had no sign ifi c ant change .The m a i n reason of the l o wer so il net n itr ogen m i n eralization rate i n Eucalyp tus forest could be the decrease of ava ilable substrates and the uptake o f larger a m oun t o f so il nutr i e n ts by the fast gro w th of Eucalyp tus .The so il nutrients i n shrubland had a qu ick restorati o n rate after burning .K ey words :so il nutrien;t bur n t forestland ;vegeta ti o n restoration ;H eshan .*国家自然科学基金重点项目(30630015)、国家自然科学基金面上项目(30771704)、中国科学院知识创新工程重要方向性项目(KZCX2 Y W 413)和中国科学院 百人计划 项目资助.**通讯作者.E m ai:l sf u@scbg .ac .c n 2008 08 25收稿,2008 12 18接受.火烧作为森林生态系统恢复和管理的一种模式,一直受到国内外生态学者的广泛关注[1-6].一定频率和一定强度的火烧能够改善生态系统的结构和功能,促进生态系统的良性循环,在维持生物多样性和维护生态平衡方面起着重要的作用[7-8].土壤养分作为植物生长发育必需的成分,影响土壤肥力和植被组成的变化,因此,有关火烧迹地土壤养分的变化过程受到了众多研究者的关注.火烧对森林生态系统土壤养分的影响非常复杂,如通过氧化、挥发、淋溶和侵蚀等途径减少土壤养分的总量,短时间内增加土壤养分的有效性,增加土壤温度,改变土壤水分含量、地上植被组成和凋落物的输入,进而影响土壤氮矿化速率[7,9-10].森林生态系统火烧后对土壤养分的作用有着短期和长期之分,而相关研究大多集中在火烧后短期内土壤养分的变化过程[11-17],很少评估火烧对土壤养分的长期影响.为此,本试验通过研究火烧3年后广东鹤山人工林土壤养分及其有效性,以及火烧迹地植被恢复后土壤养分含量的变化,以期为火烧对森林土壤养分的长期影响提供数据支持,为森林生态系统火烧迹地的可持续管理提供理论依据.1 研究地区与研究方法1 1 研究区概况研究区位于中国科学院鹤山森林生态系统国家应用生态学报 2009年3月 第20卷 第3期 Ch i nese Journa l of A pp lied E co logy ,M ar .2009,20(3):513-517野外科学观测研究站(简称鹤山站)内.该站位于广东省鹤山市中部(22!41∀N,112!54∀E ),平均海拔80m.试验样地处于鹤山站的共和试验区,占地面积约45hm 2,其中设有14个森林生态系统类型,每种类型均设3个重复,每块样地面积约1h m 2.该地区属南亚热带季风气候,年均气温21 7#,年均降水量1700mm ,年均蒸发量1600mm,年平均∃10#有效积温为7597#.地带性土壤为赤红壤,成土母质是砂页岩,土壤质地以粘壤土类和壤质粘粒为主,属强酸性土壤,pH 值在4 2~4 8.1 2 研究方法共和试验样地于2005年3月进行火烧处理.火烧前样地为荒草坡,火烧后人工种植尾叶桉(Euca l y p t u s urophy lla )、厚荚相思(Acacia crassicar pa )、阴香(C innam o m um bur m annii)和观光木(Tsoongio d en odorum )等树种.本试验选取4个不同处理:火烧桉林、未火烧桉林(对照C K )、火烧灌草坡和未火烧灌草坡(CK).每个类型试验区设有3个重复,共12个试验样地,每个样地面积约1h m 2.火烧桉林灌草丛覆盖率较低,桉林下灌丛和草坡的主要植被类型为芒萁(D icranop teris dichoto m a ).土壤氮矿化采用原状土就地连续培养法测定[18].试验周期为2008年3%5月,培养时间为30d .在每个样地的上、中、下3个坡度各选取地势平坦且具有代表性的3个点进行试验(n =9),每个点打入一组PVC 管,每组3支管,PVC 管长15c m 、直径5c m.其中一支立即取走带回实验室分析,得到当时的土壤氮状况,其余2支进行原位培养,一支管加盖,以避免雨淋,另一支管敞开,与自然条件变化一致.培养时间结束后,打入第2次的3支PVC 管,同时取走第1次打入的2支PVC 管和第2次打入的一支管,带回室内分析,其余2支留下进行培养.如此重复下去.各个坡位的3点混合成一个样品,挑出土壤样品中的植物根系和砂石,过2mm 筛,混合均匀,使土壤条件一致.称取10g 土样置于浸提瓶中,加入50m l2m o l &L -1KC l 溶液震荡1h ,过滤,提取液用流动注射分析仪(QC8000,美国LAC HAT 公司)分析土壤中NH 4+N 和NO 3- N 含量,土壤水分含量在105#下烘24h 测定,剩余样品在自然条件下风干,以供p H 、有机碳、全氮、全磷、有效磷、速效钾、交换性钙和镁的测定.土壤p H 值用土水比1∋2 5提取,p H 计测定;有机碳采用重铬酸钾氧化 外加热法;全氮经浓硫酸消煮后用流动注射仪分析;全磷用硫酸 高氯酸消解 钼锑抗比色法测定;有效磷用氟化铵 盐酸 钼锑抗比色法测定;速效K 和交换性Ca 2+、M g 2+用乙酸铵浸提后,分别用火焰光度法和原子吸收分光光度法测定[19].1 3 数据处理净氮矿化速率[m g &kg -1&(30d)-1]=培养30d 后的矿质氮(NH 4+ N +NO 3- N )-培养前的矿质氮(NH 4+N +NO 3- N )净硝化速率[m g &kg -1&(30d)-1]=培养30d 后的NO 3- N -培养前的NO 3- N净氨化速率[m g &kg -1&(30d)-1]=培养30d 后的NH 4+ N -培养前的NH 4+N数据测定结果均采用平均值,统计分析采用SPSS 11 5和Ex ce l 2003软件处理.显著性水平以P <0 05表示,采用单因素方差分析火烧对不同植被类型下土壤养分的影响.2 结果与分析2 1 火烧迹地土壤p H 的变化由图1可以看出,鹤山人工林土壤pH 值都小于4 3,属于强酸性土壤.与对照相比,火烧3年后,桉林和灌草坡的土壤pH 都有不同程度的下降,火烧桉林pH 值显著降低(P =0 024),火烧灌草坡p H 值也呈降低的趋势(P =0 1).2 2 火烧迹地土壤有机碳和全氮含量变化由表1可以看出,与对照样地相比,火烧3年后,桉林土壤有机碳含量显著降低(P =0 03),0~10c m 层土壤有机碳含量降低了38 6%;而灌草坡火烧迹地土壤有机碳含量没有显著变化.土壤全氮含量与土壤有机碳含量变化相似.与对照样地相比,火烧3年后,桉林土壤全氮含量减少了27 8%(P =图1 不同火烧迹地土壤p H 值变化Fig .1 Change o f so il p H i n diff e rent burn t sites .A :桉林Eu c a l yp t u s f orest ;B:灌草坡Sh rub l and .(:未火烧处理Un bu rnt ;):火烧处理Burn t .图中不同小写字母表示差异达0 05显著水平D i ff eren t lettersm eant si gn i fi cant d ifference at0 05leve.l 下同The sa m e bel o w.514应 用 生 态 学 报 20卷表1 不同火烧迹地的土壤有机碳和全氮含量Tab .1 Change of soil organ ic carbon and n itrogen in d if ferent burn t site s (m ean ∗SE ,n =9)火烧迹地Bur n t forestl and 处 理T reat m e nt 土壤有机碳S OC (g &kg -1)全氮TN (g &kg -1)碳氮比C /N桉林(23 54∗3 19a 0 72∗0 06a 31 60∗1 80Eucal yp t us f orest )14 45∗2 12b 0 52∗0 04b 26 54∗2 51灌草坡(18 97∗2 090 59∗0 0331 62∗2 39Shrubla nd)18 11∗2 350 62∗0 0528 36∗1 85(:未火烧处理Unburnt ;):火烧处理Bu rnt .同列数据不同小写字母表示差异达0 05显著水平D ifferen t l etters in t h e sa m e coloumn m ean t si gnifi cant differen t e at 0 05l eve.l0 015);而灌草坡火烧迹地土壤全氮没有显著变化.火烧迹地土壤碳氮比与对照相比都有不同程度的降低,但变化不明显.由图2可以看出,与对照样地相比,火烧桉林净氮矿化速率(NH 4+ N +NO 3- N )和氨化速率有降低的趋势,分别为0 3和0 54m g &kg -1&(30d)-1,但差异不显著(P =0 175和P =0 09);灌草坡火烧迹地0~10c m 土层净氮矿化速率、氨化速率和硝化速率之间差异不显著.火烧桉林净氮矿化速率较低图2 不同火烧迹地土壤氨化、硝化和净氮矿化速率的变化F i g .2 Chang e o f so il a mmon ificati on ,n itrificati on ,ne tN m i n e ra liza ti on ra te i n diff e rent burn t sites.5153期 孙毓鑫等:广东鹤山火烧迹地植被恢复后土壤养分含量变化的主要原因可能是土壤中可利用基质减少[20],以及桉树生长过程中快速消耗养分所致.2 3 火烧迹地土壤磷的变化由图3可以看出,火烧迹地土壤全磷和有效磷含量都有所降低.灌草坡火烧迹地与未火烧地土壤全磷之间差异接近于显著水平(P=0 072),桉林火烧迹地有效磷也接近于显著水平(P=0 078).土壤中磷被活化释放的最佳p H值为6 6~7 0[21],可能是火烧3年后,土壤p H值的降低影响了土壤中有效磷的释放.2 4 火烧迹地土壤阳离子的变化由图4可以看出,与对照样地相比,火烧桉林土壤速效钾含量从36 24m g&kg-1减少到23 22mg& kg-1,降低了35 93%(P=0 007);土壤交换性镁也接近显著降低(P=0 052),而交换性钙无显著差异.火烧灌草坡土壤交换性钙比对照增加了66%(P= 0 004),而土壤速效钾和交换性镁则无显著差异.3 讨论与结论土壤养分不仅影响植物群落的生长、发育和演替的速度,而且对生态系统的结构和功能有着重要影响.火烧通过挥发、氧化和淋溶等途径使土壤养分总量减少,短时间内增加了土壤养分的有效性[9].本研究中,火烧迹地土壤p H值低于未火烧地,其主要原因可能是:火烧后土壤水、热、气等微气候条件改变,光照增强,加速了表层腐殖质的分解,产生的矿质元素离子与土壤胶体表面吸附的氢离子发生交换后进入土壤溶液中,从而使土壤p H值降低[22-23].火烧3年后,桉林土壤有机碳和全氮含量都显著减少,与M onleon等[20]的研究结果相似.Guo 等[24]研究发现,火烧5年后0~10c m层土壤有机碳和全氮显著减少.Gundale等[25]研究发现,火烧3年后0~10c m层土壤碳和氮含量减少,但差异不显著.火烧对土壤碳和氮的影响取决于火烧强度和火烧时间[20,26],而气候、植被、地形等决定火烧迹地土壤碳和氮的恢复速度[8].火烧后桉林地上植被数量减少,凋落物的输入和根的周转率降低,从而使土壤碳和氮含量下降.此外,桉林的生长速率加快[27],从土壤中吸收了大量养分,也可能是导致土壤养分急剧下降的一个重要原因.NH4+ N和NO3- N是植物从土壤中吸收N的主要形态,研究火烧对土壤氮矿化作用的影响至关重要.火烧桉林净氮矿化作用呈现降低趋势,而火烧草坡几乎没有变化,因此火烧后可供桉林利用的有效氮减少.与Ada m s等[28]的研究相比,本研究中桉林的净氮矿化速率相当低,火烧后桉林净氮矿化作用进一步降低,将会影响桉林的生产力.P是南方酸性土壤中树木生长的重要限制因子之一,火烧迹地中P含量的变化对植物的生长发育有着重要作用[29].由于酸性土壤中易形成不溶于水的羟基磷酸盐,土壤有效磷含量将大大减少,随着土壤温度升高和土壤p H值降低,此过程会更加明显[9].土壤磷活化释放的最佳p H值在6 6~ 7 0[21],而火烧3年后土壤pH值的降低使得土壤中有效磷含量降低.K在土壤中流动性比较强,土壤速效钾含量水平是决定钾肥肥效的重要指标之一[25,30].火烧桉林土壤速效钾含量显著降低,可能是桉林生长吸收及淋溶流失所致.而Ca在土壤中流动性相对较小[25].火烧灌草坡交换性钙含量显著增加,火烧过程中Ca 转移到矿质层,随着时间的推移,灌草坡地上植被恢复,水土流失降低,使Ca在土壤中得到进一步积累.参考文献[1] Feeney SR,K o l b TE,Cov ing t on WW,et al.In fluenceo f th i nn i ng and burn i ng restoration treat m ents on presettl em ent pondero sa p i nes a t t he G us P earson N at ura lA rea.Canadian J ournal of Forest R esearch,1998,28:1295-1306[2] Hubbard RM,V ose J M,C li nton BD,et al.Stand restora ti on burn i ng i n oak p i ne forests in the sout hern A ppalach i ans:E ffects on aboveground b i om ass and carbonand n i trogen cyc li ng.F orest E cology and M anage m ent,2004,190:311-321[3] K aye JP,H art SC,Fu l e PZ,et al.Initial carbon,nitrogen,and phosphorus fl uxes fo llo w i ng 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Chinese)[24] G uo J F,Y ang Y S,Chen GS,et al.So ilC and N poolsin Chi nese fir and everg reen broad l ea f forests and t he irchanges w it h slash bu rning i n m i d subtrop i ca l Chi na.Pedosphere,2006,16:56-63[25] G undaleM J,D eluca TH,F ied l er CE,et al.R est o ra ti ontreat ments i n a M ontana pondero sa pi ne f o rest:Effectson so il physica,l che m ical and b i o l og ical properties.Forest Ecology and M anage m ent,2005,213:25-38 [26] Johnson DW,Curtis PS.E ffects of f o rest m anag e m enton so ilC and N st o rage:M eta ana l ys i s.Forest E co logyand M anage m en t,2001,140:227-238[27]G arc i a M onti e l DC,B ink l ey D.E ff ec t o f Eucalyp t ussali gna and A lbizia falcatar i a on so il pro cess and nitrogen supply i n H awa i.i O ecolog i a,1998,113:547-556 [28] A da m s MA,A tti w ill P M.N utr i ent cy cli ng and n i trogenm i nera li zati on i n euca lypt forests o f south eastern A ustralia:Indices o f n itrogen m i nera li za ti on.P l ant andSo il,1986,92:341-362[29] T ian K(田 昆).A study on the v ariati ons of phosphorus con tent i n fire slash.Journal of South w est Fores try College(西南林学院学报),1997,17(1):21-25(i n Chinese)[30] X u L F(许联芳),W ang K L(王克林),Zhu H H(朱捍华),et al.Effects o f d ifferen t l and use types onso il nutr i ents in karst reg i on of N orth w est Guangx.i Ch inese Journal of App lie d E co l ogy(应用生态学报),2008,19(5):1013-1018(in Chi nese)作者简介 孙毓鑫,男,1983年生,硕士研究生.主要从事恢复生态学和土壤生态学研究.E m ai:l sunyux i n@ 责任编辑 李凤琴5173期 孙毓鑫等:广东鹤山火烧迹地植被恢复后土壤养分含量变化。
血叶兰幼苗对干旱胁迫的生理响应及其抗旱性指标筛选

接收日期:2023-12-14 接受日期:2024-01-08基金项目:海南省自然科学基金项目(322MS019) *通信作者。
E-mail:*****************.cn血叶兰幼苗对干旱胁迫的生理响应及其抗旱性指标筛选许丽丽,孟新亚,尤燕平,宋希强,陈耀丽,钟云芳*(海南大学热带农林学院,海南 海口 57022)摘 要:为探究血叶兰Ludisia discolor 对干旱胁迫的耐受性,以炼苗后自然生长约6个月龄的血叶兰组培苗为试材,盆栽控水模拟干旱条件下,分析幼苗生长、生理生化指标及生物活性成分的变化,并通过相关性及主成分分析评价其抗旱性主要响应因子,为血叶兰保育栽培的水分管理提供参考。
结果表明,随着干旱程度增加,血叶兰株高较对照组呈下降趋势,但茎粗无明显影响;叶片相对含水量减少,叶绿体色素(Chl)含量先上升后降低,而花色素苷(ACN)含量则呈上升趋势。
干旱胁迫下,植株过氧化物酶(POD)、超氧化物歧化酶(SOD)活性均呈先升后降趋势,丙二醛(MDA)、可溶性糖(SS)含量及生物活性物质总黄酮(TF)、总酚(TP)和多糖(PS)含量均增加。
相关性分析和主成分分析表明,MDA 、可溶性糖、多糖和相对含水量可作为血叶兰耐旱性的首先评价指标,茎粗、SOD 活性可为辅助指标。
综上,适度干旱胁迫(土壤含水量50%~55%) 可促进血叶兰渗透调节物质、生物活性成分的合成积累,若基于提升血叶兰品质,建议在采收前进行短期的重度干旱(土壤含水量15%~20%)以提升植株生物活性含量,该研究结果对血叶兰栽培管理具有指导意义。
关键词:血叶兰;干旱胁迫;生理特性;生物活性成分Doi: 10.3969/j.issn.1009-7791.2024.01.002中图分类号:Q945.78 文献标识码:A 文章编号:1009-7791(2024)01-0012-10Physiological Response of Ludisia discolor Seedlings to Drought Stress andScreening of Drought Resistance IndicatorsXU Li-li, MENG Xin-ya, YOU Yan-ping, SONG Xi-qiang, CHEN Yao-li, ZHONG Yun-fang *(College of Tropical Agriculture and Forestry, Hainan University, Haikou 570228, Hainan China)Abstract: In order to investigate the tolerance of Ludisia discolor to drought stress, the experiments potted water control to simulate drought were used to study the changes of growth, physiological and biochemical indicators, and bioactive components in L. discolor seedlings with around 6 months of age under different water treatments. The main response factors to drought resistance were evaluated through correlation analysis (CA) and principal component analysis (PA), which would provide some references for the water management under conservation and cultivation of L. discolor . The results showed that with the increase of drought severity, the height of L. discolor seedlings showed a downward trend compared to the control group, but there was no significant effect on stem thickness. The relative water content of leaves decreased, and the content of chloroplast pigment (Chl) first increased and then decreased, while the content of anthocyanin (ACN) showed an upward trend. Under drought stress, the activities of peroxidase (POD) and superoxide dismutase (SOD) showed a trend of first increasing and then decreasing. The contents of malondialdehyde (MDA), soluble sugar (SS), and the bioactive substances such as2024, 53(1): 12~21.Subtropical Plant Science第1期许丽丽等:血叶兰幼苗对干旱胁迫的生理响应及其抗旱性指标筛选﹒13﹒total flavonoids (TF), total phenols (TP), and polysaccharides (PS) all increased. Through correlation analysis and principal component analysis, it was found that MDA, SS, PS, and relative water content could be used as the preferred evaluation indicators, and in addition, stem thickness and SOD activity could be used as auxiliary indicators for drought resistance evaluation in L. discolor. In summary, the results indicated that moderate drought stress (soil moisture content 50%–55%) could promote the synthesis and accumulation of osmotic regulating substances and bioactive components of L. discolor, At the same time, to improve the quality of L. discolor, it was recommended to carry out short-term severe drought (soil moisture content 15%–20%) before harvest so that the biological activities of L. discolor could be enhanced. These findings had practical guiding significance for cultivation management.Key words: Ludisia discolor; drought stress; physiological characteristics; biologically active ingredients干旱胁迫是影响植物生长发育和生理生化进程的关键性环境因素。
火山的爆发:地球的脉动 英语作文

Volcanic Eruptions:The Pulse of the EarthVolcanic eruptions,one of nature's most powerful and awe-inspiring phenomena,serve as a vivid reminder of the Earth's dynamic inner workings.These natural events,characterized by the explosive release of magma,gases,and ash from beneath the Earth's crust,play a crucial role in shaping our planet's landscape and atmosphere.This essay explores the significance of volcanic eruptions,highlighting their role in the Earth's geological processes,their impact on the environment and human societies,and the importance of monitoring and studying these natural phenomena.The Geological Significance of Volcanic EruptionsVolcanic eruptions are a key component of the Earth's geology,acting as a mechanism for the planet to release internal heat and pressure.The movement of tectonic plates often triggers these eruptions,especially at divergent and convergent boundaries where plates move apart or collide. As magma rises to the surface,it cools and solidifies,forming new crust and shaping the Earth's topography.Over millions of years,volcanic activity has created mountains,islands,and entire landmasses, demonstrating the planet's ever-changing nature.Environmental Impact and FertilityWhile volcanic eruptions can be destructive,they also play a vital role in replenishing the Earth's soils with nutrients.The ash and lava released during an eruption are rich in minerals that,over time,contribute to soil fertility,supporting plant growth and agriculture.For instance,the fertile soils of the Italian countryside and the Hawaiian Islands owe their richness to centuries of volcanic activity.Additionally,volcanic gases such as carbon dioxide contribute to the greenhouse effect,influencing the Earth's climate and atmospheric composition.Hazards and Human SocietyThe immediate effects of volcanic eruptions can be devastating for nearby communities,causing loss of life,destruction of property,and displacement of va flows,ash falls,and pyroclastic flows can obliterate everything in their path.Moreover,the release of volcanicash into the atmosphere can lead to respiratory health issues,disrupt air travel,and affect climate patterns globally.The eruption of Mount Tambora in1815,for example,led to the"Year Without a Summer," causing widespread crop failures and famine across the globe. Monitoring and ResearchGiven the potential hazards associated with volcanic eruptions, monitoring and research are crucial for predicting and mitigating their impact.Volcanologists use a variety of tools,including seismographs,gas sensors,and satellite imagery,to monitor volcanic activity and provide early warnings to at-risk communities.Understanding the signs of an impending eruption,such as increased seismic activity or changes in gas emissions,can save lives and minimize economic damage. ConclusionVolcanic eruptions are a testament to the Earth's vitality,reminding us of the planet's constant evolution and the forces that shape our natural world.While they pose significant risks to human society,they also enrich our environment,contributing to the cycle of renewal that sustains life on Earth.By studying and monitoring volcanic activity,we can better appreciate the complexity of our planet and learn to coexist with these powerful natural phenomena.In embracing the pulse of the Earth,we acknowledge our place within a much larger,ever-changing system.。
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Soil Contributions to Blasting Effects from Case Histories and Vibration Limits Mark R. Svinkin, Member, ASCE 1 1VIBRACONSULT, 13821 Cedar Road, #205, Cleveland, OH 44118-2376; PH (216) 397-9625; FAX (216) 397-9625; msvinkin@ Abstract The existing vibration limits were developed for 1-2 story houses surrounding coal surface mines, and these limits are applied for ground vibrations as the criteria for the possible crack formation in structures. However, other blast design, soil conditions and structures require different vibration limits. There are no regulations for multistory building vibrations from blasting and there are no limits to assess possible dynamic settlements of soil and structures triggered by ground vibrations from blasting. Nevertheless, numerous case histories are available in technical papers which describe tolerable and unacceptable soil and structural vibrations measured for different soil conditions and structures. These case histories are valuable sources of information to evaluate vibration effects on structures, analyze vibration levels that do not produce damage to structures, determine the areas of application of the existing regulations and assess tolerable vibration limits for various structures during blasting operations. Introduction Blasting operations conducted in urban areas are usually connected with potential problems of manifestation of vibration effects on adjacent and remote houses, buildings and other super and underground structures. Dynamic consequences of structural vibrations range from benign to harmful. It is common that two significant questions come up at neighborhood areas around sites with blasting operations: what is the cause of damage to structures and what vibration limits have to be used at specified areas. It is necessary to underline that similar damage to structures can be produced by different group of static and dynamic loads such as environmental forces (temperature, humidity, wind, rain, snow, etc.), geotechnical hazards (heave, settlement, stability, sliding and failure), and dynamic effects from blasting. Determination of actual causes of damage to structures withoutthe performance of a pre- and post-blast structure surveys is a complicated task, and 335D o w n l o a d e d f r o m a s c e l i b r a r y .o r g b y O c e a n U n i v e r s i t y o f C h i n a o n 11/19/13. C o p y r i g h t A S CE .F o r p e r s o n a l u s e o n l y ; a l l r i g h t s r e s e r v e d .missing surveys are the basis for contradictory judgments of blasters and house owners. Counteraction between both sides sometimes extends in large scales. On the one hand blasters stand up for their correct blasting operations without any damage to structures. On the other hand residents who believe that their houses were damaged by blasting joint efforts to push forward the legislature for diminishing the vibration limits, increase areas of pre-blasting survey and choose larger scaled-distances to decrease vibration effects on houses from blasting. Such restrictions can create substantial obstacles for production blasts without insurance of safe blasting. Obviously, a number of resident complaints are related to public perception of blasting and public relations. However, there are case histories with real damage to structures from blasting. Vibration limits correctly determined can help to properly assess vibration problems during blasting. Case histories are large and valuable sources of information which can be used to determine vibration limits. In this paper, a number of case histories are analyzed with an emphasis on soil contributions to blasting effects on wave propagation and damage to structures. The Existing Vibration Limits Apparently, it is impossible to have universal regulations of blasting vibrations applied for different kinds of blasting, variety of soil conditions and types of structures. The available optional regulations, NFPA 495 (2006), include the vibration cosmetic cracking thresholds for assessment of surface coal mine blasting effects on 1-2 story residential houses, Figure 1. These criteria developed by the U.S. Bureau of Mines (USBM) have the following displacement and velocity values for the four ranges of the dominant frequencies: 0.76 mm (0.03 in) for 1-4 Hz, 19 mm/s (0.75 in/s) for 4-15 Hz, 0.2 mm (0.008 in) for 15-40 Hz, and 50.8 mm/s (2.0 in/s) for 40-100 Hz. The limit of 19 mm/s (0.75 in/s) for 4-15 Hz is used for drywall while the limit of 13 mm/s (0.5 in/s) for 2.5-10 Hz is applied for plaster, Siskind et al. (1980). The derivative version of the USBM safe limits shown in Figure 1 was included as the Chart Option into the surface coal mine regulations by the Office of Surface Mining Reclamation and Enforcement, OSM (1983). The USBM vibration limits were built up on the basis of the two decades research studies of a correlation between ground vibrations and observations of blast damage to low-rise houses, and these limits are applied for ground vibrations as the criteria of possible crack formation in various structures. The USBM research study has been recognized as the great achievement which provides the safety of 1-2 story residential houses from vibrations generated by surface coal mining blasting. Obviously, these vibration limits can be successfully used for adequate blasting loads, similar structures and ground conditions they were developed for, but different limits should be used for other combination of dynamic loads, soil conditions and structures.FORENSIC ENGINEERING 2009336D o w n l o a d e d f r o m a s c e l i b r a r y .o r g b y O c e a n U n i v e r s i t y o f C h i n a o n 11/19/13. C o p y r i g h t A S C E . F o r p e r s o n a l u s e o n l y ; a l l r i g h t s r e s e r v e d .Figure 1. Safe level blasting criteria from USBM RI 8507 and the derivative version, the Chart Option from OSM surface coal mine regulations. Shaded area shows maximum velocities of resonant structural vibrations with amplification of 4.5. Data were modified from Siskind (2000). Plot was adapted from Svinkin (2008). Siskind (2000) presented the accumulated results of research studies accomplished by the USBM and others on vibrations from blasting and their effects on low-rise houses, Figure 2. Ground vibrations were measured near 1-2 story residential structures from 718 blasts and 233 documented observations were obtained. Non-damaging blasts are not shown although some of them produced relatively high level of ground vibrations even exceeding 51 mm/s (2 in/s). These data indicate different vibration effects on structures depending on the dominant frequency and the peak particle velocity (PPV) of ground vibrations. It is necessary to point out that the USBM criteria are conservative for assessment of direct blasting vibration effects on structures in the non-resonant frequency zones of structural vibrations when ground vibrations do not trigger plastic soil deformations under structures (Figure 2), but they cannot protect low-rise structures from appearance of cosmetic cracks by amplification of ground vibrations higher than 4.5x and beyond the 4-12 Hz frequency range, Svinkin (2003, 2004). Furthermore, the application of these limits to different super and underground structure is incorrect. AASHTO Designation: R 8-96 (2004) stated the application of the USBM limits to markedly different types of structures is common and inaccurate. Besides, the USBM limits do not actually take into account construction blasts with much higher frequency content. Dowding (1996) demonstrated examples where the dominant frequencies of ground vibrations from surface mining and construction blasting would lie between 12 and 18 Hz and 70 and 100 Hz, respectively. It means that the USBM limits cannot beused for construction blasts.FORENSIC ENGINEERING 2009337D o w n l o a d e d f r o m a s c e l i b r a r y .o r g b y O c e a n U n i v e r s i t y o f C h i n a o n 11/19/13. C o p y r i g h t A S CE .F o r p e r s o n a l u s e o n l y ; a l l r i g h t s r e s e r v e d .Some publications have stated that there are no problems with blasting vibration limits. For example, Aimone-Martin (2005) has asserted, that the safe blasting criteria defined by the U.S. Bureau of Mines in 1980 are widely used in the U.S. rock blasting industry. “This safe criteria is based on over 40 years of research and crack observations and has been scientifically supported since 1980 by experts in the field of structure response to rock blasting. There has been no scientific data to date that disputes this criteria.” On the one hand this statement is correct because the USBM criteria without doubt are good for the specific blast design, soil conditions and the types of structures they were developed for. On the other hand this statement is confusing because in a number of cases, these vibration limits are used for different blast, soil and structure conditions. Verification is necessary for the application of theUSBM criteria for other blasts, soil and 1-2 story houses. Figure 2. Ground vibrations from blasting and structural damage summary grouped in three zones. Dashed lines define USBM safe limits. Data were modified from Siskind (2000). Plot was adapted from Svinkin (2008). Siskind (1991) wrote, “Vibration criteria for nonresidential cases are needed: concrete, power poles, pipelines, bridges, etc. Without reliable criteria for such cases, regulation is often based on relatively strict levels required to prevent cosmetic damage to residences”. Also, Siskind (2000) stated that most regulatory bodies, including OSM, recognize “that a more rigorous treatment may be needed in special cases, such as that outlined in RI 8507”. Some states use single vibration limits between 6.4-51 mm/s (0.25-2.0 in/s) for PPV of ground vibrations that only aggravates problems with assessment of damage to houses because of lack of objectivity and ignorance of possible resonant structural vibrations. The British Standard BS 7385 (1993) and the USBM criteria are depicted in Figure 3. It can be seen that the BS 7385 considers two lines of the safe limits depending on a type of buildings. Line 1 with the frequency-independent criterion of 51 mm/s (2 in/s) isapplied to industrial and heavy commercial buildings. Line 2 with the frequency-based safe limits is similar to the USBM criteria and applied to residential or light commercial FORENSIC ENGINEERING 2009338D o w n l o a d e d f r o m a s c e l i b r a r y .o r g b y O c e a n U n i v e r s i t y o f C h i n a o n 11/19/13. C o p y r i g h t A S C E . F o r p e r s o n a l u s e o n l y ; a l l r i g h t s r e s e r v e d .type buildings. It seems the values presented in Figure 3 are small to represent structural vibrations. On the basis of similarity of two standards, it can be assumed that the BS 7385 requires measurement of ground vibrations as the criteria of possible structural damage. If so, the BS 7385 has similar restrictions of its application as the USBM criteria, Svinkin (2007).Figure 3. Vibration guidelines - USBM RI 8507 (solid line) compared to BS 7385 (dashed line). Line 1: reinforced or framed structures, industrial and heavy commercial buildings; line 2: unreinforced or light framed structures, residential or light commercial type buildings. From AASHTO Designation: R 8-96 (2004). The German Standard DIN 4150 (1986) and the USBM criteria are depicted in Figure 4. DIN 4150 suggests three lines of time-dependent vibration limits for different types of structures. Lines 1-3 represent different kinds of structures described in the figure caption of Figure 4. Lines 2 and 3 are located below the USBM vibration limits. Line 1 is close to the upper boundary of the USBM vibration limits in the 4-100 Hz frequency range. Comments are needed regarding structures with particular sensitivity to vibrations. Such terminology is appropriate for devices and technology sensitive to vibration, but structure sensitivity is different. Resonant vibrations are dangerous for any kind of structures: from buildings under the preservation orders to industrial buildings. Dynamic settlements can also be devastated for any kind of buildings. However, industrial buildings have much higher resistance to direct vibration effects than 1-2 story residential houses. The basis for the guideline level of DIN 4150 is unknown, AASHTO Designation: R 8-96 (2004). Obviously, these criteria intended to minimize human perceptions and complaints. This approach would be sensible if construction operationsFORENSIC ENGINEERING 2009339D o w n l o a d e d f r o m a s c e l i b r a r y .o r g b y O c e a n U n i v e r s i t y o f C h i n a o n 11/19/13. C o p y r i g h t A S CE .F o r p e r s o n a l u s e o n l y ; a l l r i g h t s r e s e r v e d .constantly affect houses and even at night. However, if blasts are performed 1-2 times per day, such an approach is unreasonable, Svinkin (2007).Figure 4. Vibration guidelines - USBM RI 8507 (solid line) compared to DIN 4150 (dashed line). Line 1: buildings used for commercial purposes, industrial buildings and buildings of similar design; line 2: dwellings and buildings of similar design and/or use; line 3: structures that because of their particular sensitivity to vibration, do not correspond to those listed in lines 1 and 2, and are of great intrinsic values (e.g. building that are under a preservation order). From AASHTO Designation: R 8-96 (2004). The Russian limits of 30-50 mm/s (1.18-1.97 in/s) for vibrations of sound structures were found by the Moscow Institute of Physics of the Earth to assess the safety of structures from explosive effects of various blasts in the air, on the ground and under the ground at the time of the Second World War, Sadovskii (1946). So, for multi-story residential, commercial and industrial buildings, the frequency-independent safe limit of 51 mm/s (2 in/s) can be chosen for the PPV of structural, not ground, vibrations. This criterion automatically takes into account soil-structure interaction for the whole building frequency range. In the support of the proposed criterion, it is necessary to underline that according to Siskind (2000), the PPV of 51 mm/s (2 in/s) is the highest vibration level generated inside homes by walking, jumping, slamming doors, etc. Besides, this vibration limit is compatible with the European Standards, and it does not exclude higher allowable vibration levels. It is easy to demonstrate compatibility of the new simplified safe criterion and the USBM vibration limits, Figure 1. To evaluate tolerable structural vibrations, the smallest vibration limits of 13 mm/s (0.5 in/s) and 19 mm/s (0.75 in/s) have to be multiplied by 4.5, and theirFORENSIC ENGINEERING 2009340D o w n l o a d e d f r o m a s c e l i b r a r y .o r g b y O c e a n U n i v e r s i t y o f C h i n a o n 11/19/13. C o p y r i g h t A S C E . F o r p e r s o n a l u s e o n l y ; a l l r i g h t s r e s e r v e d .products of 57 mm/s (2.25 in/s) and 85.5 mm/s (3.37 in/s) are higher than the simplified criterion of 51 mm/s (2 in/s), Svinkin (2007, 2008). Soil and Structure Responses to Blasting Blasting operations generate different body and surface waves which travel through the medium of soil deposits and rock. Elastic waves travel from dynamic sources and induce elastic soil deformations (ground vibrations) which levels depend on intensity of propagated waves. The structural responses to ground vibrations depend on soil-structure interaction. Ground vibrations can produce direct vibration effects on structures and trigger resonant structural vibrations of adjacent and remote structures. However, under certain circumstances such as a combination of non-cohesive soil deposits, water table levels and ground vibrations, elastic waves can be the cause of plastic soil deformations, e.g. liquefaction, densification and soil settlements triggered by small ground vibrations. Soil-structure interaction will be different for soil failure. The structural response to ground excitation depends on the soil response to waves propagated from the source and soil soil-structure interaction. Because elastic and plastic soil deformations cause dissimilar structural responses and damage, diverse thresholds have to be used for assessment of direct vibration effects, resonant structural vibrations, and plastic soil deformations (Svinkin, 2008). The existing regulations were developed for assessment of elastic soil deformations and structural responses to ground vibrations from blasting. These criteria have nothing to do with plastic soil deformations. It is necessary to underline that there are no federal, state and local regulations of the critical vibration levels of ground vibrations which may trigger dynamic soil failure. Therefore, an experience from cases histories of soil failure contribution to structural damage from blasting is very important for assessment of vibration limits to cover plastic soil deformation effects triggered by blasting. Low Attenuation of Propagated Waves in Saturated Soils C ase 1. Siskind and Stagg (2000) have made a comprehensive study of structural vibration damage to the ten typical houses from quarry blasting. The houses were selected at five areas in Miami-Dade County. Vibration measurements of ground and house structure vibrations were made from 42 quarry blasts during about a 2-month period from late February to late April 2000. The maximum distances between the active quarries and the test sites were in the 3.2-4.8 km (2-3 mi) range. Pre- and post-blasting condition surveys were made before and after vibration monitoring. Additional 756 vibration records from other reports were considered in the study. The soil at the area consisted of 0.3-0.9 m (1-3 ft) of fine grained to fibrous peat followed by 0.6-1.2 m (2-4 ft) of sand followed 0.6 m (2 ft) of marl underlain by weakly to well cemented limestone. The groundwater table is virtually coincidentwith the surface of peat. The specific condition of wave propagation has been found FORENSIC ENGINEERING 2009341D o w n l o a d e d f r o m a s c e l i b r a r y .o r g b y O c e a n U n i v e r s i t y o f C h i n a o n 11/19/13. C o p y r i g h t A S CE .F o r p e r s o n a l u s e o n l y ; a l l r i g h t s r e s e r v e d .in the Miami-Dade County: attenuation with distances is less than found on similar sites in the north. The report has revealed other interesting findings: (a) structure oscillations are superposition of vibrations with various frequencies including low frequencies of about 8 Hz, which are close to the natural frequencies of house horizontal vibrations, and very low frequencies of 2 to 4 Hz; (b) vibrations are of long duration at the houses with maximum duration about 17 second; (c) ground vibrations with the PPV of 19 mm/s (0.75 in./s) and with structure response of 6.1x would produce a global wall strain that is 1.5 times higher of the strain limit for crack formation. On the basis of vibration monitoring in the west and south-west Miami area, the authors concluded that the highest vibrations there would likely be under 3 mm/s (0.12 in/s). Liquefaction in Sands C ase 2. Sanders (1982) has performed an assessment of liquefaction danger from explosively creating breaches in the Bird’s Point – New Madrid fuze plug levee. Creation of two large crevasses would use tens tons of explosives that would cause liquefaction hazards to structures in the area. A rock layer was located at the depth greater than 30 m (100 ft). There were problems with the scarcity of borehole data below 4.5 m (15 ft) and the scarcity of data bearing on the investigation of blast-induced liquefaction. A data base from row charge experiments in soil was used in the assessment of the liquefaction hazards in the area. This study had to determine a possible liquefaction PPV threshold, the maximum distance from a blast where the threshold could be expected, and availability of structures within the distance. The safety criterion of 10 cm/s (3.9 in/s) was found out as the conservative threshold for assessment of liquefaction hazards. The maximum distances at which liquefaction might occur from blasting were ascertained in the 300-383 m (1000-1275 ft) range. The report was reviewed by Dr. H.B. Seed, one of the founders of Earthquake Engineering, who used a totally different line of approach and concluded that the threshold of 10 cm/s (3.9 in/s) was reasonable. Settlement in Sand and Clay Soils C ase 3. Charlie et al. (2001) have reported the potential responses of earth-fill and tailing dams, and other saturated earthen structures subjected to blast vibrations. Eight explosive tests were conducted on a 2.25 m (7.4 ft) high dam constructed of loose dilative sand, and they showed that significant increases in a residual pore pressure occurred when the PPV exceeded 1.5 cm/s (0.59 in/s) at shallow depths to 3.5 cm/s (1.38 in/s) at greater depths. Limited crest settlement occurred when the PPV exceeded 2.5 cm/s (1.0 in/s). Results of research studies and investigation of the field behavior of full-scale earth-fill and tailing dams indicate that the PPV below 2.5 cm/s (0.98 in/s) and 10 cm/s (3.94 in/s) are reasonable thresholds to limit pore pressurebuildup in these dams sensitive and not sensitive to vibrations, respectively.FORENSIC ENGINEERING 2009342D o w n l o a d e d f r o m a s c e l i b r a r y .o r g b y O c e a n U n i v e r s i t y o f C h i n a o n 11/19/13. C o p y r i g h t A S C E . F o r p e r s o n a l u s e o n l y ; a l l r i g h t s r e s e r v e d .C ase 4. Edwards and Northwood (1960) have presented the results of controlled blasting tests of six buildings on two different sites. Damage was correlated with explosive weight, distance, PPV of ground or structure vibrations, settlement and strain measurements in the buildings. The selected buildings were old but in good conditions except for quite localized areas in one or two of them. All had basements constructed with heavy stone masonry walls and frames with brick superstructures. The soil at the first site consisted of 6.1 m (20 ft) loose wet sand underlain by soft marine clay. The water table was about 2.1 m (7 ft) below grade. Sand soil was frozen to a depth of about 0.3 m (1 ft) at the time of the test. The buildings at the first site: church, school and house with 305 mm (12 in) brick walls and plaster inside. Large low-frequency (2-5 Hz) ground vibrations in the sand-clay soils were obtained within hundred feet of the source, and they did not occur at all at 457 m (1,500 ft) and beyond. Damage inspected in the buildings on sand-clay deposits: cracks were mainly vertical and some diagonal cracks developed in the basement and upper walls; cracks were from hairline to 13 mm (0.5 in) width; larger cracks were in walls closest to the blast. The authors concluded that the damage in the buildings on sand-clay deposits was caused by failure of the soil manifested in settlements under the building rather than by vibrations of building structures. The threshold level of 102-127 mm (4-5 in/s) was defined. Damage to Foundation Walls C ase 5. Edwards and Northwood (1960) have conducted experiments of controlled blasting operations near buildings with the objective of producing damage. General information is the same as in Case 4. The soil at the second site comprised well-consolidated glacial till which is a high shear strength material consisting of a highly compacted mixture of sand, clay, gravel and boulders. Till was frozen to a depth of about 1 ft at the time of the test. There were three houses at the second site: two with 305 mm (12 in) brick walls and plaster inside, and third with frame and vinyl sliding and wood fiber board inside. Most of the high-frequency components of ground vibrations were obtained in the till soils. Damage inspected in the buildings on till: some horizontal cracks; most of the windows in the ground floor longitudinal walls were broken while those in the walls normal to the blast remained intact. Major damage was inflicted on one building on till soil. Considerable section of the rear basement wall fell away and the masonry walls above ground level were bulged out approximately 76 mm (3 in). The threshold level of 102-127 mm (4-5 in/s) was defined. Vibration Limits and Surveys of StructuresCase histories presented above demonstrate various soil contributions to blasting effects on wave propagation and soil failure. Wave paths in saturated soils underlain FORENSIC ENGINEERING 2009343D o w n l o a d e d f r o m a s c e l i b r a r y .o r g b y O c e a n U n i v e r s i t y o f C h i n a o n 11/19/13. C o p y r i g h t A S CE .F o r p e r s o n a l u s e o n l y ; a l l r i g h t s r e s e r v e d .by rock had low attenuation and as a result ground vibrations had higher PPV. Consequently, the vibration limit of ground vibrations was decreased to 3 mm/s (0.12 in/s). This criterion is four times less than the smallest USBM vibration limit. However, the vibration thresholds of soil failure like liquefaction, settlement and soil movement damaged foundation walls were 1.5-5 times higher then the highest USBM limit in most cases.The obtained results were determined for the specific cases, and the application of these criteria to other sites can be used only for preliminary assessment of blasting effects because each site is unique. It is necessary to keep in mind that changes of blast parameters, wave paths and structure types may yield different outcomes and require different safe criteria, Siskind et al. (1980), Siskind (1991), Siskind and Stagg (2000), Svinkin (2006, 2007). Such criteria are not always available. Therefore in addition to vibration measurements, it is imperative to use other approaches like the condition survey of houses and buildings that provides good opportunities for assessment of blasting damage to structures.Pre- and post-blast surveys of structures have to be professionally performed because different kind of static and dynamic loading like environmental forces, geotechnical hazards, and dynamic effects of blasting can be the causes of similar structural damage, and such damage can exist before the beginning of blasting. It is common to consider only the effects of environmental forces such as temperature, humidity, wind, rain, snow, etc. on structural integrity. However, it is particularly important to analyze the geotechnical natural hazards at various distances from construction sites such as heave, settlement, stability, sliding and failure which may damage structures prior to construction, during and after construction. There are case histories which show the major effects of environmental forces and geotechnical causes on crack formation and structural damage in spite of blasting at various distances from houses and buildings. For example, the writer analyzed the results of pre- and post-blast structure surveys of the building and found that the geotechnical hazard, a soil failure started prior to the beginning of blasting, was the cause of damage to structures.A pre-construction survey is the first step in the control of structural vibrations to ensure safety and serviceability of adjacent and remote houses, buildings and facilities. There are four goals of this survey: (1) document the existing cracks and other damage; (2) ascertain the cause(s) of the existing cracks and other damage; (3) assess susceptibility rating of structures; (4) determine mitigation measures of blasting effects on structures.At some sites, the condition survey can provide more information about benign and harmful blasting effects on structures than vibration measurements performed during blast operations because the vibration criteria cannot embrace the whole spectrum of the blast effects on structures. The condition surveys must always accompany measurements of blasting vibrations. Surveys of structures and analysis of damage to structures should be performed by engineers who have an experience in Soil-Structural Dynamics and evaluation of blast effects on soil and structures. For FORENSIC ENGINEERING 2009344D o w n l o a d e d f r o m a s c e l i b r a r y .o r g b y O c e a n U n i v e r s i t y o f C h i n a o n 11/19/13. C o p y r i g h t A S C E . F o r p e r s o n a l u s e o n l y ; a l l r i g h t s r e s e r v e d .。