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裂隙介质污染物传质动力学 9787030729514 窦智,周志芳,王锦国等科学出版社

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作者: 窦智,周志芳,王锦国等
出版社: 科学出版社
ISBN: 9787030729514
出版时间: 2021-04

四部分类: 子部 > 艺术 > 书画
装帧: 平装
开本: 其他

作者: 窦智,周志芳,王锦国等
出版社: 科学出版社
ISBN: 9787030729514

出版时间: 2021-04
四部分类: 子部 > 艺术 > 书画

装帧: 平装
开本: 其他

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目录
Contents

Preface

Chapter 1 Introduction 1

1.1 Mass transfer in saturated system 4

1.2 Mass transfer in unsaturated system 11

Chapter 2 Concepts, Structure, and Properties of Fractured Media 15

2.1 Basic concepts of fractured media 15

2.2 Structure of fractured media 19

2.3 Properties of fractured media 23

2.3.1 Porosity of rock mass 23

2.3.2 Permeability of rock mass 24

2.3.3 Permeability of geologic formations 27

2.4 Characterization and reconstruction of fractured media 30

2.4.1 2D self-affine fracture generation 30

2.4.2 3D sheared fractures with the shear displacement 35

Chapter 3 Basic Law of Fluid Flow in Fractured Media 38

3.1 Basic concepts of fluid flow in fractured media 38

3.1.1 Viscous versus inviscid regions of flow 39

3.1.2 Laminar versus turbulent flow 39

3.1.3 One-, two-, and three-dimensional flows 40

3.2 Linear flow law 41

3.2.1 Darcy’s Law 41

3.2.2 Cubic law 45

3.3 Non-linear flow law 49

3.3.1 Izbash equation 50

3.3.2 Forchheimer equation 50

3.4 Multiphase flow 52

3.4.1 Basic concept of multiphase flow 52

3.4.2 Immiscible fluid flow 62

3.4.3 Immiscible three-phase flow 63

Chapter 4 Basic Process of Mass Transfer in Fractured Media 65

4.1 Diffusion 65

4.2 Brownian motion and Fick’s Law 70

4.2.1 Brownian motion 70

4.2.2 Fick’s First Law 74

4.2.3 Fick’s Second Law 75

4.3 Advection 77

4.4 Difference in dispersion and diffusion 79

4.5 Taylor dispersion 84

4.6 Adsorption and desorption 90

4.7 Precipitation and dissolution 91

Chapter 5 Mathematical Model of Mass Transfer in Fractured Media 93

5.1 Analytical solution of advection-dispersion equation (ADE) model 93

5.1.1 ADE model and analytical solution in one-dimensional fractured media 93

5.1.2 ADE model and analytical solution in two-dimensional fractured media 94

5.1.3 ADE model and analytical solution in three-dimensional fractured media 102

5.2 Continuous time random walk (CTRW) model 106

5.3 Mobile-Immobile (MIM) model 107

5.4 Spatial moment 108

5.5 Scalar dissipation rate(SDR)and dilution index 110

5.5.1 Scalar dissipation rate (SDR) 110

5.5.2 Dilution index 112

Chapter 6 Numerical Methods of Mass Transfer Process in Fractured Media 114

6.1 Lattice Boltzmann method 114

6.2 Immiscible two-phase transport model: Phase field method 119

6.3 Pore-scale aqueous solute transport model 121

6.4 Coupling strategy 122

6.5 Behaviors of aqueous tracer mass transfer 125

Chapter 7 Mass Transfer Between Matrix and Filled Fracture During Imbibition Process 134

7.1 LF-NMR measurement and principle 134

7.2 Experimental materials 136

7.3 Distribution of the imbibed water 138

7.4 Imbibition rate and analytical model 143

Chapter 8 Influence of Wettability on Interfacial Area for Immiscible Liquid Invasion 149

8.1 Interfacial area for immiscible liquid invasion 149

8.2 Entry pressure 151

8.3 Two phase flow characteristics 153

8.4 Capillary pressure saturation and interfacial area relationships 156

Chapter 9 Multiscale Roughness Influence on Solute Transport in Fracture 162

9.1 Statistical self-affine property 162

9.2 Roughness decomposition 166

9.3 Flow field characteristics in fractures 171

9.4 Relationship between tracer longitudinal dispersion and Peclet number 172

Chapter 10 Influence of Eddies on Solute Transport Through a Fracture 180

10.1 Flow field and eddies formation 180

10.2 Spatial evolution of solute and BTC characteristics 183

10.3 Inverse model for non-Fickian BTCs 187

10.4 Uniformity of concentration distribution 189

Chapter 11 Lattice Boltzmann Simulation of Solute Transport in Fractures 192

11.1 Coupling flow and concentration fields based on LBM 192

11.2 Taylor dispersion simulation based on LBM 194

11.3 Characteristics of solute transport in a single rough fracture 195

References 201

List of Frequently Used Symbols 213

内容摘要
Chapter 1 Introduction NAPL (Non-aqueous Phase Liquid) is a typical subsurface organic pollutant， such as tetrachloroethylene， trichloroethylene， and methylbenzene. Although the solubility of NAPLs in water is quite low (for example， the solubility of tetrachloroe- thylene in water is only 0.015 g/100 mL)， their harmfulness to the groundwater environment is surprising. Many NAPLs pose a high risk of cancer. The World Health Organization’s drinking water standard requires that benzene and trichloroethylene contain no more than 0.005 mg per liter of water， and vinyl chloride， which poses a higher cancer risk， must contain no more than 0.002 mg per liter of water. Although the solubility of many NAPLs in groundwater is quite low， it is still above the safety standard for drinking water. NAPLs are divided by the density of pure water. One is heavier than water and is referred to as DNAPL (dense NAPL)， while another is lighter than water and is referred to as LNAPL (light NAPL). Compared to LNAPL， DNAPL has a higher density than water and sinks continuously after entering the groundwater. DNAPL has the characteristics of concealment and persistence， and the problems of migration and mass transfer in fractured groundwater are more complex. DNAPL is a very special organic pollutant. Its migration and mass transfer process has the characteristics of soluble and insoluble pollutants. This is mainly because most liquid DNAPL cannot be completely dissolved in a short time and discharged from the subsurface with the runoff， but remain in the frac medium for a long time in the form of a “DNAPL pollution pool” that slowly dissolves and expands its plume with the runoff from the subsurface. The process of DNAPL migrating with the water flow as a liquid in a non-aqueous phase and DNAPL migrating with the water flow after being dissolved by the water is referred to here as mass transfer. The mass transfer process of DNAPL in fractured groundwater consists of the migration of an immiscible two-phase flow and the migration of solutes after the DNAPL is dissolved. The mass transfer of contaminant in fractured media plays an important role in the surface environment problems (e.g.， contaminant degradation (Sale et al.， 2008)， nuclear waste disposal (Bagalkot and Kumar， 2016)， and bioremediation (Song et al.， 2014). In recent decades， the investigation of dilution and mixing processes in fractured media has been focused by the scholars in various fields (Anna et al.， 2014; Soltanian et al.， 2015; Dou et al.， 2018a; Dou et al.， 2018b). The characterization of the spreading and mixing processes of the conservative solute is instrumental in understanding and assessing reactive solute transport， which is necessary for studying complex chemical biological reaction transport in groundwater. Although many studies (Shapiro and Brenner， 1988; Pini et al.， 2016) have provided new insights into the mechanisms and properties of the mixing behavior at the Darcy scale or the larger field scale， little attentions have been focused on porous media at the pore scale. There is always an influence of the smaller-scale processes on the larger scale behaviors (Bear， 2013). Therefore， to understand and evaluate mixing processes at pore-scale with suitable methods is very significant (Rolle et al.， 2013). The migration process of DNAPL in fractured groundwater can be divided into three stages: The first stage is the overall intrusion stage of DNAPL; the second stage is the comigration stage of DNAPL and water flow; the third stage is the residual dissolution stage of DNAPL， as shown in Figure 1.1.1. The residual DNAPL of fractured groundwater refers to the DNAPL that cannot be displaced by water flow alone under the conditions of natural water flow and pressure. Since the dissolution rate of DNAPL is affected by its interface area， hydrodynamic conditions， and geometric characteristics of fractures， its dissolution content in water can be ignored compared to the penetration of DNAPL in a short time. Generally， the migration process of DNAPL in the first and second stages is considered only as two-phase immiscible flow migration process， while the solubility of DNAPL in water is ignored. In the third stage， the remaining DNAPL is relatively stable and no longer migrates as a whole， but continuously dissolves in the water body and increases its dissolved pollution plume by the effect of groundwater discharge. In this stage， the problem of DNAPL dissolution process and solute transport with DNAPL as solute must be considered. The first and second stages directly affect the distribution characteristics of DNAPL residues in fractured media in the third stage， and the third stage is an important reason for the persistence and concealment of DNAPL pollutants. The spatial heterogeneities of the pore space in aquifers lead to the complex fluid flow and anomalous solute transport. As the occurrence of preferential flow paths and/o

精彩内容
本书结合我国生态文明建设的国家战略需求，依托国家重点研发计划“场地土壤污染成因与治理技术”重点专项（2019YFC1804303），紧密结合科研育人的内在要求，从培养高层次创新型人才知识结构需求出发，注重内容的理论性、系统性、前沿性和完整性。

主要内容包括裂隙介质概念、结构与特性、裂隙介质水动力学基础、裂隙介质中污染物基本传质过程、裂隙介质中污染物传质的数
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