Radionuclide Transport Models Under Ambient Conditions Rev 00, ICN 00

MDL-NBS-HS-000008

March 2000

1. PURPOSE 
The purpose of this Analysis/Model Report (AMR) is to evaluate (by means of 2-D 
semianalytical and 3-D numerical models) the transport of radioactive solutes and colloids in the 
unsaturated zone (UZ) under ambient conditions from the potential repository horizon to the 
water table at Yucca Mountain (YM), Nevada. This is in accordance with the AMR Development 
Plan U0060, Radionuclide Transport Models Under Ambient Conditions (CRWMS M&O 
1999a). This AMR supports the UZ Flow and Transport Process Model Report (PMR). 
This AMR documents the UZ Radionuclide Transport Model (RTM). This model considers 
 the transport of radionuclides through fractured tuffs 
 the effects of changes in the intensity and configuration of fracturing from hydrogeologic 
unit to unit 
 colloid transport 
 physical and retardation processes, and 
 the effects of perched water. 
In this AMR we document the capabilities of the UZ RTM, which can describe flow (saturated 
and/or unsaturated) and transport, and accounts for (a) advection, (b) molecular diffusion, (c) 
hydrodynamic dispersion (with full 3-D tensorial representation), (d) kinetic or equilibrium 
physical and/or chemical sorption (linear, Langmuir, Freundlich or combined), (e) first-order 
linear chemical reaction, (e) radioactive decay and tracking of daughters, (f) colloid filtration 
(equilibrium, kinetic or combined), and (g) colloid-assisted solute transport. 
Simulations of transport of radioactive solutes and colloids (incorporating the processes 
described above) from the repository horizon to the water table are performed to support model 
development and support studies for Performance Assessment (PA). The input files for these 
simulations include transport parameters obtained from other AMRs (i.e., CRWMS M&O 
1999d, e, f, g, h; 2000a, b, c d). When not available, the parameter values used are obtained from 
the literature. 
The results of the simulations are used to evaluate the transport of radioactive solutes and 
colloids, and to determine the processes, mechanisms, and geologic features that have a significant 
effect on it. We evaluate the contributions of daughter products of radioactive decay to transport 
from the bottom of the potential repository to the water table. The effect of the various 
conceptual models of perched water bodies on transport is also evaluated. Note that a more 
thorough study of perched water bodies can be found in another AMR (CRWMS M&O 1999d, 
Sections 6.2 and 6.6). 
The primary caveat for using the modeling results documented here is that the input transport 
parameters were based on limited site data. For some input parameters, best estimates were used 
because no specific data were available. An additional caveat is that the RTM is based on the

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 14 
conceptual models and numerical approaches used for developing the flow fields and infiltration 
maps, and thus they share the same limitations.

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MDL-NBS-HS-000008 REV 00 March 2000 15 
2. QUALITY ASSURANCE 
This AMR has been developed in accordance with procedure AP-3.10Q, Rev. 1, ICN 1, Analyses 
and Models. Accordingly, the modeling activities documented in this AMR have been conducted 
in accordance with the CRWMS M&O quality assurance program, using OCRWM 
Administrative Procedures (APs) and YMP-LBNL Quality Implementing Procedures (QIPs) 
identified in the AMR Development Plan for U0060, Radionuclide Transport Models Under 
Ambient Conditions (CRWMS M&O 1999a). 
The activities documented in this AMR were evaluated with other related activities in accordance 
with QAP-2-0, Rev. 5, Conduct of Activities and were determined to be quality affecting and 
subject to the requirements of the U.S. DOE Office of Civilian Radioactive Waste Management 
(OCRWM) Quality Assurance Requirements and Description (QARD) (DOE 1998a). This 
evaluation is documented in Activity Evaluation of M&O Site Investigations (CRWMS M&O 
1999b; and Wemheuer 1999 WP #1401213UM1).

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3. COMPUTER SOFTWARE AND MODEL USAGE 
The software codes and routines used in this study are listed in Table 3.1. TOUGH2 V1.4 
Module EOS9 V1.4 (STN: 10007-1.4-01) and T2R3D (SN: 10006-1.4-00) were appropriate for 
the intended application, were used only within the range of their software validation, and were 
obtained from configuration management per AP-SI.1Q, Rev. 2, ICN 2, Software Management. 
TOUGH2 V1.11 Module EOS9nT V1.0 (STN: 10065-1.11MEOS9NTV1.0-00) and FRACL 
V1.0 (STN: 10191-1.0-00) are being qualified and Software Activity Plans for use of unqualified 
software and copies have been submitted to configuration management per Section 5.12 of APSI.
1Q. The Q-status of these codes is provided in the Document Input Reference Sheet (DIRS), 
which is included as Attachment XIII. The software routines listed in Table 3.1 have been 
qualified per Section 5.1.1 of AP-SI.1Q and their source codes are included in Attachment XI. 
Table 3.1: Software Codes and Routines 
Software Name Version Software Tracking Number 
(STN): 
Computer Platform 
TOUGH2 V1.11 
Module EOS9nT 
V1.0 
1.0 10065-1.11MEOS9NTV1.0-00 Sun or DEC Workstation 
with Unix OS 
Apple Macintosh with Mac 
OS 8.6 
TOUGH2 V1.4 
Module EOS9 
V1.4 
1.4 10007-1.4-01 Sun or DEC Workstation 
with Unix OS 
T2R3D 1.4 10006-1.4-00 Sun or DEC Workstation 
with Unix OS 
FRACL 1.0 10191-1.0-00 Sun or DEC Workstation 
with Unix OS 
Routines: 
xtract1.f 1.0 10213-1.0-00 Apple Macintosh with Mac 
OS 8.6 
xtract2.f 1.0 10214-1.0-00 Apple Macintosh with Mac 
OS 8.6 
xtract2a.f 1.0 10215-1.0-00 Apple Macintosh with Mac 
OS 8.6 
xtract2b.f 1.0 10216-1.0-00 Apple Macintosh with Mac 
OS 8.6 
xtract5.f 1.0 10217-1.0-00 Apple Macintosh with Mac 
OS 8.6 
xtract6.f 1.0 10218-1.0-00 Apple Macintosh with Mac 
OS 8.6 
The software code TOUGH2 V1.11 Module EOS9nT V1.0 (SN: 10065-1.11MEOS9NTV1.0- 
00) simulates flow (saturated and/or unsaturated) and the transport of a multiple number of 
radioactive solutes and/or colloids in complex subsurface systems involving porous and/or 
fractured media. The transport equations account for advection, molecular diffusion, 
hydrodynamic dispersion, kinetic or equilibrium physical and chemical sorption (linear, 
Langmuir, Freundlich or combined), first-order linear chemical reaction, colloid filtration, and 
colloid-assisted solute transport.

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Industry standard graphics software programs were also used but are not subject to software 
quality assurance requirements under QARD per Section 2.0 of AP-SI.1Q. 
This AMR documents the UZ Radionuclide Transport Model. Input and output files for the 
model simulations documented in this AMR are listed in Attachment XII.

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4. INPUTS 
The input used in this AMR consist of the following: 
 Transport properties 
 Calibrated fracture and matrix properties 
 Base case flow fields 
 Geochemical data 
 Numerical grids 
4.1 DATA AND PARAMETERS 
Specific input data sets and their associated Data Tracking Numbers (DTNs), Accession 
Numbers (ACC), and sources are listed in Table 4.1. The Q-status of these data is provided in 
the DIRS in Attachment XIII. 
Table 4.1. Input Data 
Description Parameters Data Source 
Geological profile and rock properties at 
the UE-25 UZ#16 cross-section 
DTN: LB990701233129.002 
Calibrated infiltration rate DTN: LB991131233129.003 
Field measurement of the chloride 
concentration profile in the UE-25 
UZ#16 borehole 
DTN:GS950608312272.001 
Modeling the chloride 
distribution in borehole UE-25 
UZ#16 (Section 6.4.3) 
Chloride diffusion coefficient DTN: LB991220140160.019 
Grid and flow field DTN: LB990701233129.002 
Calibrated infiltration rate DTN: LB991131233129.003 
Modeling the chloride 
distribution in the ESF (Section 
6.4.4) Cl- concentration measurements in the 
ESF 
DTNs: 
LAJF831222AQ98.007, 
LA9909JF831222.010, and 
LA9909JF831222.012 
Molecular diffusion coefficient DTN: LB991220140160.019 
Half-life for the first-order radioactive 
decay T1/2 
DTN: LB991220140160.019 
Properties of the main 
radionuclides in the transport 
simulations ( 99Tc, 237Np, 239Pu, , 
235U, 231Pa, 233U, and 229Th) 
(Sections 6.5.2 and 6.11.3) 
Sorption coefficient Kd DTN: LB991220140160.019

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Table 4.1. Input Data (continued) 
Description Parameters Data Source 
Geologic profiles and rock properties at 
the three cross-sections 
DTNs: 
LB990501233129.004 
Matrix properties (porosity , immobile 
water saturation Sr), fracture properties 
(Sr, active fracture parameter , frequency 
fa), rock grain density s 
DTN: LB997141233129.001 
Matrix (Swm ) and fracture water saturation 
(Swf ) at steady state 
DTN: LB990801233129.003 
Fracture aperture DTN: LB990501233129.001 
FRACL transport simulations 
in Cross Sections 1,2 and 3 
(Sections 6.5, 6.6, 6.7, 6.8, 
6.9) 
Tortuosity t for each hydrogeologic layer DTN: LB991220140160.019 
Calibrated flow parameters for base-case 
infiltration in the matrix of the ch1v and 
ch2v layers (porosity , permeability k, 
van Genuchten and m parameters, 
residual saturation Sr, satiated saturation 
Sw, rock grain density s, tortuosity t) 
DTN: LB997141233129.001 
Matrix porosity , permeability k, initial 
saturation, and rock grain density s of 
the field samples 
DTNs: 
GS990308312242.007 and 
GS990708312242.008 
Calibrated flow parameters for dualpermeability 
model base-case in the 
matrix of the ch1v and ch2v layers 
(porosity , permeability k, van 
Genuchten and m parameters, residual 
saturation Sr, satiated saturation Sw, rock 
grain density s, tortuosity t) 
DTN: LB971212001254.001 
Modeling the Phase1A test of 
Busted Butte (Section 6.10.1) 
Br- diffusion coefficient and sorption 
coefficient 
DTN: LB991220140160.019

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MDL-NBS-HS-000008 REV 00 March 2000 21 
Table 4.1. Input Data (continued) 
Description Parameters Data Source 
Calibrated flow parameters for base-case 
infiltration in the matrix of the tsw39 
layer (porosity , permeability k, van 
Genuchten and m parameters, residual 
saturation Sr, satiated saturation Sw, rock 
grain density s, tortuosity t) 
DTN: LB997141233129.001 
Matrix porosity, permeability, and initial 
saturation of the field samples 
DTNs: GS990308312242.007 
and GS990708312242.008 
Diffusion coefficient for Li+ and 2,6- 
DFBA 
DTN: LB991220140160.019 
Modeling the Phase1B test of 
Busted Butte (Section 6.10.2) 
Sorption coefficient for Li+ and 2,6-DFBA DTN: LB991220140160.019 
Present-day lower-bound infiltration 
(perched water model #1) 
DTN: LB990801233129.001 
Present-day mean infiltration (perched 
water model #1) 
DTN: LB990801233129.003 
Present-day upper-bound infiltration 
(perched water model #1) 
DTN: LB990801233129.005 
Glacial lower-bound infiltration (perched 
water model #1) 
DTN: LB990801233129.007 
Glacial mean infiltration (perched water 
model #1) 
DTN: LB990801233129.009 
Glacial upper-bound infiltration (perched 
water model #1) 
DTN: LB990801233129.011 
Monsoon lower-bound infiltration 
(perched water model #1) 
DTN: LB990801233129.013 
Monsoon mean infiltration (perched 
water model #1) 
DTN: LB990801233129.015 
Monsoon upper-bound infiltration 
(perched water model #1) 
DTN: LB990801233129.017 
Present-day mean infiltration (noperched-
water model) 
DTN: LB990801233129.019 
Flow fields for 3-D site-scale 
radionuclide transport modeling 
(Sections 6.11, 6.12, 6.13, 6.14, 
6.15, 6.16 and 6.17) 
Present-day mean infiltration (perchedwater 
model #2) 
DTN: LB990801233129.004

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Table 4.1. Input Data (continued) 
Description Parameters Data Source 
Properties and characteristics of the 
geologic units, steady-state pressures, 
water saturations and flow fields 
DTN: LB990801233129.003 
Tortuosity t DTN: LB991220140160.019 
Molecular diffusion coefficient D0 DTN: LB991220140160.019 
EOS9nT 3-D site-scale 
simulations of colloid transport 
(perched water model #1, mean 
present-day infiltration) (Sections 
6.16 and 6.17) 
Colloid density rc DTN: LB991220140160.019 
4.2 CRITERIA 
This AMR complies with the DOE interim guidance (Dyer 1999). Subparts of the interim 
guidance that apply to this modeling activity are those pertaining to the characterization of the 
Yucca Mountain site (Subpart B, Section 15), the definition of hydrologic parameters used in 
performance assessment (Subpart E, Section 114(a)) and providing the technical basis for the 
description of natural barriers identified as important to waste isolation (Subpart E, Sections 
114(h), (i) and (j)). 
4.3 CODES AND STANDARDS 
No specific formally established codes or standards have been identified as applying to this 
AMR.

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
5. ASSUMPTIONS 
In this section we discuss the basic assumptions in the mathematical basis of the transport model, 
and we provide a short discussion of the supporting rationale. This section is structured as follows: 
Section 5.1 addresses the general assumptions underlying the flow component of the transport 
model of the Yucca Mountain (YM) unsaturated zone (UZ). Section 5.2 lists the assumptions of the 
transport processes. The assumptions involved in the treatment and mathematical representation of 
the fractured rocks using the dual-continuum approach are discussed in Section 5.3. Assumptions 
related to the initial and boundary conditions of the model domain are presented in Section 5.4. 
Sections 5.1 to 5.4 address issues related to large-scale 3-D numerical simulations. Section 5.5 
discusses the assumptions involved in the semianalytical transport solution used for 2-D transport 
submodels. 
5.1 ASSUMPTIONS INVOLVEDIN THE FLOW COMPONENT 
OF THE TRANSPORT PROCESSES 
The transport phenomena and processes in the unsaturated zone of Yucca Mountain have a flow 
component and a transport component, each of which are described by a set of governing equations. 
These conserve mass, energy and momentum in the system understudy, while quantifying the system 
response to external mass and energy inputs and interrelationships between the various processes 
involved. 
The basic flow assumptions are consistent with those of discussed in CRWMS M&O (1999d, 
Sections 5 and 6): they share identical conceptual models, which are stated below. 
1. The macroscopic-continuum approach is a valid concept for the description of the flow and 
transport processes in the fractured UZ rocks. 
Rationale: The rationale for this assumption is provided in CRWMS M&O (1999d, Section 
6.1.2). 
Applicability: This assumption applies to all numerical (i.e., 3-D site-scale) simulations of 
flow and transport in this AMR (Sections 6.4.3 and 6.11 to 6.17). No further confirmation is 
required for the purposes of this study. 
2. Darcys law is a valid model to describe the flow of gas and water in the matrix and fractures 
of the UZ. 
Rationale: Given the applicability of the macroscopic continuum approach, the gaseous and 
aqueous flows under ambient conditions in the UZ are sufficiently slow to correspond to a 
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Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Reynolds number  10, i.e., the upper limit of applicability of Darcys law (Bear, p: 127, 
1972). 
Applicability: This assumption applies to all 3-D site-scale simulations of flow and transport 
in this AMR (Sections 6.4.3 and 6.11 to 6.17). No further confirmation is required for the 
purposes of this study. 
3. Richards equation (Richards 1931, pp: 218-233) is a valid model of unsaturated water flow 
in both the matrix and the fractures of the UZ. 
Rationale: Under ambient conditions, the gas-phase pressure in the UZ is atmospheric, 
corrected for elevation. The absence of gas pressurization makes possible the adoption of 
Richards equation, because the gas phase can be neglected and the aqueous phase flow occurs 
in response to gravitational and capillary pressure differentials. 
Applicability: This assumption applies to all 3-D site-scale simulations of flow and transport 
in this AMR (Sections 6.4.3 and 6.11 to 6.17). No further confirmation is required for the 
purposes of this study. 
4. Relative permeabilities and capillary pressures are assumed to follow the van Genuchten 
(1980) and Mualem (1978) model and are continuous functions of the effective liquid and gas 
saturations. 
Rationale: This model is consistent with the the macroscopic continuum approach, has been 
successfully used to determine relative permeability and capillary pressure parameters from 
UZ rocks (matrix blocks), and is reasonable for fractures (CRWMS M&O, 2000a, Section 6). 
Applicability: This assumption applies to all 3-D site-scale simulations of flow and transport 
in this AMR (Sections 6.4.3 and 6.11 to 6.17). No further confirmation is required for the 
purposes of this study. 
5. The water flow is isothermal. 
Rationale: This is a reasonable approximation. The flow parameters affected by temperature 
are the water density and the water viscosity. The ambient temperature extremes at the domain 
boundaries are about 20 oC at the top and about 30 oC at the the water table at the bottom 
(CRWMSM&O 1999d, Section 6.3). Between 20 oC and 30 oC, the water density decreases 
from 998.21 kg/m3 to 995.65 kg/m3 (Lide 1992, p: 6-10), i.e., the change is very small. 
The effect on viscosity is more pronounced. Between 20 oC and 30 oC, the water viscosity 
decreases from 1:002103 Pas to 7:977104 Pas (Lide 1992, p: 6-10), i.e., a reduction 
of about 20%. Although this variation is not excessive (given the uncertainty in the values 
of the hydraulic properties of the UZ system), its effects are minimized by conducting the 
isothermal flow simulations at 25 oC. 
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Title:Radionuclide Transport Models Under Ambient Conditions U0060 
The assumption of isothermal flow may be less valid in the immediate vicinity of the waste 
package because of the heat generated by the radioactive decay process. The non-isothermal 
flow under these conditions is the subject of another AMR (CRWMS M&O 2000b). 
Applicability: This assumption applies to all 3-D site-scale simulations of flow and transport 
in this AMR (Sections 6.4.3 and 6.11 to 6.17). No further confirmation is required for the 
purposes of this study. 
6. Waterflow through the UZ in the numerical simulations of radionuclide transport is considered 
time-invariant (steady-state). 
Rationale: This is a reasonable approximation, given the very long simulation periods ( 100,000 years). This approach allows the determination of the envelope of the transport 
behavior by considering nine different infiltration scenarios (and, consequently, flow fields), 
and is consistent with the flow regimes discussed in CRWMSM&O (1999d, Section 6.1.2). 
Applicability: This assumption applies to all 3-D site-scale simulations of flow and transport 
in this AMR (Sections 6.4.3 and 6.11 to 6.17). No further confirmation is required for the 
purposes of this study. 
5.2 ASSUMPTIONS INVOLVEDIN THE TRANSPORT PROCESSES 
7. Theindividualandcombinedeffectsofdiffusion(molecularand/orcolloidal), surfacediffusion 
and hydrodynamic dispersion follow a Fickian model. 
Rationale: Given the macroscopic continuum approach, this is a valid assumption (de Marsily 
1986, pp: 228-277). 
Applicability: This assumption applies to all studies in this AMR (Sections 6.4 to 6.17). No 
further confirmation is required for the purposes of this study. 
8. Transport is assumed to occur isothermally at 25 oC. 
Rationale: This assumption of isothermal transport at the average ambient temperature of the 
UZ is consistent with the assumption of isothermal flow at the same temperature. The transport 
parameters affected by temperature are (a) the diffusion coefficient D0 of the dissolved or 
colloidal species and (b) the sorption parameters of the dissolved species or the filtration 
parameters of the suspended colloid. Natural temperature differentials in the undisturbed 
UZ profile occur because of the geothermal gradient. Substantial temperature increases over 
the ambient are expected after the radioactive waste emplacement in the potential repository 
(CRWMSM&O 2000b, Section 6.5). 
An increasing temperature leads to a higher D0 value according to the relationship discussed 
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Title:Radionuclide Transport Models Under Ambient Conditions U0060 
in Section 6.1.2.9 of this AMR. Based on this relationship, an increase in temperature from 
20 oC (at the top of the UZ domain) to 30 oC (at the water table , i.e., the bottom of the UZ 
domain) leads to an increase of D0 by about 30%. 
The effect of temperature on sorption and/or filtration is less well-defined. The general effect 
of an increasing temperature is a decrease in the sorption of anionic species and an increase 
in the sorption of cationic species. Theoretical and experimental studies indicate an increase 
of the distribution coefficientKd with temperature when sorption follows a linear equilibrium 
isotherm (CRWMSM&O 1999e, Section 6.4.6). 
Colloidfiltration (deposition) generally followsa kinetic process (see Sections 6.2.3 and 6.16.2 
in this AMR). Equation 31 in this AMR indicates that an increase in temperature increases 
the forward filtration coefficient +, indicating to an increase in the filtration (deposition, 
clogging) rate. There is no information on the effect of temperature on the reverse filtration 
coefficient . 
Thus, an increasing temperature in the UZ enhances diffusion (a particularly important 
mechanism in species mass transfer from the flow-dominating fractures to the matrix) and 
increases sorption and/or filtration. The cumulative effect is slower transport. The assumption 
of isothermal transport should not be viewed as an approximation of the prevailing conditions 
in the UZ, but rather as a condition that reflects a worst-case transport scenario and leads to 
conservative estimates of radionuclide travel times to the water table . Investigation of the 
effect of water phase chages on transport may be included in future revisions of the present 
AMR. 
Applicability: This assumption applies to all studies in this AMR (Sections 6.4 to 6.17). No 
further confirmation is required for the purposes of this study. 
9. The concentration of the radioactive solutes or colloids is at a tracer level, i.e., too low to have 
any measurable effect on the flow regime. 
Rationale: Ambient tracers and radionuclides escaping from the potential repository are 
expected to occur at concentrations that are too low to affect the aqueous solution density 
(CRWMSM&O 1999e, Section 6.3). 
Applicability: This assumption applies to all studies in this AMR (Sections 6.4 to 6.17). No 
further confirmation is required for the purposes of this study. 
10. There is no phase change, i.e., no water evaporation and condensation. 
Rationale: The rationale for this assumption is covered by the discussion in assumption (5). 
Water evaporation and condensation due to the heat generated by the radioactive decay of the 
wastes is covered by CRWMS M&O (2000b, Section 6.5), in which it is shown that phase 
changes are not expected to last longer than the first 10,000 years after the waste placement 
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(i.e., a rather short time compared to the 100,000 to 1,000,000 years covered by the studies in 
this AMR) and are limited to a rather small volume in the immediate vicinity of the potential 
repository. However, investigation of the effect of water phase chages on transport may be 
included in future revisions of the present AMR. 
Applicability: This assumption applies to all studies in this AMR (Sections 6.4 to 6.17). No 
further confirmation is required for the purposes of this study. 
11. Filtration of colloids is limited to deep filtration, i.e., it does not affect the medium porosity 
and permeability. 
Rationale: Pseudocolloids (i.e., colloidal waste forms) and natural pseudocolloids (such as 
clays)undernatural conditions arepresent insufficiently smallconcentrations (CRWMSM&O 
1999f, Section 6) to make this a valid assumption. This reference also indicates that, as a 
result of adverse chemical conditions (e.g., pH, ionic strength) in the immediate vicinity of 
the potential repository, true colloids (i.e., radionuclides in colloidal form) will be released in 
low concentrations for a long time. 
Applicability: This assumption applies to the colloid studies in this AMR (Section 6.16 and 
6.17). No further confirmation is required for the purposes of this study. 
These assumptions allow decoupling of the flow and transport equations. The Richards equation 
is first solved in the flow component of transport, followed by the sequential solution of the n 
independent tracer transport equations. 
5.3 ASSUMPTIONS INVOLVEDIN THE DUAL-CONTINUAAPPROACH 
The treatmentof fracture-matrix interactions is a critical issue inthe simulation of flow and transport 
under the two-phase flow conditions of the fractured UZ rocks. This AMR closely follows the 
approach of (CRWMSM&O 1999d, Section 6.1.2), which assumes the following: 
12. The dual-permeability model is a valid approximation for flow and transport simulations in 
the fractured UZ rocks. 
Rationale: In addition to its computational efficiency, this model has a strong conceptual 
basis because it describes the matrix and fractures as separate but interconnected gridblocks 
and permits flow and transport between matrix gridblocks, fracture gridblocks, and fractures 
and matrix. A more detailed discussion on the rationale for this assumption can be found in 
(CRWMSM&O 2000c, Section 5.3) 
Applicability: This assumption applies to all 3-D site-scale studies in this AMR (Sections 
6.4.3 and 6.11 to 6.17). No further confirmation is required for the purposes of this study. 
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5.4 ASSUMPTIONS INVOLVINGINITIAL AND BOUNDARY CONDITIONS 
13. The top boundary of the UZ model domain in the numerical simulations is maintained at 
spatially variable conditions of 
(a) temporally constant gas pressure and saturation, 
(b) temporally constant temperature, and 
(c) temporally constant infiltration rates (steady state). 
Rationale: The spatial variations of the parameters reflect differences in elevation, climate 
and topography, and represent realistic approximations of the prevailing conditions. For 
sufficiently long simulation periods, temporal variations in these parameters tend to diminish. 
Moreover, at a relatively short distance below the land surface, such temporal variations 
diminish rapidly. 
Applicability: This assumption applies to all 3-D site-scale studies in this AMR (Sections 
6.4.3 and 6.11 to 6.17). No further confirmation is required for the purposes of this study. 
14. The bottom boundary of the UZ model domain in the 3-D simulations coincides with the water 
table . It is maintained at spatially variable conditions of 
(a) temporally constant water pressure and saturation, and 
(b) temporally constant temperature. 
Rationale: This is a good representation of conditions in the saturated zone for the reasons 
discussed in the rationale for Assumption 13. 
Applicability: This assumption applies to all 3-D site-scale studies in this AMR (Sections 
6.4.3 and 6.11 to 6.17). No further confirmation is required for the purposes of this study. 
15. In the numerical studies of radionuclide transport, the boundaries of the UZ domain through 
which flow and transport occur are the top and bottom boundaries (i.e., the ground surface 
and the groundwater, respectively). No lateral flow and/or transport occur across any other 
boundaries. 
Rationale: The flow and transport through the top and bottom boundaries is consistent with the 
patterns of rainfall-fed infiltration and gravity-drivenflow and drainage. The distance between 
the potential repository and these boundaries is sufficiently large to justify the assumption of 
no lateral flow and/or transport. 
Applicability: This assumption applies to all 3-D site-scale studies in this AMR (Sections 
6.4.3 and 6.11 to 6.17). No further confirmation is required for the purposes of this study. 
16. The potential repository is located in the TSw hydrogeologic unit. 
Rationale: This is consistent with the repository design in CRWMSM&O (1999g). 
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Applicability: This assumption applies to all UZ transport studies in this AMR (Sections 6.5 
to 6.9 and 6.11 to 6.17). No further confirmation is required for the purposes of this study. 
17. In the transport studies of radionuclides released from the wastes in the potential repository, 
the initial tracer (solute or colloidal species) concentrations are assumed to be 
(a) constant in the gridblocks corresponding to the potential repository, and 
(b) zero throughout the rest of the domain. 
Rationale: This is an accurate system description. The very large mass of radionuclides 
stored in the potential repository and their low release rates (CRWMS M&O 1999e, Section 
6.3; CRWMS M&O 1999f, Section 6) support the case for continuous constant release over 
the simulation periods. This is accomplished by treating the potential repository gridblocks 
as internal boundary gridblocks. 
The radionuclides investigated in this AMR are 99Tc, 237Np and 239Pu. These do not occur 
naturally. Thus the assumption of zero initial concentration in the UZ domain is accurate. 
Applicability: This assumption applies to all UZ transport studies in this AMR (Sections 6.5 
to 6.9 and 6.11 to 6.17). No further confirmation is required for the purposes of this study. 
5.5 ASSUMPTIONS INVOLVEDIN THE 2-D SEMIANALYTICAL STUDIES 
The semianalytical model of transport through layered fractured media is based on some of the 
assumptions previously discussed. More specifically, it assumes isothermal steady-state flow and 
incorporates all the assumptions in Section 5.3. The additional assumptions it makes are the 
following: 
18. Advection occurs only in the fractures. The only mechanism of radionuclide transport from 
the fracture to the matrix is molecular diffusion (matrix diffusion). 
Rationale: This is a necessary assumption for the development of the semianalytical solution. 
Because of the significantly smaller magnitude of the water velocity in the matrix compared 
to that in the fractures (Bodvarsson et al. 1999, p: 14), this is a reasonable approximation. 
Applicability: This assumption applies to all 2-D studies in this AMR (Sections 6.4 to 6.9). 
No further confirmation is required for the purposes of this study. 
19. The upper bound of radionuclide transport predictions can be obtained by assuming that 
transport between the non-aligned fractures in adjacent layers is continuous, i.e., by not 
considering transport along the layer interface between the offset fractures. 
Rationale: This is a valid assumption. By not considering transport along the layer interface, 
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diffusion into and sorption onto the matrices (in the case of sorbing species) of the adjacent 
layers are reduced. This leads to faster transport and shorter travel times to the groundwater. 
Applicability: This assumption applies to all 2-D studies in this AMR (Sections 6.4 to 6.9). 
No further confirmation is required for the purposes of this study. 
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6. MODELS 
The objective of this AMR is to provide a defensible and credible model of radionuclide transport 
in individual vertical 2-D slices of the UZ and in large 3-D systems using the flow fields submitted 
for use in TSPA calculations (CRWMS M&O 1999d, Section 6.6). In this section we describe the 
development, verification and calibration of the Radioactive Transport Model (RTM). The primary 
objectives of the RTM are: 
 Using the comprehensive calibrated 3-D model of the unsaturated flow developed in CRWMS 
M&O (1999d, Section 6.2.5), to integrate the available data for the development of a 
comprehensive model of radionuclide transport through the UZ of the YM under a range 
of current and future climate conditions. 
 Toidentifythecontrollingtransportprocessesand phenomena,andtoevaluatetheeffectiveness 
of matrix diffusion and sorption as retardation processes. 
 To identify the geologic features that are important to radionuclide transport. 
 To obtain an estimate of the migration of important radionuclide solutes and their daughter 
products from the potential repository toward the groundwater. 
 To evaluate the effects of various climatic conditions on radionuclide transport. 
 To evaluate the effect of three perched water conditions on radionuclide transport. 
 To obtain an estimate of the migration of radioactive colloids from the potential repository 
toward the groundwater, and to determine the sensitivity of colloid transport to the kinetic 
coefficients of colloid filtration. 
 Toevaluate the effect of fracture spacing, intensity and configuration on radionuclide transport 
and retardation through important hydrogeologic units. 
This section consists of the following subsections: 
Section 6.1. Geological Model and Physical Processes. In this section we focus on (a) the geology 
and stratigraphy in the UZ of YM in relation the likely site for the potential repository, (b) the 
processes and phenomena involved in and affecting transport, and (c) important issues that may 
have an impact on the predictions and understanding of the transport behavior of radioactive solutes 
and colloids in the UZ. 
Section 6.2. Mathematical Model of Transport. In this section we present the mathematical basis 
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and discuss the implications of the various processes and phenomena involved in the transport of 
solutes and colloids in the UZ. 
Section 6.3. The Numerical and Semianalytical Models. In this section we discuss the codes that 
implement the semianalytical and numerical models developed based on the principles discussed in 
Section 6.2. These codes are FRACL V1.0 (STN: 10191-1.0-00, hereafter referred to as FRACL) 
and TOUGH2 V1.11 Module EOS9nT V1.0 (STN: 10065-1.11MEOS9NTV1.0-00, hereafter 
referred to as EOS9nT), respectively, and were used for the simulations discussed in Sections 
6.4 to 6.9 and 6.11 to 6.17. 
Section 6.4. Model Validation and Calibration. This section includes a short validation study, 
followed by calibration studies of FRACL and EOS9nT against field measurements and other 
numerical predictions. 
Section 6.5. 2-D Transport Simulations in Individual Hydrogeologic Units. In this section we 
discuss the individual hydrogeologic units in three representative vertical cross sections (within the 
proposed site of the repository) that are the domains for the ensuing 2-D simulations (Section 6.6 
to 6.9). The radionuclides (solutes) considered in these simulations and general issues related to 
the application of the FRACL code are also discussed. 
Section 6.6. 2-D Transport in the TSw Layers. In this section we investigate the transport patterns 
of three radionuclides (99Tc, 237Np, and 239Pu) in the layers of the TSw hydrogeologic units in the 
three vertical cross sections. 
Section 6.7. 2-D Transport in the CHn Layers. In this section we study the transport of 99Tc, 
237Np, and 239Pu in the layers of the CHn hydrogeologic units (underlying the TSw units) in the 
same three cross sections. 
Section 6.8. 2-D Transport in the PP Layers. In this section we study the transport of 99Tc, 237Np, 
and 239Pu in the layers of the PP hydrogeologic units (underlying the CHn units) in the same three 
cross sections. 
Section 6.9. 2-D Transport Underneath the Potential Repository. In this section we discuss 
radionuclide transport in composite 2-D sections covering the geologic spectrum from the potential 
repository to the groundwater in order to evaluate the integrated transport performance of the 
completegeologic systembeneath thepotentialrepository. Aconceptual model oftransport through 
the various hydrogeologic units is also presented. 
Section 6.10. 3-D Busted Butte Studies. In this section we conduct a modeling study to predict 
the concentration and water saturation distributions of various non-reactive tracers injected into 
Busted Butte rocks. These predictions are compared to currently available measurements from 
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field injections, or will be used for comparison when additional field data become available. 
Section 6.11. 3-D Transport Simulations. In this section we discuss the grids, climatic conditions, 
perched water model, radionuclides and flow fields used in the ensuing 3-D site-scale simulations 
of transport through the UZ (Sections 6.12 to 6.17), as well as the conditions and general options 
used in these EOS9nT simulations. 
Section 6.12. 3-D Simulations of 99Tc Transport. In this section we study the transport of 99Tc 
through the UZ under various climatic scenarios, and show that the 3-D EOS9nT prediction of the 
99Tc travel time to the groundwater is consistent with the 2-D FRACL prediction from Section 6.9. 
Wealso identifytransport-controllinggeologic features,transport patternsandimportant retardation 
mechanisms. 
Section 6.13. 3-DTransportof 237NpanditsDaughters. In thissectionwe investigate thetransport 
of 237Np through the UZ under various climatic scenarios and determine that the contribution of 
its daughters to releases at the water table is negigible. We identify transport-controlling geologic 
features and important retardation mechanisms, and we compare the concentration distributions 
and the transport patterns of 237Np to those of 99Tc. We also show that the 3-D EOS9nT site-scale 
prediction of the 237Np travel time to the groundwater is consistent to that from the 2-D FRACL 
simulations from Section 6.9. 
Section 6.14. 3-D Transport of 239Pu and its Daughters. In this section we study the transport of 
239Pu through the UZ under various climatic scenarios and determine that the contribution of its 
daughters to releases at the water table is significant. We identify transport-controlling geologic 
features and important retardation mechanisms, and we compare the concentration distributions 
and the transport patterns of 239Pu to those of 99Tc and 237Np. Wealso show that the 3-D EOS9nT 
site-scale prediction of the 239Pu travel time to the groundwater is consistent to that from the 2-D 
FRACL simulations from Section 6.9. 
Section 6.15. Effect of VariousPerched-WaterRegimes on3-D Transport. Radionuclide transport 
under three different perched water models is studied in this section, and the differences in transport 
behavior are discussed. 
Section6.16. 3-DSite-ScaleTransportofPuTrueColloids. Inthissectionwestudythetransportof 
four radioactivecolloids through theUZ for amean present-day infiltration and the #1 perchedwater 
model. Weidentify transport-controlling geologic features and important retardation mechanisms, 
and discuss the differeces between the transport patterns of the four colloids. 
Section 6.17. Alternative Models. In this section we investigate an alternative model of transport 
that does not consider diffusion. The transport behavior and patterns of solutes and colloids under 
thealternativemodel arecompared tothose from thestandard model ofnon-zero diffusion discussed 
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in Sections 6.12 to 6.16. 
The scientific notebooks used for the activities in this AMR are listed in Table 6.1. 
Table 6.1. Scientific notebooks used for AMR U0060 
LBNL Scientific Notebook YMP M&O Scientific 
Notebook ID 
Page Numbers Accesion Number 
YMP-LBNL-GJM-3 SN-LBNL-SCI-099-V1 675-768 MOL.19991221.0429 
YMP-LBNL-GSB-QH-1 SN-LBNL-SCI-168-V1 1-38 MOL.19991221.0430 
6.1 GEOLOGICAL MODEL AND PHYSICAL PROCESSES 
6.1.1 Geological Layering 
Thesubsurfaceformations at YMconsists ofheterogeneous layersofanisotropic, fractured volcanic 
rocks. There are alternating layers of welded and nonwelded ash flow and air fall tuffs. The 
cooling history of these volcanic rock units determines their mechanical and hydrologic properties. 
Beginning from the land surface, the YM geologic units are the Tiva Canyon, Yucca Mountain, 
Pah Canyon, and the Topopah Spring Tuffs of the Paintbrush Group. Underlying these are the 
Calico Hills Formation, and the Prow Pass, Bullfrog, and Tram Tuffs of the Crater Flat Group. 
These formations have been divided into major hydrogeologic units based roughly on the degree of 
welding. These are the Tiva Canyon welded (TCw); the Paintbrush nonwelded (PTn), consisting 
primarily of the Yucca Mountain and Pah Canyon members and the interbedded tuffs; the Topopah 
Spring welded (TSw); the Calico Hills nonwelded (CHn); and the Crater Flatundifferentiated (CFu) 
hydrogeologic units (Bodvarsson et al. 1999, p: 8; CRWMSM&O 1999h, Section 6). 
Conceptual models of flow and transport at YM are described in CRWMS M&O (1999d, Section 
6). In the present AMR, we focus on the subject of radionuclide transport in the hydrogeologic 
units beneath the potential repository horizon. A likely site for the potential repository is the TSw 
unit (CRWMS M&O 1999g), and more specifically the tsw34, tsw35, and tsw36 layers of the 
unsaturated zone (UZ), depending on the location. More information on these layers can be found 
in CRWMSM&O (1999h, Section 6) and CRWMSM&O (2000d, Section 6). Unsaturated flow in 
the TSw is primarily through the fractures, because the matrix permeability in many of the TSw 
layers can support flows of only a few millimeters per year, and the average fracture spacing in the 
TSw layers is on the order of 0.5 m (CRWMS M&O 2000d, Section 6; Bodvarsson et al. 1999, p: 
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13). 
The CHn unit and the Prow Pass (PP) unit (formally a part of CHn, but studied separately in the 
present AMR) below the potential repository horizon are complex geological systems with very 
heterogeneous distributions of fracture and matrix hydrological properties that are expected to have 
pronounced effects on flow and transport of radionuclides in the UZ. There is limited information 
on the CHn unit, and even less on PP.The permeability of nonwelded tuffs is strongly dependent on 
the degree of alteration of the rock minerals into zeolites. Zeolitic alteration in the CHn (a common 
occurrence in its lower layers) can reduce the matrix permeability by orders of magnitude in relation 
to that of the welded tuffs (CRWMSM&O 2000d, Section 6). In nonwelded vitric tuffs, the matrix 
and fracture permeabilities are on the same order of magnitude (CRWMSM&O 2000d, Section 6). 
Thus, these layers behave as porous (rather than fractured) media, and flow is matrix-dominated. 
This has important implications for transport, as the longer contact times in these nonwelded tuff 
units allow increased radionuclide sorption. 
The CHn major hydrogeologic unit is composed of vitric (CHv) and zeolitic (CHz) units (CRWMS 
M&O 1999h, Section 6). Typically, radionuclides are more strongly adsorbed onto zeolitic units 
than onto vitric units (DTN: LAIT831341AQ96.001). For example, the Kd (see Equation 9) of 
237Np in the vitrified and the zeolitic tuffs is 1 mL/g and 4 mL/g, respectively (DOE 1998b, p: 
3-122). Consequently, migration of 237Np is expected to be more retarded in the zeolitic than in 
the vitrified units, if the contact time is the same. 
Flow in the CHz units is expected to be concentrated in the fractures because of low fracture 
density (compared to the TSw) and the large permeability contrast between matrix and fractures 
(CRWMSM&O2000d, Section6);thepermeabilityinthefracturesisaboutfiveordersofmagnitude 
larger than in the matrix. Fracture-dominated flow is associated with short contact times, limited 
radionuclide removal through diffusion and sorption, and thus transport over longer distances. 
6.1.2 Transport 
Radioactive contaminants can escape from the wastes stored in the potential repository. These 
contaminants can migrate through the UZ of YM as a dissolved molecular species or in colloidal 
form. Transport of these radioactive solutes or colloids involves advection, hydrodynamic 
dispersion, sorption (solutes) or filtration (colloids), matrix diffusion, and radioactive decay. The 
transport of radionuclides is also affected by factors such as solubility limits, the presence of 
perched water, and heating effects from the potential repository. In this section we briefly discuss 
the phenomena, processes, and factors affecting transport. 
6.1.2.1 Advection 
Advection is the transport of dissolved or colloidal species by flowing water. In YM, flow is 
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predominately downward (in response to gravitational differentials), and so is advective transport 
(DOE 1998b, p: 3-112). Some lateral advection is also expected inresponseto lateralflow diversion 
at the boundaries of hydrogeologic units with sharp contacts in their hydraulic properties. Such 
diversion occurs in the perched water bodies of the UZ (CRWMS M&O 1999d, Section 6.2.2). 
Laterally diverted flow ultimately finds a pathway to the water table through other, more permeable 
zones (e.g., faults). 
Advectionisprobably themostimportanttransport processinthis studybecauseitcontrolsthespeed 
at which radionuclides move through the UZ to reach the water table. Advection in the fractures 
is expected to be the dominant transport mechanism in many layers of the various hydrogeologic 
units. This is because the expected flow rates in the matrix exceed the matrix permeability (which 
gives the measure of flow capacity under the gravitational gradient). This leads inevitably to flow 
focusing in the more permeable fractures. Advection is the dominant transport mechanism in the 
fractures because of high permeability, limited fracture pore volumes, limited contact area and short 
contact times between the radionuclide-carrying liquid phase and the matrix (only at the fracture 
walls). In a few hydrogeologic units, such as the CHv, matrix flow is dominant, resulting in much 
slower transport velocities (compared to those in the fractures of other units) and longer contact 
times of the radionuclides with the matrix (DOE 1998b, pp. 3112). 
6.1.2.2 Hydrodynamic Dispersion 
The hydrodynamic dispersion combines mechanical dispersion, which is caused by localized 
velocityvariations,andmoleculardiffusion,whichiscausedbyBrownianmotionandisproportional 
to the concentration gradient. The dispersion of the radionuclides can occur both along and 
transverse to the average flow direction. Hydrodynamic dispersion leads to the smoothing of 
sharp concentration fronts and reduces the breakthrough time (which can be defined as the arrival 
time of the edge of the contaminant front) at the groundwater table. 
There is little information on the values of the longitudinal (L) and transverse (T ) dispersivity 
([L]) in the various hydrogeologic units of the UZ. In past simulations (DOE 1998b, p: 3122), the 
longitudinal dispersivity (L) values for both the fractures and the matrix of all units had a mean 
of 20 m and a standard deviation of 5 m. Dispersion is not expected, however, to play a significant 
role in the advective transport of radionuclides in the fractures because of the predominant role of 
advection as the main transport mechanism. 
Dispersion is affected by the scale of observation. The value of dispersivity appears to increase with 
the scale of observation (Gelhar et al. 1992, p. 1955; Fetter 1993, p. 65-66). Thus, L increased 
from 102 to 104 m when the observation scale increased from from 101 to 105 m, and its value 
does not appear to be significantly affected by the texture (porous versus fractured) of the aquifer 
medium (Gelhar et al. 1992, p. 1955). 
The ratio L=T controls the shape of a contaminant plume in multidimensional transport. There is 
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a paucity of data on the relationship between L and T . Based on limited field data, Fetter (1993, 
p: 65-66) reported that L=T ranged between 6 and 20. Gelhar et al: (1992, p: 1955) indicated 
that vertical T is typically an order of magnitude smaller than the horizontal L. 
6.1.2.3 Sorption 
Sorption is a general term that describes a combination of chemical interactions between the 
dissolved radionuclides and the solid phases, that is, either the immobile rock matrix or colloids 
(mobile or immobile). In transport studies, the concept of sorption does not identify the specific 
underlying interactions, such as surface adsorption, precipitation, and ion exchange. By removing 
a portion of the mass of the dissolved species from the mobile liquid phase and transferring it to 
the immobile solid phase, sorption reduces the rate of advance of (i.e., retards) the concentration 
front of a dissolved or suspended species. 
In YM studies, the effective Kd approach (see Equation 9) is employed to quantify the extent of 
radionuclide-rock interactions by measuring the overall partitioning between the aqueous and the 
solid phase. Threebasicrock types(devitrifiedtuffs, vitric tuffs, andzeolitic tuffs)havebeenstudied 
as having distinctively different (i.e., from each other) sorption interactions with the radionuclides 
(DOE 1998b, p. 3-118). The Kd values for several radionuclides in each of these rock types are 
listed in the TSPA conceptual model (DOE 1998b, p: 3-122). Note that sorption is not only a 
function of the sorptive strength (as quantified by the value of Kd), but also of the contact time of 
the radionuclides with the rock matrix during transport through the UZ. 
Sorption kinetics could be important, especially for radionuclides sorbing onto zeolitic tuffs. 
Column experiments of 237Np transport in tuffs (Viswanathan et al. 1998, p. 267) indicate the 
existence of kinetic sorption under flowing conditions, possibly as a result of the slow diffusion of 
237Np into the tuff pores. It is not possible to analyze these experimental data without considering 
a kinetic sorption model. Kinetic sorption can have a substantial effect on transport in fast fracture 
flow because it reduces sorption in the matrix, thus allowing larger radionuclide concentrations and 
migration over longer distances in the fractures. Nonlinear and irreversible sorption are evident 
from the diffusion and transport studies discussed in CRWMSM&O (1999e, Section 6.4). 
The Kd values used in the YM studies have been estimated from batch experiments using crushed 
tuffs with a particle size of 75  500 munder saturated conditions (CRWMSM&O 1999e, Section 
6.4). There are indications that this experimental approach may overestimate the Kd values. This 
is because the batch experiment conditions (involving saturated crushed tuff samples) may not be 
representative of the UZ conditions, which are characterized by unsaturated conditions, a limited 
contact area and short contact times (see Section 6.1.3.1 for a more thorough discussion). The 
importance of kinetic, nonlinear, and irreversible sorption may need to be evaluated against the 
linear equilibrium isotherm assumed in UZ transport studies. 
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6.1.2.4 Matrix Diffusion 
Diffusion can play an important role in radionuclide exchange between the fractures and the 
rock matrix. This process transfers radionuclides into the matrix (where water flow is slow and 
sorption occurs), thus removing them from (and slowing the advance of their front in) the fast 
fracture flow. Diffusive flux acros a given interface is a function of the concentration gradient, the 
temperature, the size of the dissolved species and its electric charge, the matrix pore structure and 
the water saturation (DOE 1998b, p. 3-116  3-117). 
Matrix diffusion is a linear function of tortuosity coefficient , which describes the tortuous nature 
of the pore networks (Grathwohl, 1998, p: 2835), including dead-end pores and steric hindrance 
(in extremely narrow pores). Note that, according to the definition used in this AMR,  < 1. 
There are very limited experimental data on the  distribution in the various YM hydrogeologic 
units. In this study,  is approximated by the value of porosity  (Farrell and Reinhard, 1994, p.64; 
Grathwohl, 1998, p: 2835). 
This approach was confirmed experimentally. From rock diffusion experiments using devitrified 
tuffs, the effective diffusion coefficient De (=   Sw D0, where D0 is the molecular diffusion 
coefficient [L2T1] and Sw is the water saturation) for 3H2O was obtained from six tuff samples. 
Based on the literature value of D0 for 3H2O (Hu and Brusseau 1995), a  estimate of 0.0806  
0.035 was obtained in media in which the reported average porosity was 0.0767  0.019 (DTN: 
LAIT831341AQ96.001 and Scientific Notebook YMP-LBNL-GSB-QH-1, p: 23). The good match 
between these two numbers validates the approach of using the porosity value as the tortuosity 
coefficient. 
Even less information exists on the effect of Sw on De. Porter et al. (1960) reported that the 
  Sw product decreased consistently in medium- and fine-textured soils as the capillary pressure 
increased from 0.33 to 15 atm. The effect of saturation on De may be more complex than the linear 
relationship currently assumed. Supporting evidence was provided from experiments by Conca and 
Wright (1990), who determined De values for K+ ions for a variety of water contents and grain 
sizes on four types of angular crushed gravel. For volumetric water contents ranging from 0.5% 
to 6%, the De ranged from 1014 m2/s to 1011 m2/s, i.e., the dependence was much stronger 
than what could be expected from the linear relationship between De and Sw. This subject could 
merit additional attention because it can provide an additional safety factor. The linear relationship 
assumed in this AMR results in more conservative transport estimates because diffusion from the 
fractures into the matrix is reduced. 
6.1.2.5 Solubility 
The concentration of any radionuclide (released from the stored radioactive wastes at the potential 
repository) in the water cannot exceed the radionuclide solubility limit, unless suspended colloids 
are involved. Limitations to radionuclide solubility in the water infiltrating the potential repository 
constitute thefirstbarriertotransport and canreducethe extent ofradionuclide migration by limiting 
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the available source. 
The solubilities of the radionuclide of interest are reported in CRWMS M&O (1999e, Section 6). 
The lower solubility of many radionuclides can lead to slower and continuous release over time 
at the outer boundaries of engineered barrier systems surrounding the radioactive wastes because 
the source is not exhausted. For example, the solubility of 237Np is sufficiently low to extend the 
period of its release to tens of thousands of years (Viswanathan et al. 1998, p: 273). 
6.1.2.6 Colloids 
Colloids are fine particles, between 0.001 and 1 m in diameter, that become suspended and are 
transportable in a moving liquid. The generation and mobilization of colloids are considered 
important issues in contaminant transport, particularly the transport of radioactive true (intrinsic) 
colloids (e.g., colloidal Pu(IV) and Pu(V)) and the colloid-assisted transport of radioactive species 
(e.g., 239Pu, 237Np, 243Am, and 247Cm from high-level radionuclide wastes, or 137Cs, 90Sr, 
and 60Co from low-level radioactive wastes, see CRWMS M&O (1999e, Section 6)) sorbed on 
pseudocolloids (e.g., naturally occurring clay colloids). See Sections 6.1.3.3 to 6.1.3.7 for a more 
detailed discussion. 
6.1.2.7 Perched Water 
Perched water is defined as a saturated zone that is located at a higher elevation than the static water 
table, to which it is not directly connected. Perched water usually occurs where low permeability 
horizons do not permit the rapid downward flow of water. Such bodies have been reported at several 
locations in UZ boreholes (Wu et al. 1999). The presence of perched water has implications for 
the travel times and flow paths of water and radionuclides through the UZ. 
The majority of the perched water bodies detected in the UZ boreholes were observed in formations 
overlaying relatively impermeable matrix material, such as the TSw basal vitrophyre (a glassy 
cooling unit). Although the vitrophyre is extensively fractured, many of the fractures have been 
filled with zeolitic material, thus limiting flow. A portion of the Calico Hills formation has been 
extensivelyalteredtozeolites, creatingperchedwater bodies(Bodvarssonetal. 1999, p.14-15). The 
blockage of fracture flow which occurs in these perched water bodies can lead to lateral diversion 
of radionuclide migration if the percolation flux is sufficiently large. 
Three perched water models, namely no perched water, perched water model #1 (flow through the 
perched water), and perchedwater model #2 (flow bypassing the perchedwater) havebeen proposed 
in CRWMS M&O (1999d, Sections 6.2.2 and 6.2.5). The effects of each of these perched water 
models on radionuclide transport will be investigated in the 3-D site-scale simulations discussed in 
Section 6.15. 
6.1.2.8 Daughter Products 
Chain-decay adds another layer of complexity because of the need to account for the transport of the 
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daughter products, i.e., the new radionuclides created from the decay of a parent radionuclide. The 
daughter products may have significantly different transport behavior than the parent radionuclide. 
Thus, the migration and fate of all the important members of the decay chain, rather than just the 
parent radionuclide, must be considered. 
6.1.2.9 Effect of Heat on Transport 
Radionuclide transport may also be influenced by the heat generated by the decaying radioactive 
waste, which affects the ambient hydrologic and chemical conditions and can thermally alter the 
rock near the potential repository. For example, if the zeolitic layers below the potential repository 
horizon are thermally altered, the sorption of radionuclides is reduced. 
In addition to the thermal effect on the flow field and radionuclide sorption coefficient, temperature 
also enhances diffusion by increasing Brownian motion. This effect is quantified by an increase 
in the D0 of radionuclides. The temperature-dependent D0 is described by the following equation 
(Robin et al. 1987, p: 1105-1106): 
D0 
T T1 
= D0 
T T2 
where T is the absolute temperature and  is the viscosity of water. 
The effect of temperature on sorption has been discussed in CRWMSM&O (1999e, Section 6.4.6). 
In general, an increase in temperature leads to increased sorption of cationic species and decreased 
sorption of anionic species. In addition to theoretical predictions, CRWMSM&O (1999e, Section 
6.4.6) includes a discussion of experimental data that show an increase of sorption by an order of 
magnitude when temperature increases from 25 oC to 75 oC. 
Temperatures in the UZ increase naturally with depth because of the geothermal gradient. 
Additionally, heat from the stored waste is expected to lead to higher temperatures over a large 
volume of the UZ for as long as 100,000 years (CRWMSM&O 2000b, Section 6.5). The combined 
effect of higher temperatures is increased retardation of the radionuclides becaused of (a) increased 
dffusion from the fractures into the matrix and (b) increased sorption. The assumption of isothermal 
25 oC conditionsinthestudiesof thepresent AMRreflectsaconservativeapproachand yieldsresults 
that describe the worst-case scenario. 
6.1.3 Important Transport Issues 
6.1.3.1 Measurements of Kd Values 
The sorption behavior of radionuclides is usually described by the distribution coefficients (Kd), 
which quantifies the partitioning of radionuclides between the solid and aqueous phases under a 
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linear equilibrium isotherm. Most of the Kd values are obtained from batch experiments using 
crushed rock, the particle size of which is determined only by experimental convenience and is 
more or less arbitrary. 
Compared to intact rock samples, batch experiments using crushed rock samples may overestimate 
the Kd values. Crushing of the material creates new contact surfaces and also increases the 
radionuclide accessibility to pores that may not contribute to sorption to intact rocks. Comparison 
of the Kd values obtained from batch sorption experiments and from diffusion experiments (which 
use larger samples) show significant differences, which are attributed to differences in the size of 
the samples. 
Bradbury and Stephen (1985) investigated the sorption of 85Sr, 85Tc, 125I, and 137Cs onto Darley 
Dale sandstone samples. Comparing Kd values obtained from batch (using <0.1 mm and 1-2 mm) 
and diffusion-sorption experiments (using disks of 25mmindiameter and about 5mminthickness), 
they determined that crushed rock tests can overestimate sorption by as much as one or two orders 
of magnitude. They concluded that the magnitude of the difference in the value of Kd depends on 
the radionuclide, its concentration, the rock, the water/solid ratio, and the particle size distribution 
in the batch tests. 
Holtta et al. (1997) studied the effect of specific surface area onthe sorption of 22Na, 45Ca and 
85Sr on crushed crystalline rocks of six size fractions (0.071-0.15, 0.15-0.20, 0.2-0.3, 0.3-0.85, 
0.85-1.25, >1.25 mm). Sorption of 22Na, 45Ca and 85Sr on unaltered tonalite and mica gneiss was 
slight and exhibited virtually no dependence on the fraction size. Considerably higher sorption 
of 22Na and 85Sr occurred on altered tonalites of smaller fractions because of their larger specific 
surface areas. Kd values from thin sections (0.030 mm in thickness) were in good agreement with 
those obtained from batch experiments, possibly because the thin-section thickness is within the 
range of the crushed-rock size fractions. 
Johansson et al. (1997; 1998) conducted batch sorption tests of alkali- and alkaline earth metals 
(22Na, 137Cs, 45Ca, 85Sr, and 133Ba) using six crushed size fractions (0.045-0.090, 0.090-0.25, 
0.25-0.5, 0.5-1, 1-2, 2-4 mm) of medium-grained Aspo diorite and fine grained granite. The Kd 
increased with a decreasing particle size, and differed by approximately one order of magnitude 
between the largest and smallest particle because of different specific surface areas. They also 
determined that the the best agreement between the Kd values from diffusion experiments (using 
20 mm rock disks) and from batch experiments was observed for the largest size fractions (2-4 
mm) in the batch studies. They explained this observation by suggesting that, unlike the smaller 
fractions, the largest size fraction involved a large number of whole mineral grains. 
Tachietal : (1998)studiedthesorptionanddiffusionbehaviorofSeinTonotuffsinbatchexperiments 
(using crushed rock with sample sizes ranging between 0.075 and 0.355 mm) and in throughdiffusion 
experiments (using samples 30 mm in diameter and 5 mm in thickness). The Kd values 
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from the diffusion experiments were one order of magnitude lower than those from the batch 
experiments. Correcting for the difference in the specific surface areas could not fully account for 
theKd discrepancy. Mercury porosimetry suggested that the differences were caused by sorption in 
microscopic pores (less than 20 nm in diameter) in the crushed rock samples. Whenthe contribution 
of these pores to sorption was not considered, the Kd values from the batch sorption experiments 
and from the diffusion experiments were consistent. 
The effect of the specific area surface of ground rock samples on the sorption of 137Cs, 85Sr, and 
237Np was studied in nine size fractions (< 0.038, 0.038-0.063, 0.063-0.075, 0.075-0.106, 0.106- 
0.25, 0.25-0.50, 0.5-1, 1-2, 2-4 mm) of devitrified Topopah Spring tuff and zeolitized Calico Hills 
tuff(Rogersand Meijer1993). Theyshowedthatthegrindingprocessdoesnotinfluence thesorption 
behavior for particle sizes larger than about 63 m. They also indicated that ground samples must 
be washed carefully to remove very fine particles generated during the grinding process, which 
could lead to irreproducible or anomalously high Kd values. 
6.1.3.2 Sorption of 129I and 99Tc 
Iodineandtechnetium,whicharepresentrespectivelyasI  andpertechnetate(TcO 4 )underambient 
oxidizing conditions, do not sorb onto tuffs. The recommended sorption coefficient for both iodine 
and technetium is therefore zero for performance assessment in both saturated and unsaturated units 
(DOE 1998b, p: 3-122). 
I is expected to have no significant retardation in the YM rock-water system and may even have 
slightly enhanced migration rates because of anion-exclusion effects. If conditions were to become 
sufficiently oxidizing to convert iodide to iodate, some retardation of iodine is possible. Although 
such conditions can occur locally for a short time (e.g., due to radiolysis), it is unlikely that they 
can occur over a significant volume of the flow system for an extended period of time (CRWMS 
M&O 1999e, Section 6). 
99Tc appears to show nonzero, though minimal, retardation in the YM rock-water systems, which 
could be important in long-term transport. If, however, sufficiently reducing conditions could be 
shown to occur in portions of the flow system between the potential repository and the groundwater, 
precipitation and sorption of the Tc4+ species can result in significant retardation of 99Tc (CRWMS 
M&O 1999e, Section 6). 
6.1.3.2.1 Potential Sorption of Anions 
Adsorption of negatively-charged ionic species from the aqueous phase onto mineral substrates is 
likely to occur whenever the mineral surface exhibits a net positive surface charge. Most rockforming 
alumino-silicate minerals under typical ambient conditions in shallow systems (saturated 
or unsaturated) have negatively charged surfaces. It is possible, however, for these surfaces to 
become positively charged in the presence of acids or if the surfaces dry out and only residual 
oligolayers of water remain. 
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The transition from negatively to positively charged surface occurs at the point of zero charge 
(PZC), where the surface charge is zero, and is usually expressed in terms of pH. The PZC differs 
from one mineral to another, but for most rock-forming minerals it is less than 4. However, in some 
materials (such as iron oxides, sulfides and some organic matter), the PZC can be as high as 8 or 9. 
These minerals display a tendency to adsorb anionic species such as I and TcO4 
under ambient 
groundwater conditions. For example, the extent of AsO3 4 sorption on hydrous ferric oxide is a 
function of pH (Dzombak and Morel 1990, pp: 200-204). The edge sites on clays are also reported 
to contain positive sites. Under low pH conditions (e.g., pH = 5), significant sorption of anionic 
tracers occurs in systems with high concentrations of iron oxides and kaolinite (Boggs and Adams 
1992; Seaman 1998). 
Despite the availability of positively charged adsorption sites, 129I and 99TcO4 
are in competition 
with other anionic species in solution, such as SO2 4 , NO3 
, OH etc, which are usually present in 
concentrations orders of magnitude larger than either 129I or 99TcO4 
. Because of competition, 
their effective sorption is minimal. There are, however, exceptions, and these should be taken into 
account when evaluating their retardation. 
Kaplan and Serne (1995) determined that iodine sorbed on all Hanford sediments, and its Kd 
ranged from 0.7 to 15 mL/g, with a median value of 7 mL/g. This finding could have significant 
implications for radionuclide transport. Positively charged adsorption sites may exist on the edges 
of 2:1 clays such as smectite and illite, on Al- and Fe-oxide surfaces, and on 1:1 clays such as 
kaolinite. Anions may sorb onto these locally positive-charged sites, even though their numbers 
are limited under typical pH conditions. 
Note that the study of Kaplan and Serne (1995) involved extremely low iodine concentrations 
(approximately 12 ppt). Therefore, only a small number of positively charged sites would be 
needed for the sorption of a measurable portion of the dissolved iodine. Had an initially larger 
concentration been used in these experiments (e.g., 1 ppm), it is reasonable to expect that a small 
fractionofiodinewould havesorbedonto thesolidphase, resultinginpracticallyundetectableiodine 
sorption. It must be pointed out that the 129I concentrations is expected to be in the part-per-trillion 
(ppt) range in a low-level waste plume (Kaplan and Serne 1995). 
Similarly, significant sorption of technetium could occur in soils containing considerable amounts 
of natural organic matter, which tends to sorb anionic species and could reduce technetium to its 
+4 oxidation state, causing precipitation and/or sorption (Kaplan and Serne 1995). In the UZ of 
YM, however, conditions are both oxidizing and deficient in organic matter. Therefore, significant 
sorption is unlikely to occur until more reducing conditions are encountered within the saturated 
zone. 
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Currently, there is no information on the occurrence and extent of localized positively charged 
sorption sites in YM tuffs. The existence of such sites cannot be ruled out. Clays and oxides 
can potentially contribute to positively charged sites. Smectite is a significant constituent of some 
unwelded tuff horizons at Yucca Mountain. Although hematite and illite are present in minor or 
trace amounts in the unwelded tuffs, hematite is widely distributed in the matrix of the devitrified 
units. Smectite and hematite also coat fracture walls in Yucca Mountain tuffs (CRWMS M&O 
1999e, Section 6). No estimate exists of the potential effects of such sites on the site-scale transport 
of radioactive anionic species. 
6.1.3.2.2 Solute Size Effects 
Another aspect about technetium and iodine transport is the exclusion effect resulting from their 
relatively large ionic radius and low charge density. Technetium travels faster than tritium in both 
diffusion and column studies (CRWMS M&O 1999e, Section 6). This is attributable to the large 
size of the pertechnetate anion, which is excluded from tuff pores. In contrast, in crushed-rock 
column experiments, anion-exclusion effects for pertechnetate are essentially negligible, except 
in the case of technetium transport through zeolitic tuffs in the J-13 well water. In this case, the 
anion-exclusion effect was small but measurable (CRWMSM&O 1999e, Section 6). 
It should be emphasized that 3H+ can sorb weakly onto tuffs, as TcO4 can. The faster TcO4
breakthrough curves (compared to those for 3H+) reported in CRWMS M&O (1999e, Section 
6.5.3.3) should not be necessarily interpreted to indicate TcO4 
size-exclusion, but could also 
denote larger 3H+ sorption. This is supported by the slight retardation of 3H2O reported by Hu 
and Brusseau (1996). The apparent sorption is in essence ion-exchange and has been postulated to 
occur via OH exchange on the clay lattices. 
6.1.3.3 Colloidal Behavior 
Radioactive true colloids or radionuclides adsorbed onto pseudocolloids can be transported over 
significant distances (McCarthy and Zachara 1989, pp. 496-497). The significant migration of 
strongly sorbing Pu and Am (more than 30 m) from a low-level waste site at Los Alamos National 
Laboratory through unsaturated tuff over a period of approximately 30 years is attributed to colloid 
and/or colloid assisted transport, a hypothesis confirmed by laboratory experiments (Buddemeier 
and Hunt 1988, p: 536). Using the 240Pu/239Pu isotope ratio to fingerprint the source of Pu in 
groundwater, Kersting et al. (1999, pp. 56-59) recently demonstrated that the soluble (ionic) Pu is 
practically immobile in the subsurface of the Nevada Test Site (NTS) because of its strong sorption, 
but can be transported over significant distances ( 1.3 km over a 30-year period) in a colloidal form. 
Colloids are very fine particles (such as clay minerals, metal oxides, viruses, bacteria, and organic 
macromolecules) that range in size between 1 and 10,000 nm (McCarthy and Zachara 1989, pp: 
497-498) and have high specific surface areas ('300 m2/g). Their chemical behavior is dominated 
by surface processes (EPRI 1999, p: 3-1), and can have a high sorptive capacity for contaminants. 
Colloids are deposited on porous and fractured media by surface filtration, straining filtration, and 
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physical-chemical filtration. Colloid transport differs from solute transport because the colloidal 
particle interactions (e.g., flocculation), mechanical clogging effects, and surface reactions (e.g., 
deposition or attachment) are substantially different from the solute processes and phenomena. 
A natural colloid becomes a pseudo-colloid when a radionuclide adsorbs onto it. True (intrinsic) 
Pu(IV) colloids (generated from the contaminant when its concentration exceeds its solubility) 
have been produced by the agglomeration of hydrolyzed Pu(IV) ions under acidic conditions (EPRI 
1999, p: 3-2). When immature, actinide true colloids display hydrophilic properties, but become 
hydrophobic with increasing age. 
Acomplete description of colloid-facilitated radionuclide transport requires consideration of alarge 
number of processes (EPRI 1999, pp: 4-5  4-6), including advection, diffusion, colloid generation, 
colloid stability, colloid-solute-matrix interactions, affinity of colloids for the gas-water interface, 
colloid filtration (surface and straining), and kinetically controlled physical-chemical filtration. 
6.1.3.3.1 Colloid Generation and Stability 
The formation of mobile colloidal suspensions in the subsurface is attributed to a number 
of mechanisms: (1) matrix dissolution caused by changes in pH or redox conditions; (2) 
supersaturation with respect to the inorganic species; (3) disruption of the mineral matrix by large 
changes in the flow regimes due to injection, pumping or large episodic rainfall infiltrations; (4) 
release and movement of viruses and bacteria; and (5) formation of micelles from the agglomeration 
of humic acids(Abdel-Salam and Chrysikopoulos1995, pp.199-200). Buddemeier and Hunt(1988, 
p: 536) indicate that submicrometer colloids can easily be released from mineral and glass surfaces 
that are chemically, hydrodynamically, or mechanically stressed. 
Colloid stabilization/destabilization include steric stabilization by mechanisms such as organic 
coating of inorganic colloids, and the effects of pH and ionic strength on coagulation and 
precipitation. The stability of colloid suspension is very sensitive to changes in ionic strength 
(EPRI 1999, p: 4-6). 
6.1.3.3.2 Colloid Deposition 
Colloid deposition (physico-chemical filtration) during saturated flow through a porous medium 
is commonly assumed to occur in two steps: (1) transport of colloids to matrix surfaces by 
Brownian diffusion, interception, or gravitational sedimentation (i.e., colloid-matrix collision) 
and (2) attachment of colloids to matrix surfaces. The attachment efficiency (i.e., the fraction 
of collisions resulting in attachment) is strongly influenced by interparticle forces between colloids 
and matrix surfaces, such as vander Waalsand electric double layer interactions, steric stabilization, 
and hydrodynamic forces (Kretzschmar et al: 1995, p: 435). Kretzschmar et al: (1997, p: 
1129) demonstrated that colloid deposition generally follows a first-order kinetic rate law and 
experimentally determined the corresponding collision efficiencies. 
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6.1.3.3.3 ColloidContaminantMatrix Interactions 
Colloid attachment to the host rock is strongly dependent on electrostatic interactions. Once attached, 
colloid detachment (declogging) is generally slow to irreversible. Sorption of radionuclides 
on colloids is controlled by a range of chemical processes such as ion exchange, surface complexation, 
and organic complexation (EPRI 1999, pp. 4-9). 
If sorption of metal ions onto colloids is assumed to follow an equilibrium isotherm, metals are 
stripped very fast from the colloids when these enter a clean part of the porous medium. This 
approach was incapable of explaining the long transport distances observed in field experiments 
(van de Weerd and Leijnse 1997, p. 246). The problem was addressed by assuming (a) kinetic 
sorption of radionuclides onto the humic colloids and (b) kinetic colloid deposition (van de Weerd 
and Leijnse 1997, pp. 245, 255). 
The sorption of dissolved ionic Pu(IV) onto hematite, geothite, montmorillonite, and silica colloids 
in both natural and carbonate-rich synthetic groundwater was reported to be fast (CRWMS M&O 
1999e, Section 6). Under equilibrium conditions, the Kd values of Pu(V) was about 100 mL/g for 
hematite and montmorillionite colloids. These very large values indicate that ion oxide and clay 
colloids in groundwater can significantly enhance the transport of 239Pu. 
6.1.3.3.4 Colloid Migration in Macroporous and Fractured Systems 
Jacobsen et al. (1997, pp. 185-186) conducted infiltration experiments in intact structured sandy 
loam cores using two types of colloidal suspensions, and observed significant transport of clay and 
silt colloid particles through the macropores. Macropores can enhance the transport of colloids 
because all types of filtration are less pronounced in large pores and the large water velocities can 
lead to increased detachment (as the large hydrodynamic forces can overcome the colloid-grain 
bonding forces). 
In a study of colloid-facilitated transport of radionuclides through fractured media, Smith and 
Degueldre (1993, pp. 143, 162-163) determined that the assumption of fast, linear, and reversible 
radionuclidesorptionontocolloidsisnon-conservative. Theyobservedthatthetimeforradionuclide 
desorption (days or weeks) significantly exceeded the time for sorption (seconds or minutes). Such 
radionuclide-laden colloids can migrate over long distances in macropores and fractures, and the 
larger colloids exhibit little retardation because their size prevents them from entering the wall-rock 
pores. The Smith and Degueldre (1993, pp. 143, 162-163) study concluded that the transport of 
radionuclides sorbed irreversibly on to colloids depends strongly on the extent of colloid interaction 
with the fractures. 
Vilks and Bachinski (1996, pp. 269, 272-278) studied particle migration and conservative tracer 
transport inanatural fracturewithinalargegranite blockwithoveralldimensions of 839060 cm. 
Flushing experiments showed that suspended particles as large as 40,000 nm could be mobilized 
from the fracture surface. The mobility of suspended particles with diameters of 1000-40,000 nm 
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was significantly less than that of colloids (<90 nm). They observed that the the conservative tracer 
lagged slightly behind the colloid front, but colloid mobility was significantly reduced when the 
average groundwater velocity decreased. Compared to dissolved tracers, the migration of colloids 
was more affected by the flow path and flow direction. This tendency can have a significant effect 
in the fracture-dominated flow of the UZ in the YM system. 
In field-scale colloid migration experiment, Vilks et al. (1997, pp. 203, 212-213) showed that 
silica colloids as small as 20 nm can migrate through open fractures over distances of 17 m when a 
colloidal suspension was injected at average flow velocities of 1.6 and 2.9 m/h (orders of magnitude 
higher than the natural flow rates at the site). Based on the analysis of the results of the study, they 
also suggested that although colloid migration appeared to behave conservatively, colloids may 
have followed different pathways than dissolved conservative tracers. 
6.1.3.4 Colloidal Behavior in Unsaturated Media 
Most of the available literature focuses on the behavior of colloids in saturated media. The behavior 
of colloids in unsaturated media is a relatively new area of study and has significant additional 
complexity. 
6.1.3.4.1 Filtration as a Function of Water Saturation 
Colloid filtration is a physical retardation process. Wan and Tokunaga (1997, p. 2413) distinguish 
two types of staining: conventional staining (if the colloid is larger than the pore throat diameter 
or the fracture-aperture width) and film straining (if the colloid is larger than the thickness of the 
adsorbed water film coating the grains of the rock). 
Wan and Tokunaga (1997, pp. 2413, 2419) developed a conceptual model to describe colloid 
transport in unsaturated media as a function of water saturation Sw. If the rock Sw exceeds a 
critical saturation value Sc, colloids move through the system entirely within the aqueous phase. 
For Sw < Sc, colloids can only move in the thin film of water that lines the grain boundaries, and 
colloid transport through the water film depends on two parameters: the ratio of the colloid size to 
the film thickness, and the flow velocity. Temporal variations in the Sw in the subsurface profile 
and in the infiltration rate can lead to strongly nonlinear colloid mobility in the vicinity of Sc. 
McGraw and Kaplan (1997, p. 5.2) investigated the effect of colloid size (from 52 to 1900 nm) and 
Sw (from 6 to 100 %) on colloid transport through unsaturated media in Hanford sediments. They 
showed a very strong dependence of filtration on the colloid size under unsaturated conditions. At 
a volumetric water content of 6%, (the expected water content in the Hanford vadose zone), colloid 
removal increased exponentially with the colloid size. The decrease in colloid mobility at low 
volumetric contents was attributed to resistance due to friction (as the colloids were dragged along 
the sand grains). The colloid retardation increased as the ratio between the water film thickness 
and colloid diameter decreased. 
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6.1.3.4.2 GasWater Interface 
Under unsaturated conditions, colloid transport may be either inhibited or enhanced (compared to 
that under saturated conditions) because of the presence of the air-water interface. Wanand Wilson 
(1994, pp. 857, 863) determined that he retention of both hydrophilic and hydrophobic colloids 
increased with the gas content of the porous medium. They showed that colloids preferentially 
concentrate in the gas-water interface rather than on the matrix surface. This tendency increases 
with the colloid surface hydrophobicity or contact angle, with hydrophobic colloids having the 
strongest affinity for the gas-water interface. 
The implications of this colloid behavior are important. The colloid affinity for the gas water 
interface may retard their transport through the unsaturated zone. Conversely, if the subsurface 
conditions permit the stability and migration of bubbles, colloid transport may be enhanced. 
6.1.3.5 Colloids at Yucca Mountain 
The available data on colloid occurrence and concentrations at the YM site are limited, and pertain 
to saturated zone studies. There is no published information on colloids in the unsaturated zone. 
The current state of understanding is that (a) the natural colloid concentrations in native waters at 
the YM site are low (106 - 1010 particles/mL), and (b) waste-form colloids will be the dominant 
colloidal species of concern to transport studies (CRWMS M&O 1999f, Section 6). 
Additional information from nearby sites, however, cannot be ignored. Preliminary results of a 
survey of groundwater from the Nevada Test Site (NTS) have shown that, in the Pahute Mesa 
drainage (both on and off the NTS), have colloidal particle (>3 nm in diameter) loadings of 0.8-6.9 
mg/L. Such relatively high concentrations can explain the observed transport of strongly sorbing 
radionuclides over significant distances, particularly because the ionic composition of the NTS 
groundwater is not expected to promote the coagulation of clay colloids (Buddemeier and Hunt 
1988, p. 537). This is because NTS groundwater is oxygenated and low in organic matter, and a 
substantial fraction of the colloidal material is composed of stable natural minerals (Buddemeier 
and Hunt 1988, p. 543-544). 
In addition to natural colloids, anthropogenic colloids may be created from the waste itself or from 
repository construction and sealing materials. Waste- and repository-derived colloids at Yucca 
Mountain are likely to include organic colloids, iron oxyhydroxides, and aluminosilicate colloids 
(EPRI 1999, p. 2-2, 6-22). In a 50-month experiment of simulated weathering of a high-level 
nuclear waste glass, spallation and nucleation were identified as the main mechanisms of colloid 
genesis (Bates et al. 1992, pp. 649-651). The created colloids were identified as inorganic. The 
same study determined that Pu and Am released from waste were predominantly in the colloidal, 
rather than in the dissolved, form. 
6.1.3.6 Impact of Colloids on Radionuclide Transport in YM 
EPRI (1999, pp: xv-xvii and 2-2) indicated that it is important for the YMPto consider the migration 
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of radionuclides, and assess the potential role of colloids on radionuclide transport, within both the 
saturated and the unsaturated systems. Furthermore, EPRI (1999, pp. 4-6 to 4-7) identified the 
following key areas of uncertainty for further study: 
1. Colloid-matrix interactions. 
2. Thermodynamic data for certain radionuclides and kinetic data to describe virtually all ratedependent 
reactions. 
3. Representation of the hydrological system: colloid transport differs from the transport of 
conservative tracers and is influenced by the details of the permeability structure, such as 
fracture geometry and the hydraulic conditions within the fracture zones. 
4. The effects of partially-saturated conditions on colloid transport. 
6.1.4 Important Points for Consideration in Colloid Transport 
Theassessmentofthe potentialroleof colloidsinthetransportof radionuclidesatYucca Mountainis 
particularlychallengingfor thereasonsdiscussedintheprevious sections, andis furthercomplicated 
by the following factors: 
1. Different types of colloids (minerals, organics, microbes, and polymeric actinide colloids) 
with substantially different characteristics and properties (e.g., hydrophobicity and surface 
charges) that strongly affect their behavior in the subsurface. 
2. Colloid generation, growth, stability, size distribution, and concentration are dynamic. 
Knowledge on the temporal and spatial distributions of colloid populations in the different 
hydrogeologic units is difficult to obtain. Changes in the ionic strength of the aqueous solution 
(e.g, when percolating water in an episodic infiltration event encounters resident pore water) 
canaffectcolloid stability. Therearealsouncertainties aboutthecolloid stabilityintheaqueous 
phase of the UZ and about the colloid generation from mineral-coated fracture walls (given 
the predominance of fracture flow in the UZ). 
3. Measurements of colloid concentration in the unsaturated zone are difficult. Because of the 
low concentrations and low saturations in the UZ, the determination of colloid concentration 
in pore water is challenging, and serious questions arise about sample representativity and 
integrity. 
4. The concentration of waste-form colloids is a key uncertainty. There is evidence to suggest 
that the low concentration of natural colloids in the UZ of YM will not lead to significant 
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colloid-assistedtransport, and that waste-form colloids willbe the dominantcolloidal transport 
problem (see CRWMS M&O 1999f, Section 6). Thus, there is a need for reliable estimates 
of the types and generation rates of waste-form colloids. Currently, there is considerable 
uncertainty on this subject (EPRI 1999, p. 6-7). 
Important processes to consider are: 
6.1.4.1 Colloid Diffusion 
Colloids diffuse slower than dissolved species because of their larger size (see Section 6.2.5, 
Equation 23). For the largest colloids, diffusion is approximately three orders of magnitude slower 
than that for molecular species (Nuttall et al. 1991, p: 189). For example, the diffusion coefficient 
D0 of a 0.1 m colloid at 20 oC is 4:29  1012 m2/sec (see Equation 23 in the present AMR), 
while the D0 of Br is 2:08  109 m2/sec (Cussler 1984, p.147). 
6.1.4.2 Pore Exclusion 
Using mercury porosimetry, Roberts and Lin (1997, pp. 577-578) determined that the average 
pore diameters of welded and densely welded TSw tuff samples were 53.1 nm and 19.7-21.4 nm, 
respectively. These extremely small pores are certain to exclude a significant proportion of colloids. 
It is possible for colloids to accumulate on the fracture walls and thus clog the matrix pores open to 
the fracture. This can lead to reduction in the matrix permeability and in the colloid diffusion into 
the matrix. Pore exclusion is not expected to be significant in the fractures, and colloids can travel 
cover significant distances in the fractures (especially given the limited diffusion into the matrix). 
6.1.4.3 Role of Air-Water Interface 
The affinity of colloids for the air-water interface depends on their hydrophobicity and electrostatic 
charge. Hydrophilic colloids, such as mineral fragments, have a low affinity for the interface, in 
contrast to hydrophobic colloids (such as organic colloids and microbes). This affinity increases 
with the positive charge on the colloids (EPRI 1999, p: 6-11). The flow and saturation conditions in 
the UZ will determine whether this will enhance or retard transport. Note that the potential impact 
of the air-water interfaces on colloid transport has not been quantified yet. 
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6.2 MATHEMATICALMODEL OF TRANSPORT 
The mathematical model of the flow component in thisAMR is included inCRWMSM&O (1999d, 
Section 6), in which it is thoroughly discussed. Here we focus on the mathematical model of 
transport anddiscuss theimplicationsofthevariousprocesses itdescribesforradionuclide transport. 
There are 8 subsections in Section 6.2. The basic mass balance equation of solutes and colloids 
are discussed in Section 6.2.1. Section 6.2.2 focuses on the accumulation terms of the mass 
balance equation. The equations of sorption (for solutes), filtration (for colloids) and colloidassisted 
transport of solutes are described in Sections 6.2.3, 6.2.4, and 6.2.5, respectively. The 
flux terms of the mass balance equation (Section 6.2.1) are described mathematically in Section 
6.2.6. Radioactive decay is discussed in Section 6.2.7, and Section 6.2.8 describes the equations of 
transport of the daughter products of radioactive decay. 
6.2.1 General Mass Balance Equations 
Following Pruess (1987, 1991), mass balance considerations in a control volume dictates that 
d 
dt ZVn 
M dV = Zn 
F  n d + ZVn 
q dV (Eq. 1) 
where
V; Vn = volume, volume of subdomain n [L3] 
M = mass accumulation term of component (tracer)  [ML3] 
; n = surface area, surface area of subdomain n [L2] 
F = Darcy flux vector of component  [ML2T1] 
n = inward unit normal vector [L0] 
q = source/sink term of tracer  [ML3T1] 
t = time [T]. 
The conservation of mass for any subdomain n is given by Equation 1, which in space-discretized 
form assumes the form of the following ordinary differential equation: 
dM 
dt n 
= 
1 
Vn Xm 
Anm(F)nm + (q)n (Eq. 2) 
where Anm is the surface segment between elements n and m [L2], (F)nm is the mass flux of 
tracer  between elements n and m [ML2T1], and (qi)n is the mass rate of the source/sink of 
tracer  in element n [ML3T1]. Equation 2 is general, and applies to solutes and colloids. 
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6.2.2 Accumulation Terms 
6.2.2.1 Equations of the Accumulation Terms 
The accumulation term M of a tracer  (solute or colloid) in a porous or fractured medium (PFM) 
is given by 
M = 8<: 
ML; +MAg; + cMAc; for solutes 
ML; +MF; for colloids 
(Eq. 3) 
where
ML; = the mass of tracer i in the the aqueous phase [ML3] 
MAg; = the mass of solute tracer i adsorbed onto the PFM grains [ML3] 
MAc; = the mass of solute tracer i adsorbed onto colloidal particles [ML3] 
MF; = the mass of filtered colloidal tracer i [ML3] 
and the parameter 
c = (1 for pseudocolloids 
0 otherwise. 
(Eq. 4) 
Pseudocolloids must be clearly differentiated from true colloids. The term true colloids refers 
to those generated from contaminants (Saltelli et al. 1984) when their concentrations exceed 
their solubility, and their study focuses on their transport. Colloids from other sources (e.g., clay 
particles naturally occurring in the subsurface) are termed pseudocolloids (Ibaraki and Sudicky 
1995, p: 2945), and their transport behavior must include both colloid transport and sorption of 
contaminants onto them. A detailed discussion on the subject can be found in Ibaraki and Sudicky 
(1995). 
Omitting for simplicity the  subscript, ML is obtained from 
ML =  (Sw  Sr) X +  Sr X ; (Eq. 5) 
where
X = the mass fraction of the tracer in the mobile fraction of 
the aqueous phase [M=M] 
X = the mass fraction of the tracer in the immobile fraction 
the aqueous phase [M=M] 
Sr = the immobile water saturation (can be set equal to 
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the irreducible) [L3=L3] 
 = the porosity (matrix or fracture) [L3=L3] 
 = the water density [ML3]. 
Equation 5 reflects the fact that solute concentrations are different in the mobile and immobile 
water fractions. Because water is very strongly bound (in electric double layers) to the PFM grain 
surface, Brownian motion is limited and solubility in the immobile water is lower than in the mobile 
water fraction. The importance of this boundary layer has been recognized by de Marsily (1986, 
p: 234), who differentiates X and X, and Moridis (1999), who used the mobile fraction of water in 
the analysis of diffusion experiments. Using the linear equilibrium relationship (Moridis 1999), 
X = Ki X; (Eq. 6) 
where Ki is a dimensionless mass transfer coefficient. For solutes 1  Ki > 0. Because of 
their double layers and their relatively large size (compared to solutes), colloids are expected to 
concentrate in the mobile water fraction and to be practically absent from the immobile water 
fraction. Then, a good approximation is Ki ' 0. 
Substitution into Equation 5 then leads to 
ML =  h X; where h = Sw  Sr + Ki Sr : (Eq. 7) 
6.2.2.2 Implications for Transport in the UZ 
For rocks with high irreducible water saturations at the UZ of Yucca Mountain, Ki < 1 can lead to 
smaller h values, indicating lower accumulation in the liquid phase. Under conditions of steadystate 
release, this can result in faster breakthroughs and, consequently, shorter travel times to the 
groundwater. 
6.2.3 Sorption Terms 
The discussion in this section is limited to sorption onto the matrix and fractures. Sorption onto 
pseudocolloids will be discussed in Section 6.2.4. 
6.2.3.1 Equilibrium Physical Sorption 
Omitting again for simplicity the  subscript, the mass of a solute sorbed onto the PFM grains and 
following a linear equilibrium isotherm is given by 
MAg = (1  ) s F ; (Eq. 8) 
where 
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s = the rock density [ML3]; 
F = Fp + Fc, the total sorbed mass of solute per unit mass 
of the PFM [M=M]; 
Fp = the physically sorbed mass of solute per unit mass of the PFM [M=M]; 
Fc = the chemically sorbed mass of solute per unit mass of the PFM [M=M]; 
Following the concepts of de Marsily (1986, p: 234) and considering that sorption onto the soil 
grains occurs as the dissolved species diffuses through the immobile water fraction (Moridis 1999), 
the equilibrium physical sorption is described by the equation 
Fp = 
8>
>>>><>
>>>>:
Kd Ki X for linear equilibrium (LE) sorption, 
KF (Ki X) for Freundlich equilibrium (FE) sorption, 
K1 Ki X 
1 + K2 KiX 
for Langmuir equilibrium (LAE) sorption 
(Eq. 9) 
where Kd [M1L3], KF [ML3], , K1 [M1L3], and K2 [M1L3] are sorption parameters 
specific to each solute and rock type. Of particular interest is the parameter Kd, called the 
distribution coefficient, which is the constant slope of the linear equilibrium adsorption isotherm of 
a solute in relation to the medium. The sorption of the various radionuclides in this AMR follows 
a linear equilibrium isotherm (See Section 5.2). 
6.2.3.2 Kinetic Physical Sorption 
If a kinetic isotherm is followed, then sorption is described by sorption is given by 
dFp 
dt 
= 
8>
>>>><>
>>>>:
k`(Kd Ki X  p Fp) for linear kinetic (LKP) sorption, 
kF [KF (Ki X)  Fp] for Freundlich kinetic (FKP) sorption, 
kL  K1 Ki X 
1 + K2 Ki X  Fp for Langmuir kinetic (LAKP) sorption, 
(Eq. 10) 
where 
p = (1 for linear kinetic physical (LKP) sorption; 
0 for linear irreversible physical (LIP) sorption, 
(Eq. 11) 
and k`, kF and kL arethekineticconstantsforlinear, FreundlichandLangmuirsorption, respectively 
[T1]. For p = 0, the linear kinetic expression in Equation 9 can also be used to describe the 
chemical process of salt precipitation. 
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6.2.3.3 Kinetic Chemical Sorption 
The first-order reversible chemical sorption is represented by the linear kinetic chemical (LKC) 
model 
dFc 
dt 
= k+
c Ki X  kc Fc ; (Eq. 12) 
where k+
c [M1L3T1] and kc [T1]aretheforwardand backwardkinetic constants, respectively. 
Note that Equation 11 can be used in conjunction with the physical sorption equations to describe 
combined sorption (Cameron and Klute 1977), e.g., physical and chemical sorption. Combined 
sorption accounts for the different rates at which a species is sorbed onto differentPM constituents. 
Thus, sorption onto organic components may be instantaneous (LE), while sorption onto mineral 
surfaces may be much slower and kinetically controlled (Cameron and Klute 1977). 
6.2.3.4 Implications for Transport in the UZ 
Sorption is the main mechanism of radionuclide mass removal from the transporting liquid phase. 
Nonsorbing radionuclides (such as 3H or 99Tc) will not be retarded. Strongly sorbing radionuclides 
(such as Np, Pu, U, Th, Am) will exhibit much longer arrival times to the groundwater. The transfer 
coefficientKi is obviously quite important, because aKi < 1 reduces the radionuclide sorbed onto 
the particle surfaces. Thus, the larger Ki is, the more the radionuclide is retarded. Although this 
may not be significant in the case of strong sorbers, it may be important in less-strongly sorbing 
tracers. 
Also of interest is sorption onto the fracture surfaces, as opposed to the volume-base sorption in 
the matrix. Currently, no information exists on the subject. The conventional approach in fractures 
with  = 1 results in zero sorption. It is possible to obtain an estimate of surface sorption by (a) 
assuming a reasonable grain size for a matrix, (b) computing the internal surface area (available 
for sorption) per unit volume of the matrix, and (c) computing the surface area of a corresponding 
fracture for the same grain size. This approach usually produces very small surface Kd values. 
6.2.4 Colloid Filtration Terms 
6.2.4.1 Equations of Colloid Filtration 
Colloidal particles moving through porous media are subject to filtration, the mechanisms of which 
have been the subject of several investigations (e.g., Herzig et al: 1970). The mass of filtered 
colloids is then given by 
MF; = c; ; (Eq. 13) 
where c; is the density of the colloidal particles of colloid  [ML3] and  is the filtered 
concentration of the colloid expressed as volume of colloids per volume of the porous medium. 
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When colloid deposition is a relatively fast process compared to the groundwater velocity, it is 
possible to describe colloid filtration as a linear equilibrium process (James and Chrysikopoulos 
1999). Omitting the  subscript, linear equilibrium filtration is then described by 
 = K Ki X ; (Eq. 14) 
where K is a distribution coefficient [M1L3]. 
The colloid filtration is more accurately described by a linear kinetic model (C orapcioglu et al: 
1987, pp: 269-342), which can take the following form: 
@ 
@t 
=  (K Ki X  p ) = +X    ; (Eq. 15) 
where  [T1] is a kinetic coefficient, and + and  [T1] are the kinetic forward and reverse 
colloid deposition rates (clogging and declogging coefficients), respectively, which are specific to 
each colloid and rock type. The term  is commonly assumed to be zero (Bowen and Epstein 
1979), but there is insufficient evidence to support this. As will be seen in Section 6.16 and 6.17 of 
the present AMR, colloid transport in the UZ is very sensitive to this parameter. The parameter p 
is analogous to that for sorption in Equations 10 and 11, and describes the reversibility of filtration. 
From de Marsily (1986, p: 273) and Ibaraki and Sudicky (1995, p: 2948), the following expression 
for the + coefficient can be derived: 
+ =  f uG; (Eq. 16) 
where  is the filter coefficient of the porous medium [L1], f is a velocity modification factor, u is 
the Darcy velocity [LT1], andGis a dynamic blocking function (DBF) that describes the variation 
of the PM porosity and specific surface with  (James and Chrysikopoulos 1999). The factor f 
(1  f  1:5) accounts for the velocity of the colloidal particle flow being larger than that of water 
(Ibaraki and Sudicky 1995, p: 2948). This results from the relatively large size of the colloids, 
which tends to concentrate them in the middle of the pores where the groundwater velocity is larger 
than the bulk average velocity. The factor f tends to increase with decreasing ionic strength, but 
cannot exceed 1:5 because colloids cannot move faster than the maximum groundwater velocity 
(Ibaraki and Sudicky 1995, p: 2948). 
For deep filtration (i.e., in the case of very dilute colloidal suspensions), there is no interaction 
among the colloidal particles and no effects on the medium porosity and permeability, i.e.,  is 
constant, andG = 1. Note that it is possible for both EOS9nT(the codeof the numerical model) and 
FRACL (the code of the semianalytical model) to have combined filtration, in which two different 
types of filtration (e.g., equilibrium and kinetic, or two kinetic filtrations with different + and ) 
occur simultaneously. 
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6.2.4.2 Implications for Transport in the UZ 
Filtration is one of the main mechanism of radioactive colloid removal from the transporting liquid 
phase, the others being chemical destabilization (e.g., because of pH changes) and flocculation. 
Three types of filtration mechanisms may affect the transport of colloids through PFM: surface 
filtration, straining filtration and physical-chemical filtration. Surface filtration occurs when 
particles are larger than the pores, in which case a filter cake is formed. 
Straining filtration is determined by the ratio Rd = dg=dp, where dg is the diameter of the grains 
of the porous medium and dp is the suspended particle diameter. Based on the experimental data of 
Sakthivadivel (1969), Rd  10 leads to cake filtration, 10 < Rd  20 corresponds to substantial 
straining filtration (permeability reductions by a factor of 7  15 and particles occupying 0:3), 
and Rd > 20 results in limited straining (only 2 5% of  occupied by particles and permeability 
reductions by 10-50%). Herzig et al: (1970, p: 15) indicated that little straining was expected when 
Rd > 12, and calculated that when Rd = 50, only 0:053% of  would be occupied by particles. 
A detailed discussion of the physical-chemical filtration of colloids can be found in C orapcioglu et 
al: (1987, pp: 269-342). The physical-chemical colloidal filtration by the porous/fractured medium 
incorporates three mechanisms: (a) contact with the pore walls, (b) colloid fixation onto the walls, 
and (c) release of previously fixed colloids (Herzig et al: 1970; C orapcioglu et al: 1987). 
Contact with the pore walls and colloidal capture can be the result of sedimentation (caused by 
a density differential between the colloidal and the carrier liquid), inertia (deviation of colloidal 
trajectories from the liquid streamlines because of their weight), hydrodynamic effects (caused by 
a variation in the velocity field of the liquid), direct interception (caused by collisions with the pore 
walls at convergent areas) and diffusion (Brownian motion causing colloids to move toward pore 
walls or dead-end pores). 
Fixation on the pore walls occurs at retention sites that include edges between two convex surfaces, 
pore throats smaller than the colloidal size, and dead-end pores or regions of near-zero liquid 
velocity. Fixation is caused by retentive forces, which include axial pressure of the fluid at 
constriction sites, friction forces, Vander Waalsforces, electrical forcesand chemicalforces (Herzig 
et al: 1970, pp: 4, 11-17). Finally, remobilization of colloidal particles may be caused by a number 
of factors, including collision between a loosely held colloid with a moving particle, an increase in 
pressure as colloids constrict flow, and a change in external conditions. 
All three mechanisms are expected to be present in the UZ of Yucca Mountain. The EOS9nT 
simulations can account for surface filtration by using a particle size versus pore size criterion, 
and by not allowing colloidal entry into media that do not meet this criterion. Straining filtration 
(pore-size exclusion) is described by using appropriate colloid accessibility factors (see Section 
6.3.5), and physical-chemical filtration is represented by using appropriate parameters in Equations 
14 or 15. 
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Note that it is not possible to account for cake filtration or for the effects of filtration on permeability 
and porosity, as this would violate the linearity in the models. However, these scenarios would be 
unlikelyintheUZ ofYM because(a) natural pseudocolloids (suchas clays)under natural conditions 
occur in small concentrations, and (b) it is expected that, owing to adverse chemical conditions 
(e.g., pH, ionic strength) in the immediate vicinity of the potential repository, true colloids will be 
released at low concentrations for a long time. 
6.2.5 Colloid-Assisted Transport Terms 
6.2.5.1 Equations of ColloidAssisted Transport 
The mass of a tracer  sorbed onto pseudocolloids is described by 
MAc; = 
Nc Xj=1
(j j + Xj)F;j (Eq. 17) 
where F;j denotes the sorbed mass of solute  per unit mass of the pseudocolloid j [M=M] 
and Nc is the total number of pseudocolloid species. The first term in the sum inside the 
parenthesis of Equation 17 describes the filtered (deposited) colloid concentration, and the second 
the concentration of the suspended colloids in the liquid phase. F;j is computed from any 
combination of Equations 912, with the appropriate sorption parameters corresponding to each 
colloid. Note that Equation 17 applies to pseudocolloids only, as opposed to true colloids, onto 
which radionuclides are not considered to sorb. 
6.2.5.2 Implications for Transport in the UZ 
The formulation of Equation 17 allows consideration of the whole spectrum of sizes of a particular 
colloid, as each sizewould havedifferent transport behavior (see Equation16) and differentsorption 
properties (resulting from different surface area). 
Of particular interest inUZ radioactive transport models is the potential of colloid-assisted transport 
to significantly enhance the migration of tracers whose normally strong sorbing behavior would 
confine them to the vicinity of the point of release. Sorption of such a radionuclide (e.g., Pu) onto 
pseudocolloids renders the whole colloid radioactive. The transport of such a colloid is no longer 
dictated by the strong Pu sorption behavior, but by the kinetics of colloid filtration. Coupled with 
the fact that colloids can move at velocities up to 50% higher than the groundwater Darcy velocity 
(see Equation 16), this can result in travel times to the groundwater orders of magnitude shorter 
than the ones predicted by sorption. 
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6.2.6 Flux Terms 
6.2.6.1 Equations of the Flux Terms 
The flux term has contributions from advective, diffusive, and dispersive transport processes and is 
given by 
F = Fw X   D rX  Fs; ; (Eq. 18) 
where Fs; is the flux due to surface diffusion and D is the dispersion tensor of tracer , a second 
order symmetric tensor with a principal axis aligned with the Darcy flow vector. Omitting the  
subscript, D is described by the equations 
D = DT I + DL  DT 
u2 u u ; (Eq. 19) 
DL =  (Sw  Sr)  D0 +  Sr  D0 + L u ; (Eq. 20) 
DT =  (Sw  Sr)  D0 +  Sr  D0 + T u ; (Eq. 21) 
where
I = the unit vector 
 = the tortuosity coefficient of the pore paths [L=L] 
D0 = the molecular diffusion coefficient of tracer i in water [L2T1] 
L; T = longitudinal and transverse dispersivities, respectively [L] 
u = the Darcy velocity vector [LT1] 
Equation 18 accounts for surface diffusion, which can be responsible for significant transport in 
strongly sorbing media (Moridis 1999; Cook 1989). The surface diffusion flux is given by Jahnke 
and Radke (1987) as 
Fs = (1  ) s s DsrFp; (Eq. 22) 
where s is the tortuosity coefficient of the surface path [L0], Ds is the surface diffusion coefficient 
[L2T1], and Fp isthephysicaldiffusioncomputedfrom equations(19)or (10). There istheoretical 
justification for the relationship s = 2
3  (Cook 1989, p: 10). 
6.2.6.2 Application to Colloid Fluxes 
Equations 17 through 20 apply to solutes, but need the following modifications to render them 
suitable to colloidal transport. More specifically: 
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1. Fs = 0 because surface diffusion does not occur in colloids. 
2. The flux Fs and the Darcy velocities u are multiplied by the factor f (see Section 6.2.4.1). 
3. Thedispersivities L andT aregenerallydifferentfromthose forsolutes(IbarakiandSudicky 
1995) and may be a function of the colloidal particle size. 
4. The term D0 is the colloidal diffusion coefficient in water [L2T1] and is described by the 
Stokes-Einstein equation, according to (Bird et al: 1960, p: 514), as 
D0 = k T 
3  w dp 
; (Eq. 23) 
where k is the Boltzmann constant (1:38 1023 J K1 in SI units), T is the absolute water 
temperature [K], w is the dynamic viscosity of water [ML1T1], and dp is the colloid 
diameter [L]. 
5. The fluxes in Equation 18 are multiplied by the colloid accessibility factors fc (0  
fc  1) at the interface of different media. The fc factor describes the portion of the 
colloidal concentration in a medium that is allowed to enter an adjacent medium of different 
characteristics, and quantifies pore size exclusion (straining). 
In the treatment of the general 3-D dispersion tensor, velocities are averaged by using the projected 
area weighting method (Wu et al: 1996, p: 23), in which a velocity component uj (j  x; y; z) of 
the vector u is determined by vectorial summation of the components of all local connection vectors 
in the same direction, weighted by the projected area in that direction. This approach allows the 
solution of the transport problem in irregularly shaped grids, in which the velocities normal to the 
interface areas are not aligned with the principal axes. 
6.2.6.3 Implications for Transport in the UZ 
Because it is directly proportional to the water fluxes, advection in the fractures is by far the 
dominant mechanism of transport in the UZ of Yucca Mountain. This is further enhanced by 
longitudinal dispersion, molecular diffusion, and (possibly) surface diffusion (in decreasing order). 
Coupled with the fracture orientation and gravitational differentials, the result of the fracture and 
flow characteristics is a mainly downward migration of the radionuclides. Note that advection also 
occurs in the matrix (and is accounted for in the simulations), albeit at significantly lower rates. 
Lateral spreading of the contaminants can be achieved through transverse dispersion, molecular 
diffusion, and (possibly) surface diffusion. As sorption occurs from the liquid phase onto the 
solids, and fractures are by far the main conduits of water, retardation of sorbing radionuclides 
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will be controlled by the rate of tracer movement from the fractures to the sorbing matrix. This is 
represented by the sum of diffusive, dispersive and surface diffusion fluxes, and results in the lateral 
migration of the contaminants. 
Currently, there are no field study estimates of L and T in the UZ. When not ignored in the 
numerical simulations (justified by the relative magnitude of advection), reasonable L estimates 
are used, and T is usually set to zero (especially in the fractures). Accurate values of D0, 
coupled with estimated tortuosity coefficient values from laboratory experiments, provide a rather 
representative estimate of diffusive fluxes in the UZ simulations. 
No information exists on whether the UZ media support surface diffusion (a possibility in zeolites). 
Surface diffusion can be important in tracers that exhibit strong sorption (e.g., Pu). A larger Kd 
clearly indicates stronger sorption, but this does not mean immobilization of the dissolved species 
when the porous/fractured medium supports surface diffusion. On the contrary, the stronger the 
sorption (i.e., the larger the Kd), the larger the diffusion rate, and practically all of it attributable to 
the surface process (Moridis 1999, pp: 13751376). 
6.2.7 Radioactive Decay 
6.2.7.1 Equations of Radioactive Decay 
When a tracer  undergoes radioactive decay, the rate of mass change is described by the first-order 
decay law 
dM 
dt 
= M ; where  = 
ln2 
(T1=2) 
; (Eq. 24) 
and (T1=2) is the half life of tracer . Substitution of Equations 18 and 24 into Equation 2 yields 
dM 
dt n 
+  (M)n = 
1 
Vn Xm 
Anm [Fnm X   D rX  Fs;] + (q)n (Eq. 25) 
6.2.7.2 Implications for Transport in the UZ 
The decay of radioactive substance is completely predictable and well documented. Thus, thedecay 
of radioactive substances in UZ simulations can be computed very reliably. 
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6.2.8 Daughter Products of Radioactive Decay 
6.2.8.1 Transport Equations of Daughters 
If a radioactive tracer  is a daughter product of the decay of tracer j, then the mass accumulation 
terms are adjusted (de Marsily 1986, pp: 265266) to yield the equation of transport of the daughter 
products as
dM 
dt n 
+  (M)n  j mr (Mj)n 
= 
1 
Vn Xm 
Anm [Fnm X   Di rX  Fs;] + (q)n ; 
(Eq. 26) 
wheremr = W=Wj , andW andWj arethe molecular weights of the daughterand parent species. 
Equation 26 applies to radioactive solutes or radioactive true colloids. 
For daughters following an isotherm other than LE, Equations 9 and 10 need to account for the 
generation of daughter mass from the decay of the sorbed parent, and become 
@F 
@t 
+  F  1mr  F1 = kA X  kB (F +mr F1) ; (Eq. 27) 
where F1 is the sorbed mass of the parent, 
kA = 8<: 
k` Kd Ki for LKP/LIP sorption, 
k+
c Ki for LKC sorption, 
kB = 8<: 
kp p for LKP/LIP sorption, 
kc for LKC sorption, 
and  is the fraction of the mass of the decayed sorbed parent that remains sorbed as a daughter 
(0    1). The term  is introduced to account for the different sorption behavior of parents 
and daughters, and the fact that daughters can be ejected from grain surfaces due to recoil (e.g., the 
ejection of 234Th from grain surfaces during the alpha decay of 238U) (Faure 1977, pp.288-289). 
6.2.8.2 Implications for Transport in the UZ 
If decay results in radioactive daughters, UZ simulations must compute the total radioactivity 
distribution, i.e., the sum of the concentrations of all the members of the radioactive chain. This 
is especially true if the daughters have long half lives. Intermediate chain products with short half 
lives relative to the simulation periods can be ignored with impunity. 
Although the EOS9nT and the FRACL codes can theoretically obtain the transport scenario of any 
number of daughters in the radioactive chain, this is especially true for daughters with short half 
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lives. With longer half-lives (such as for 237Np, 239Pu, etc.), machine accuracy considerations and 
roundoff errors (with the daughter concentrations becoming increasingly smaller as we move down 
the radioactive chain) limit their number to a maximum of four or five with comparable half lives. 
The  factor is a function of the type of decay, as well as of the chemical form of the sorbed cation. 
In alpha decay (e.g., 237Np, 239Pu),  = 0. There is no information on the behavior of  for other 
types of decay. The  factor can have significant implications for the transport behavior of daughters 
if (a) the large sorbed masses of strongly sorbing parents are ejected back into the aqueous phase 
after decay, (b) the daughter is a much weaker sorber, and (c) its sorption is kinetically controlled. 
Such a possibility could arise in the kinetic sorption of radionuclides onto pseudocolloids (CRWMS 
M&O 1999e, Section 6). For equilibrium isotherms, this is not an issue. 
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6.3 THE NUMERICAL AND SEMIANALYTICALMODELS 
In mathematical simulations, the conventional meaning of the term model is the mathematical 
description of the physics governing the behavior of the simulated system, while the term code is 
the implementation of the mathematical model ina computer language. Because model and code are 
inexorably intertwined, these terms have been historically used interchangeably. In the context of 
EOS9nT and FRACL applications in the present AMR, when the word model is used, it is preceded 
by the qualifying words numerical or semianalytical. 
6.3.1 The EOS9nT Code 
The code used for the 3-D site-scale transport simulations in the AMR is TOUGH2 V1.11 Module 
EOS9nT V1.0 (STN: 10065-1.11MEOS9NTV1.0-00, Moridis et al: 1999), which is a member of 
the TOUGH2 family of codes (Pruess 1991). It can simulate flow and transport of an arbitrary 
number n of non volatile tracers (solutes and/or colloids) in the subsurface. 
EOS9nT first solves the Richards equation, which describes saturated or unsaturated water flow in 
subsurface formations, and obtains the flow regime. The set of n linearly independent transport 
equations (corresponding to the n solutes/colloids) are then solved sequentially. The n tracer 
transport equations account for (a) advection, (b) molecular diffusion, (c) hydrodynamic dispersion 
(with full 3-D tensorial representation), (d) kinetic or equilibrium physical and chemical sorption 
(linear, Langmuir, Freundlich, or combined), (e) first-order linear chemical reaction, (e) radioactive 
decay, (f) colloid filtration (equilibrium, kinetic or combined), and (g) colloid assisted solute 
transport. A total of n-1 daughter products of radioactive decay (or of a linear, first-order reaction 
chain) can be tracked. 
EOS9nT includes two types of Laplace transform formulations of the tracer equations, in addition 
to conventional timesteping. The Laplace transform is applicable to steady-state flow fields and 
allows a practically unlimited time step size and more accurate solution (as numerical diffusion is 
significantly reduced). Additional information on the EOS9nT numerical model can be found in 
Attachment I. 
6.3.2 The FRACL Code 
FRACL V1.0 (STN: 10191-1.0-00) is the FORTRAN implementation of semianalytical solutions 
developed to solve for the problem of transport of stable, radioactive or reactive tracers (solutes 
or true colloids) through a 2-D layered system of heterogeneous fractured media. (Moridis and 
Bodvarsson 1999). The transport equations in the matrix account for matrix and surface diffusion, 
masstransfer betweenthemobile andimmobilewater fractions, and physical, chemicalorcombined 
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sorption following a linear equilibrium, kinetic, or irreversible isotherm. In the case of true colloids, 
linear kinetic, equilibrium or combined filtration can be accounted for. Radioactive decay, firstorder 
chemical reactions, and tracking of up to five products of radioactive decay or chemical 
reactions are also included in the solution. The transport equations in the fractures account for the 
same processes in addition to advection and hydrodynamic dispersion. The solutions are analytical 
in the Laplace space and are numerically inverted to provide the solution in time. 
FRACL also accounts for the effects of different fracture spacing and misalignment of fractures. It 
can accommodate layers of fractured rocks, or a combination of fractured rock and non fractured 
strata (see Figure 6.3.1). It can describe fractured systems of finite fracture spacing, or single 
fractures in a semi-infinite medium. A complete description of the semianalytical solutions on 
which FRACL is based can be found in Moridis and Bodvarsson (1999). Additional information 
on the FRACL semianalytical model can be found in Attachment I. 
6.3.3 Other Computational Tools 
In addition to EOS9nT and FRACL, the following computational tools were used: 
1. The TOUGH2 V1.4 Module EOS9 V1.4 (STN: 10007-1.4-00) code, to obtain the flow 
velocities for the various perched water and climatic scenarios discussed in CRWMS M&O 
(1999d, Section 6.2). 
2. The T2R3D V1.4 (STN: 10006-1.4-00) code, to conduct the Busted Butte solute transport 
simulations. 
3. The xtract1.f V1.0 routine (ACC: MOL.19991221.0431), to modify the grid system for use in 
theEOS9nTruns. The modifications involved(a) determining the grid elementscorresponding 
to the potential repository, (b) moving them to the end of the element file, where (c) the 
upper and lower boundary elements are also moved. This was necessitated by the fact that 
contaminant release is considered constant and continuous in this AMR. Thus the repository 
elements represent internal boundary points. After moving these elements to the bottom of the 
element file, the volume of the first element is set to zero or a negative number. Then, these 
elements are considered in the determination of fluxes but are not included in mass balance 
computations. 
4. The xtract2.f V1.0 routine (ACC: MOL.19991221.0432), to obtain initial condition files 
(INCON) using the SAVEfiles from the EOS9 runs for the EOS9nT simultaneous simulations 
of 99Tc, 237Np and 239Pu transport. 
5. The xtract2a.f V1.0 routine (ACC: MOL.19991220.0397), to obtain INCON files (using the 
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SAVEfiles from the EOS9 runs) for the EOS9nT simultaneous simulations of transport of the 
237Np and the 239Pu decay-chains. 
6. The xtract2b.f V1.0 routine (ACC: MOL.19991220.0398), to obtain INCON files (using the 
SAVE files from the EOS9 runs) for the EOS9nT simultaneous simulations of transport of 
99Tc, and the 237Np and 239Pu decay-chains. 
7. The xtract5.f V1.0 routine (ACC: MOL.19991220.03900), to obtain INCON files (using the 
SAVEfiles from the EOS9 run) for the EOS9nT simulations of Cl transport in the ESF. 
8. The xtract6.f V1.0 routine (ACC: MOL.19991220.0400), to extract the Cl concentrations 
corresponding to the ESF elements from the output of the EOS9nT simulation of Cl transport. 
Figure 6.3.1. An example of a layered fractured system in FRACL studies. Each layer has its own distinctive 
geometry and fracture and matrix properties. Note that the last subdomain (layer 5) is semi-infinite. 
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6.4 MODEL VALIDATIONAND CALIBRATION 
In this section we validate and calibrate the RTM using the FRACL and EOS9nT codes. We 
first validate the RTM using both codes in a comparison to the analytical solution of Sudicky and 
Frind (1982). We then calibrate the RTM by employing FRACL and analyzing field data of Cl 
distribution in the UE-25 UZ#16 borehole, and compare the FRACL results to the predictions from 
a 3-D simulation using the T2R3D code. Finally, we calibrate the RTM by using EOS9nT and 
analyzing field data of Cl distribution in the ESF, and compare the results of the 3-D site-scale 
simulation to the T2R3D predictions for the same grid and conditions. 
6.4.1 Validation and Calibration Criteria 
For accurate predictions of the EOS9nT and FRACL codes, three conditions must be met: 
1. The relevant physical processes must be accounted for and accurately represented by the 
mathematics. 
2. The mathematical equations must be accurately solved by the numerical or semianalytical 
methods. 
3. The physical properties of the rocks must be correct. 
For validation of the the RTM using the EOS9nT and FRACL codes, their simulation results are 
compared to the analytical solution of Sudicky and Frind (1982). The criterion for validation 
was that the analytical solution and the FRACL and EOS9nT solutions agree within 1%. Results 
presented in the section show that this criterion was easily met by both codes. 
Calibration and additional validation of the RTM using the FRACL and EOS9nT codes was 
accomplished by comparing their predictions to (a) field measurements and (b) numerical results 
from previously validated T2R3D V1.4 (STN: 10006-1.4-00, See Sections 3 and 6.3) simulations 
with the same input data. Agreement within 1% of the T2R3D predictions was the easily-met 
criterion for validation and matching the calibrated prediction. 
6.4.2 Validation 
The 2-D analytical solution of Sudicky and Frind (1982) was used to validate the RTM using the 
EOS9nT and the FRACL codes. This problem involves a single fracture and a matrix block of finite 
thickness (see Figure 6.4.1) and assumes diffusion but no advection through the matrix. Additional 
verification studies can be found in Moridis et al: (1999) and Moridis and Bodvarsson (1999). 
The parameters (and the corresponding data sources) used in the simulations are shown in Table 
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Figure 6.4.1. The fracture-matrix system in the validation study of FRACL and EOS9nT. 
6.2. For the EOS9nT simulations, three different 2-D grids in (x, z) were used for the EOS9nT 
simulations, with increasingly finer discretization in the matrix block. The first gridblock in the 
x direction at any z level corresponds to the fracture; all other gridblocks at the same z level 
correspond to the matrix. 
The discretization of the coarse grid was 2320 in (x, z). In the medium grid, the fracture occupied 
a single gridblock, and the matrix block was discretized into four gridblocks at any z level. In the 
fine grid, the fracture discretization was the same, but the matrix block was subdivided into 11 
gridblocks. Thus, the discretization of the medium and of the fine grids were 5320 and 12320 
in (x, z), respectively. 
Three EOS9nTsimulations were conducted for each discretization, using (a) conventional timestepping, 
(b) the Stehfest (1970a,b) implementation of the Laplace space formulation, and (c) the De 
Hoog et al: (1982) implementation of the Laplace space formulation, for a total of nine EOS9nT 
runs. The DTN for the EOS9nT input and output data files is LB991220140160.001. 
Two FRACL simulations were conducted. The first considered a single domain semi-infinite in z; 
the second subdivided the domain into three segments in z, two of which were finite and the last 
semi-infinite. The DTN for the FRACL input and output data files is LB991220140160.002. 
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Table 6.2. Input parameters for model validation against an analytical solution. 
Parameters Values (*) 
D0 1.6109 m2/s 
Fracture  1.0 
Fracture  1 
Fracture aperture 100 m 
Longitudinal dispersivity L in the fracture 0.1 m 
Fracture Kd 0 m3/kg 
Fracture flow velocity V 0.1 m/day 
Matrix block length 0.5 m 
Matrix  0.01 
Matrix  0.1 
Matrix flow velocity 0 m/s 
Matrix Kd 0 m3/kg 
Radionuclide T1=2 12.35 years (tritium) 
(*): From Sudicky and Frind (1982) 
Figure 6.4.2 shows the distribution relative concentration CR (defined as CR = C=C0, where C = 
X is the solute concentration [ML3] and the subscript 0 denotes the concentration at the release 
point) in the fractures at t = 1,000 days. The analytical and the two FRACL solutions were obtained 
at the same points along the z axis and were identical in the first 5 significant digits. To improve 
clarity, the FRACL solutions are not shown in Figure 6.4.2 because it is not possible to distinguish 
them from the analytical. 
Forthesamediscretization, theEOS9nTsolutionsforthethreedifferenttime treatmentsarevirtually 
indistinguishable. The coarser EOS9nT grid results in a solution that deviates significantly from the 
analytical solution and tends to indicate an early breakthrough. This deviation diminishes as time 
increases (Moridis et al: 1999). The solutions from the medium and the fine grids are very accurate, 
very close to each other, and exhibit very small deviations from the analytical and the FRACL 
solutions. These deviations are confined to the steepest portion of the curve. This indicates that 
there is practically no incremental benefit from refining the grid beyond the medium discretization. 
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6.4.3 CalibrationCl Concentration in UE-25 UZ#16 
The RTM was calibrated by using the FRACL code to analyze field measurements of aqueous 
chloride concentration from the UE-25 UZ#16 Borehole. The strata crossed by UE-25 UZ#16 are 
shown in Figure 6.4.3, which shows the simulation domain and provides the vertical thickness of 
the layers in the various hydrogeologic units. A total of 25 layers were involved in the simulations. 
The 2-D geological profiles were constructed by combining (a) fractures of known aperture and 
frequency (per unit of length) in each of the layers with (b) the corresponding matrix blocks (the 
sizes of which were obtained from data on the active fracture spacing). The input parameters (and 
the corresponding data sources) are shown in Table 6.3. The DTN for the FRACL input and output 
data files is LB991220140160.003. 
Figure 6.4.4 shows (a) measurements, (b) the FRACL predictions, and (c) the T2R3D predictions 
of the Cl concentration in the fractures as a function of depth at various times. The curves for t < 
10000 years show the evolution of the Cl concentration profile with depth over time. Of interest is 
the steady-state, which has already been reached at t = 10,000 years. Comparison of the FRACL 
predictions to the field measurements indicate a reasonable agreement. 
Note that the FRACL solution is practically identical to the predictions of the T2R3D code 
obtained by employing a 3-D site-scale transport model and a calibrated infiltration (CRWMS 
M&O 1999d, Section 6.4). The two models share the same transport and infiltration data. This 
positive comparison supports the validation and calibration of the RTM. 
Table 6.3. FRACL input data and sources for modeling the Cl distribution in the UE-25 UZ#16 borehole 
Parameters Source 
Geologic profile and rock properties at the 
UE-25 UZ#16 cross-section 
DTN: LB990701233129.002 and 
SN: YMP-LBNL-GSB-QH-1, page 31 
Calibrated infiltration rate DTN: LB991131233129.003 
Field measurements of the Cl concentration 
profile in the UE-25 UZ#16 borehole 
DTN: GS950608312272.001 
Longitudinal dispersivity in the fracture L 
= 0.1 m 
Scientificjudgementintheabsenceof 
data 
D0 of Cl: 2.03109 m2/s DTN: LB991220140160.019 (Cussler 
1984, p. 147) 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
Relative concentration in the fracture 
30 25 20 15 10 5 0 
Distance along fracture (m) 
Analytical solution 
EOS9nT, 12x320 
EOS9nT, 5x320 
EOS9nT, 2x320 
T = 1000 days 
Figure 6.4.2. Analytical and numerical solutions of the concentration distribution in a fracture for three different 
gridsat t=1000days. Theerrorcausedbythecoarsediscretizationaccuracyis significant. The solutions 
for a medium and coarse grid are indistinguishable. The two FRACL solutions are identical 
totheanalytical andare notdifferentiated (DTN: LB991220140160.001and LB991220140160.002, 
data submitted with this AMR). 
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Figure 6.4.3. Vertical profile of hydrogeologic units at the UE-25 UZ#16 borehole (CRWMS M&O 1999h, Table 
III-1). 
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Figure 6.4.4. FRACL predictions of the Cl concentration in the fractures of the UE-25 UZ#16 profile (DTN: 
LB991220140160.003, data submitted with this AMR). Measurements are also shown (DTN: 
GS950608312272.001). The T2R3D predictions from a 3-D site-scale model are shown for 
comparison (DTN: LB991131233129.003). 
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6.4.4 Calibration - Cl Concentration in the ESF 
The RTMwas calibrated through comparison of the EOS9nT predictions to (a) field measurements 
of chloride concentration in the ESF and (b) numerical predictions obtained by using the T2R3D 
code (CRWMSM&O 1999d, Sections 3, 6.4 and 6.7). For this EOS9nT simulation, the site-scale 
3-D grid, the initial and boundary conditions, and the water flow velocities were obtained from the 
EOS9 simulation using the calibrated infiltration data (CRWMSM&O 1999d, Section 6.4.4). The 
Cl sources (and their areally nonuniform distribution) in the EOS9nT model reflected the calibrated 
Cl source conditions used in the T2R3D simulation (CRWMS M&O 1999d, Section 6.4.4 and 
Figure 6.4.8). The parameters (and the corresponding data sources) used in this simulation are 
listed in Table 6.4. The DTN for the EOS9nT input and output data files is LB991220140160.004. 
Figure 6.4.5 shows (a) the measured and (b) the predicted Cl concentration distribution along the 
ESF from both the EOS9nT and the T2R3D runs. The EOS9nT results were obtained using the De 
Hoogetal : (1982)implementationof theLaplacespaceformulationatt=10,000,000 years, atwhich 
time Cl concentrations are expected to have reached steady state. This 3-D site-scale simulation 
takes only about 12 minutes to complete because the Laplace-space formulation eliminates the need 
for solutions at any intermediate times. 
Comparison between the EOS9nT predictions and the field measurements in Figure 6.4.5 shows 
a satisfactory agreement and helps support the validation of EOS9nT. In the same figure, note 
the practical identity of the EOS9nT and the T2R3D predictions. This further supports the RTM 
calibration. 
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Table 6.4. EOS9nT input data and sources for modeling the Cl distribution in the ESF 
Parameters Source 
Grid and 3-D flow field DTN: LB990701233129.002 
Calibrated infiltration rate DTN: LB991131233129.003 
Measurements of the Cl concentration 
distribution in the ESF 
DTN: LAJF831222AQ98.002 
DTN: LAJF831222AQ98.010 
DTN: LAJF831222AQ98.015 
150 
100 
50
0 
8000 6000 4000 2000 0 
ESF station (m) 
EOS9nT 3-D simulation (calibrated infiltration) 
T2R3D 3-D simulation (calibrated infiltration) 
Field measurements 
Figure 6.4.5. Comparison of (a) EOS9nT predictions (DTN: LB991220140160.003, data submitted with this 
AMR), (b) T2R3D predictions and (c) measurements of Cl concentration distribution along the ESF. 
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6.5 2-D TRANSPORT SIMULATIONS IN INDIVIDUAL 
HYDROGEOLOGIC UNITS 
6.5.1 General Issues 
In Sections 6.6 to 6.8 we study radionuclide transport in 2-D systems that are representative of the 
individual hydrogeologic units present at the site of the potential repository. The focus of these 
studies is to determine the important processes and the effect of differences in geology on the 
transport of radionuclides with different transport and decay properties. 
In all the 2-D studies in Sections 6.6 to 6.8, water infiltrates at a rate of 6 mm/year. This is close to 
the mean present-day infiltration rate (see Table 6.11). 
6.5.2 Radionuclides Considered 
Three radionuclides are considered: 99Tc (nonsorbing), 237Np (moderately sorbing) and 239Pu 
(strongly sorbing). Their properties are listed in Table 6.5. When occurring, sorption follows a 
linear equilibrium isotherm. The distribution coefficientKd values used in the FRACL simulations 
in Sections 6.6 through 6.9 are listed in Table 6.6. 
The scenario being investigated here is the fate and transport of radionuclides that manage to enter 
the layers of the TSw, CHn, and PP hydrogeologic units. In the TSw hydrogeologic unit, the 
radionuclides are released at an elevation corresponding to the bottom of the potential repository; in 
the the CHn and PP hydrogeologic units, the radionuclides are released at the top of the units. The 
contaminant distribution is then monitored over time. For purposes of discussion and comparison 
among cases, breakthrough is defined as the point at which the relative concentration CR (see 
Section 6.4.2) exceeds 1012 at the bottom of the domain under investigation. 
6.5.3 Hydrogeologic Profiles 
Transport was studied in three hydrogeologic profiles called Cross Sections 1, 2 and 3. These 
profiles are two-dimensional in the sense that concentrations are computed in both the vertical (z) 
and horizontal (x) directionsinthe fracturesand thematrix blocks of eachlayer inthehydrogeologic 
units in the cross sections (see Figure 6.4.1). It must be pointed out that the use of the term Cross 
Section does not imply a (x; z) profile that spans a considerable distance in the x direction, but 
a 2-D simulation domain of limited width in the x direction. This limited width is the minimum 
necessary to describe the simulation stencil of the matrix-fracture system, i.e., the basic repeatable 
element of a representative hydrogeologic profile at the given location. 
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Table 6.5. Properties of the main radionuclides in the transport simulations 
Radionuclide D0 (m2/s) T1=2 (years)y  = ln2 
T1=2 
(s) Decay modey 
99Tc 4.551010 2.13105 1.0311013  
237Np 7.121010 2.14106 1.0261014  
239Pu 6.081010 2.41104 9.1141013  
: From DTN: LB991220140160.019 and DTN: LAIT831341AQ96.001 
y: From Lide (1992, pp: 11-53, 11-125, 11-126) 
Table 6.6. Distribution Coefficients Kd (in m3/kg) in the 2-D FRACL simulations 
Model Layer 99Tc 237Np 239Pu 
tsw35, tsw36, tsw37, tsw38, tsw39 0.000 0.001 0.100 
ch1v, ch2v, ch3v, ch4v, ch5v 0.000 0.001 0.100 
ch1z, ch2z, ch3z, ch4z, ch5z, ch6z 0.000 0.004 0.100 
pp4, pp1 0.000 0.004 0.100 
pp3, pp2 0.000 0.001 0.100 
bf3 0.000 0.001 0.100 
bf2 0.000 0.004 0.100 
DTN: LB991220140160.019 and DTN: LAIT831341AQ96.001 
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The three cross sections are located in the vicinity of the USW SD-6, SD-12, and UZ-14 boreholes, 
respectively. The locations of the three boreholes in the context of the UZ site- scale model are 
showninFigure 6.5.1. Thus, CrossSection3islocatedinthenorthernpartofthepotentialrepository 
site, while Cross Sections 1 and 2 are located in the southern part. The geologic profiles in Cross 
Sections 1, 2 and 3, including the layers of all the hydrogeologic units involved in radionuclide 
transport, and their elevations and thicknesses, are shown in Figures 6.5.2 through 6.5.4. 
The domains for the 2-D semianalytic FRACL simulations were constructed by combining (a) 
fractures of known aperture and frequency (per unit of length) in each of the layers in the 
hydrogeologic units with (b) the corresponding matrix blocks (the sizes of which were determined 
from the active fracture spacing) at each location. 
6.5.4 The 2-D FRACL Transport Simulations 
All the 2-D simulations were conducted using the FRACLcode. The DTN for the FRACLinput and 
output data files is LB991220140160.005. Because they are based on a semianalytical solution of 
thetransportproblem,FRACLsimulationsareveryfast, needinglessthanaminuteofcomputational 
time on any of the computing platforms used in the simulations. 
Note thatmisalignment of fracturesis notaccountedfor inthesimulationsdiscussedinSections6.5 
6.8. Thus, the results represent the worst case scenario, yield the shortest possible breakthrough 
times, and provide the upper limit of radionuclide transport. By assuming fracture alignment, 
transport between the offset fractures at the interface of adjacent layers (and the corresponding 
delay in the breakthrough curves) is not considered. 
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Figure 6.5.1. 2-D (plan view) of the Yucca Mountain site identifying the locations of boreholes USW SD-6, SD-12 
and UZ-14 (CRWMS M&O 1999h, Section 6, Figure 1). 
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Figure 6.5.2. Hydrogeologic units (and their layers) of the UZ model domain from the potential repository to the 
groundwater in Cross Section 1 near the USW SD-6 borehole (CRWMS M&O 1999h, Table III-1). 
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Figure 6.5.3. Hydrogeologic units (and their layers) of the UZ model domain from the potential repository to the 
groundwater table in Cross Section 2 near theUSW SD-12 borehole (DTN:LB990501233129.004). 
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Figure 6.5.4. Hydrogeologic units (and their layers) of the UZ model domain from the potential repository to the 
groundwater in Cross Section 1 near the USW UZ-14 borehole (CRWMS M&O 1999h, Table III-1). 
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6.6 2-D TRANSPORT IN THE TSw LAYERS 
This section focuses on radionuclide transport in 2-D vertical cross sections of the TSw hydrogeologic 
unit under the conditions discussed in Section 6.5, and is subdivided in five subsections. 
Section 6.6.1 discusses the transport of 99Tc, 237Np and 239Pu through the TSw at Cross Section 1. 
The results of the study appear in Figures II.1 to II.4 (Attachment II). The subject of Section 6.6.2 
is the transport of the same radionuclides through the TSw at Cross Sections 2 and 3 (Figures II.5 
to II.10). 
Sections 6.6.3 to 6.6.5 involve sensitivity analysis studies, in which we evaluate the importance of 
various parameters on the transport of the three radionuclides. The effect of the transfer coefficient 
Ki is discussed in Section 6.6.3 (Figures II.11 to II.15). Section 6.6.4 addresses the effect of matrix 
tortuosity coefficient  (Figures II.16 to II.21). The sensitivity of transport to the longitudinal 
dispersivity L in the fractures is discussed in Section 6.6.5 (Figures II.22 to II.25). 
6.6.1 2-D Transport in TSw, Cross Section 1 
6.6.1.1 Results and Discussion 
The parameters and the data sources for this simulation are listed in Table 6.7. The distribution 
of relative concentration (with respect to the concentration at the release point) of the three 
radionuclides in the fractures along the z-axis are shown in Figures II.1-II.3 in Attachment II. 
Figure II.4 shows the concentration distributions in the matrix at a depth of 10 m from the top of 
the TSw (in the tsw36 geologic layer). 
The lack of retardation of 99Tc is obvious from Figure II.1, which shows breakthrough occurring 
in less than a year. At t = 1 year, significant concentrations of 99Tc are observed at the lower TSw 
boundary at this location. The moderately sorbing 237Np reaches the bottom boundary of the TSw 
at this location in about35 years, but appears to have a transport behavior similar to that of 99Tcafter 
t  100 years. The concentration profile of 239Pu in the fractures is consistent with expectations 
because of its high Kd values. 239Pu reaches the bottom boundary at about t = 300 years. 
Because of the limited thickness of the TSw unit, even 239Pu exhibits substantial transport at t 
 100 years. The relative sorption behavior of the three radionuclides is demonstrated by their 
distribution in the matrix along the x axis at a depth of z = 10 m from the top of the TSw (Figure 
II.4). 
6.6.1.2 Synopsis of Important Findings 
The TSw unit at the location of Cross Section 1 does noteffectively retard the radionuclide transport 
because of its fractured nature and its limited thickness. This is true even for a strong sorber such 
as Pu. 
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Table 6.7. Input parameters for the FRACL transport simulations in Cross Sections 1, 2 and 3 
Parameters Source 
Geologic profiles and rock properties at the 
three cross-sections 
CRWMSM&O 1999h, TableIII-1, 
DTN:LB990501233129.004 
Percolation rate (6 mm/yr) Reasonable value of current mean 
percolation flux for present-day climate 
(see Table 6.11) 
Matrix properties (porosity , immobile water 
saturation Sr), fracture parameters (, 
Sr, active fracture parameter  and frequency 
fa ), rock grain density s 
DTN: LB997141233129.001 
Matrix (Swm) and fracture water saturation 
(Swf ) at steady state 
DTN: LB990801233129.003 
Fracture apertures DTN: LB990501233129.001 
Active interface area fraction [=S1 
wf ], 
active fracture spacing [=1=(fa S1 
wf )] 
Liu et al. (1998, pp: 2637-2638) 
Sorption coefficientsKd DTN: LAIT831341AQ96.001 
Tortuosity  '  DTN: LB991220140160.019 and 
DTN: LAIT831341AQ96.001, 
Grathwohl (1998, pp: 28-35), 
Farrell and Reinhard (1994, p: 64) 
Transfer coefficientKi = 1 Conventionally used value 
Longitudinal dispersivity L = 1 m in the 
fractures, 0.1 m in the matrix 
Scientific judgement in the absence of 
available data 
6.6.2 2-D Transport in TSw, Cross Sections 2 and 3 
6.6.2.1 Results and Discussion 
The parameters for this simulation and the data sources are listed in Table 6.7. Compared to Cross 
Section 1, TSw is substantially thicker in Cross Sections 2 and 3, and the effect of the longer (in 
the z direction) domain is evident in Figures II.5 to II.10 in Attachment II. The figures also denote 
the configuration and thickness of the various TSw layers. 
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The transport of the non sorbing 99Tc in Cross Section 2 (Figure II.5) is fast, and reaches the lower 
boundary of the TSw unit in about 20 years. For t  100 years, the relative concentration of 99Tc 
in the fracture water reaches high levels, and is equal to 1 at t  1,000 years. The transport of 
99Tc in Cross Section 3 (Figure II.8) is analogous to that in Cross Section 2 and shows an earlier 
breakthrough, consistent with the thinner TSw at this location. 
Breakthrough of the moderately sorbing 237Np takes about 60 years in Cross Section 2 (Figure II.6) 
and about 40 years in Cross Section 3 (Figure II.9). In both cases, significant amounts are released 
from the bottom of the TSw for t  100 years. The 239Pu breakthrough occurs at about 6,000 years 
in Cross Section 2 (Figure II.7) and 4,000 years in Cross Section 3 (Figure II.10). 
6.6.2.2 Synopsis of Important Findings 
The TSw layers at the location of Cross Sections 2 and 3 retard radionuclide transport more 
effectively than in Cross Section 1 because of larger total horizon thickness. 
6.6.3 Effect of the Transfer Coefficient Ki 
6.6.3.1 Results and Discussion 
The effect of the transfer coefficient Ki (Section 6.2.1, Equation 6) is investigated here. Although 
this effect is not expected to be significant in non sorbing and weakly sorbing radionuclides, it can 
besubstantial in strong sorbers. SmallerKi valuescorrespond to weaker sorption, thus contaminant 
retardation and/or removal is reduced, leading to larger concentrations in the fractures and increased 
transport. 
Thesemi-infinitesysteminthesesimulations(as wellas inthoseinSections 6.6.4and 6.6.5) consists 
of a fracture and a matrix block corresponding to the properties of TSw35. The parameters for this 
FRACL simulation set (and the corresponding data sources) are listed in Tables 6.7 and 6.8. The 
DTN for the input and output data files is LB991220140160.006. Relative concentration profiles 
in the fractures were obtained for t = 1,000 years. 
The relative concentration of 99Tc in the fractures as shown in Figure II.11 (see Attachment II) 
conforms with the expectation of limited effect ofKi on the transport of a non-sorbing radionuclide. 
Significant differences are observed at very large distances from the point of release. The effect 
on the transport of 237Np, shown in Figure II.12, is much more pronounced. It is obvious that a 
lower Ki corresponds to weaker sorption (because it leads to a lower effective Kd), thus larger 
concentrations in the fractures at the same point. This is supported by Figure II.13, which shows 
the relative concentration profiles in the matrix at z = 50 m. The reduced sorption onto the the 
matrix leads to higher concentration in the liquid phase of the matrix. 
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Table 6.8. Input parameters in the FRACL sensitivity analysis simulations 
(transport in the TSw35 layer) 
Parameters Source 
Transfer coefficientKi = 1, 0.5, 0.1 Reasonable value range for sensitivity 
analysis 
Tortuosity  ' , 0.2, 5 Reasonable value range for sensitivity 
analysis 
Longitudinal dispersivity in the fractures 
L = 1 m, 0.1 m, 10 m 
Reasonable value range for sensitivity 
analysis 
The 239Pu transport in Figures II.14 and II.15 show the most pronounced effect of Ki. Lower 
Ki results in significantly higher Pu concentrations both in the fractures and in the matrix, and, 
consequently, in transport over longer distances. 
6.6.3.2 Synopsis of Important Findings 
The transfer coefficient Ki may be important in the migration of strongly sorbing radionuclides 
(such as Pu) from possible releases from the potential repository. Currently it is not known whether 
the effects of the Ki variations in the UZ are within the PA tolerances. 
6.6.4 Effect of the Matrix Tortuosity 
6.6.4.1 Results and Discussion 
The RTMsensitivity to tortuosity coefficient (  1) is investigated in this section. The parameters 
for this FRACL simulation set (and the corresponding data sources) are listed in Tables 6.7 and 
6.8. The simulations were conducted under the same conditions discussed in Section 6.6.3, from 
which they differed only in that the matrix tortuosity coefficient was varied. Increasing matrix 
tortuosity coefficientleads tomore pronounced diffusionin thematrix, which in turn results inlower 
concentrations in the fractures, increased sorption in the matrix, and thus delayed breakthroughs. 
The effect of tortuosity coefficient is therefore expected to be more pronounced in strongly sorbing 
systems. 
TheDTNoftheFRACLinputandoutputdatafiles isLB991220140160.006. Relativeconcentration 
profiles in the fractures and in the matrix were obtained at t = 1,000 years. The FRACL simulations 
indicate that the effect of matrix tortuosity coefficient on the transport of 99Tc is substantial. Larger 
tortuosity coefficient values (as multiples of porosity) lead to lower relative concentrations and 
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delayed breakthroughs in the fractures (Figure II.16, see Attachment II), and larger concentrations 
in the matrix (Figure II.17). 
The tortuosity coefficient effect becomes increasingly important as sorption (quantified by the 
Kd value) increases. With increasing tortuosity coefficient, transport of 237Np in the fractures is 
greatly retarded (Figure II.18), and its concentration profile in the matrix (Figure II.19) shows a 
more uniform distribution, consistent with the higher matrix diffusion. A low tortuosity coefficient 
value (= 0:2  ) leads to a dramatically faster transport of 239Pu in the fractures (Figure II.20), 
while a high tortuosity coefficient value (= 5 ) reduces 239Pu concentrations to practically non 
detectable levels in the matrix (Figure II.21). 
6.6.4.2 Synopsis of Important Findings 
The sensitivity analysis study in this section indicates that tortuosity can have a significant effect 
on transport, and the issue of obtaining accurate  data merits attention. Currently it is not known 
whether the effects of the  variations in the UZ are within the PA tolerances. 
6.6.5 Effect of Dispersion in the Fractures 
6.6.5.1 Results and Discussion 
The RTM sensitivity to the longitudinal dispersion L is investigated in this section. The FRACL 
simulations in this study were conducted under the same conditions discussed in Section 6.6.3, from 
which they differed only in that the longitudinal dispersivity L of the fracture was varied. The 
parameters for this FRACL simulation set (and the corresponding data sources) are listed in Tables 
6.7 and 6.8. The DTN for the input and output data files is LB991220140160.006. The FRACL 
simulations indicate that at t = 1,000 years the effect of L is minimal on the 99Tc transport (Figure 
II.22) and marginal on the 237Np transport (Figure II.23). 
Conversely,variations in the magnitude of L have a pronounced effect on the transport of 239Pu. A 
larger L value significantly enhances transport in the fractures, and leads to earlier breakthroughs 
(Figure II.24) and higher concentrations in the matrix (Figure II.25). 
6.6.5.2 Synopsis of Important Findings 
Knowledge of L can be important in reliably predicting the transport of strongly sorbing 
radionuclides. Currently it is not known whether the effects of the L variations in the UZ are 
within the PA tolerances. 
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6.7 2-D TRANSPORT IN THE CHn LAYERS 
This section focuses on radionuclide transport in 2-D vertical cross sections of the CHn hydrogeologic 
unit under the conditions discussed in Section 6.5. It is subdivided in three subsections. 
In Section 6.7.1 we address general issues. In Section 6.7.2 we investigate the transport of 99Tc, 
237Np and 239Pu at Cross Sections 1 and 2. The results of the study appear in Figures III.1 to III.6 
(Attachment III). The subject of Section 6.7.3 is the transport of the same radionuclides at Cross 
Section 3 (Figures III.7 to III.9). 
6.7.1 General Issues 
6.7.1.1 The FRACL Simulations 
The simulations in Section 6.7 were conducted using the FRACL code and involved 99Tc, 237Np, 
and 239Pu (Table 6.5). The parameters and the data sources for these simulations are listed in Tables 
6.6 and 6.7. The DTN for the FRACL input and output data files is LB991220140160.007. The 
radionuclide release scenario was the same as in the TSw unit (Section 6.6). Transport was studied 
in the CHn layers at the three locations (Cross Sections 1, 2 and 3) discussed in Section 6.5. 
6.7.1.2 Perched Water Considerations 
Note that the perched water at the TSw/CHn interface is not considered in this 2-D study, which 
focuses on transport exclusively within the CHn hydrogeologic unit and not at (or through) its 
interfaces. This subject is addressed in the study of transport underneath the potential repository in 
Section 6.9, in which we discuss transport across all the hydrogeologic units from the stratigraphic 
horizon of the potential repository to the groundwater. 
The 3-D site-scale studies in Sections 6.11 to 6.14 account for the complexities of the effects 
of perched water on transport. Additionally, Section 6.15 focuses exclusively on the effect of 
three different conceptual models of perched water on the transport behavior of 99Tc, 237Np and 
239Pu. The 3-D studies in Sections 6.11 to 6.15 can address complex issues of flow bypassing and 
focusing (and their effect on transport) that are beyond the capabilities of the 2-D FRACL code. 
The discussion in this section should be viewed as strictly an investigation of the fate and transport 
of radionuclides that manage to enter the CHn Formation. 
6.7.2 2-D Transport in CHn, Cross Sections 1 and 2 
6.7.2.1 Results and Discussion 
Cross Sections 1 and 2 are located in the southern part of the potential repository. Their location 
relative to the potential repository is discussed in Section 6.5.3 and is shown in Figure 6.5.1. The 
stratigraphy of the CHn unit in Cross Sections 1 and 2 is dominated by vitric layers (Figures 6.5.2 
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and 6.5.3). 
The CHn hydrogeologic unit in Cross Section 1 (see Figure 6.5.2) consists of five vitric layers 
(ch1v, ch2v, ch3v, ch4v, and ch5v) and one zeolitic layer (ch6z). The CHn unit in Cross Section 2 
(see Figure 6.5.3) consists of four vitric layers (ch1v, ch2v, ch3v, ch4v, and ch5v) and two zeolitic 
layers (ch5z and ch6z). Transport is studied in Cross Sections 1 and 2 together because of the 
similarity of geology and transport behavior. 
Transport in the vitric layers is expected to be substantially different from that in the zeolitic 
layers because of the distinctively different properties and characteristics of these layers. The 
permeabilitiesofthefracturesandofthematrixofthevitriclayersaresimilarinmagnitude(CRWMS 
M&O 2000a, Section 6). This permeability parity, coupled with a large fracture spacing, result in 
a behavior similar to that of a nonfractured porous medium (CRWMS M&O 2000a, Section 6). 
In contrast, the zeolitic layers in the northern part of the potential repository (Cross Section 3) have 
similar fracture spacing and fracture permeability, but the matrix permeability is about five orders 
of magnitude lower than that in the fractures (CRWMSM&O 2000a, Section 6). Thus, matrix flow 
in the zeolitic layers of Cross Section 3 is extremely slow and practically all the flow occurs in the 
fractures, leading to relatively fast transport. 
In Cross Section 1, the distribution of relative concentration (with respect to the concentration at 
the release point) of the three radionuclides in the fractures along the z-axis are shown in Figures 
III.1 to III.3 (see Attachment III), which also denote the various layers of the CHn hydrogeologic 
unit involved in transport. Figures III.4 to III.6 show the radionuclide concentration in the fractures 
of the CHn unit in Cross Section 2. 
As expected, an increasing Kd results in transport over a longer distance for a given time. The 
strong sorptive tendency of 239Pu is demonstrated in Figures III.3 and III.6, which indicate that 
the advancement of the Pu front is limited to a few meters (<10 m) from the point of release. The 
different (fracture-controlled) transport properties of the zeolitic zone ch6z are shown in Figures 
III.1 and III.2, and are denoted by the almost flat (i.e., constant) concentration (characteristic of 
fast transport) once the zeolitic layer is reached. The same (and even more pronounced) pattern of 
constant concentration is observed in the thickest zeolitic layers (ch5z and ch6z) of Cross Section 
2 (Figure III.4 and III.5) 
Figures III.1 and III.4 show that the 99Tc front reaches the bottom of the CHn unit in a few hundred 
years (<1,000 years). The 237Np takes several thousand years (<10,000 years) in Cross Section 1 
(Figure III.2), and over 10,000 years in the thicker CHn unit of Cross Section 2 (Figure III.5). In 
either column, the 239Pu front does not escape ch1v, i.e., the first layer in the unit, within 100,000 
years (Figures III.3 and III.6). 
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6.7.2.2 Synopsis of Important Findings 
It appears that, at Cross Sections 1 and 2, the CHn unit is an effective transport barrier. This results 
from the dominant presence of vitric layers, which act as a porous (rather than fractured) medium 
by virtue of their infrequent fracture spacing and similar permeabilities in the matrix and in the 
fractures. 
6.7.3 2-D Transport in CHn, Cross Section 3 
6.7.3.1 Results and Discussion 
TheCHnunitinCross Section3presents anentirely differentgeologic picturethanatCross Sections 
1 and 2. It is characterized by the absence of vitric layers (see Figure 6.5.4). This hydrogeologic 
unit consists of six zeolitic layers (ch1z, ch2z, ch3z, ch4z, ch5z, and ch6z). Because the fracture 
permeability is about five orders of magnitude larger than that in the matrix (CRWMSM&O2000a, 
Section 6) of the zeolitic layers, radionuclide transport through the unit is expected to be advectioncontrolled 
and rapid at this location. Thus, the greater potential adosorption of radionuclides onto 
the zeolitic matrix (as quantified by the Kd values) does not result in increased retardation because 
the fracture-dominated flow does not allow significant contact of the water with the matrix. 
The simulation results are entirely consistent with the expected transport behavior. Despite the 
relatively large thickness of the unit at this location, 99Tc and 237Np reach the bottom boundary in 
less than 10 years (Figures III.7 and III.8, Attachment III). The stronger-sorbing 239Pu needs more 
than 1,000 years (but less than 10,000 years) to cover this distance (Figures III.9), a relatively short 
time compared to its half-life of 2.41104 years (Table 6.5). 
6.7.3.2 Synopsis of Important Findings 
At the location of Cross Section 3, the CHn unit is extremely inefficient in retarding transport 
despite its relatively large thickness. This is caused by the uniformly zeolitic nature of the unit 
at this location, the layers of which are characterized by high fracture permeability and a nearly 
impermeable matrix. 
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6.8 2-D TRANSPORT IN THE PP LAYERS 
This section focuses on radionuclide transport in 2-Dvertical cross sections of thePP hydrogeologic 
unit under the conditions discussed in Section 6.5. Section 6.8 is subdivided in three subsections. 
In Section 6.8.1 we address general issues. In Section 6.8.2 we investigate the transport of 99Tc, 
237Np and 239Pu at Cross Sections 1 and 2. The results of the study appear in Figures IV.1 to IV.6 
(Attachment V). The subject of Section 6.8.3 is the transport of the same radionuclides at Cross 
Section 3 (Figures IV.7 to IV.9). 
6.8.1 General Issues 
The simulations in Section 6.8 were conducted using the FRACL code and involved 99Tc, 237Np 
and 239Pu (Table 6.5). The parameters and the data sources for these simulations are listed in Table 
6.6 and 6.7. The DTN for the input and output data files is LB991220140160.008. 
The radionuclide-release scenario was the same as in the TSw and the CHn units (see Sections 6.5 
to 6.7). The purpose of this study was to investigate the fate and transport of radionuclides that 
manage to migrate through the overlaying TSw and CHn hydrogeologic units and enter the PP unit 
at the three locations (Cross Sections 1, 2 and 3) discussed in Section 6.5 (Figures 6.5.2 to 6.5.4). 
Note that layer numbering in the PP units decrease with depth. 
As indicated in the previous sections, Cross Sections 1 and 2 are located in the southern part of 
the potential repository. At these locations, the PP hydrogeologic units directly underlie the vitric 
layers of the CHn unit. Cross Section 3 is in the northern part of the potential repository, at a 
location where the PP hydrogeologic unit underlie the highly-permeable (compared to the matrix) 
fractures of the zeolitic layers of the CHn unit. More complex phenomena and processes (such as 
transport in fault zones, transport across geologic interfaces, flowdiversion, and funnel flow through 
the areally shrinking (with depth) vitric layers of the CHn hydrogeologic unit overlying the PP unit 
near Cross Section 1) cannot be resolved by the 2-D nature of FRACL. These are investigated in 
the 3-D studies discussed in Sections 6.11 to 6.15. 
6.8.2 2-D Transport in PP, Cross Sections 1 and 2 
6.8.2.1 Results and Discussion 
The PP hydrogeologic units in Cross Sections 1 and 2 are similar in terms of geologic structure, 
relative thickness of the various PP layers, and total thickness. Thus, they are studied together. At 
these two locations, PP consists of (a) a rather thin zeolitic layer (pp4), (b) a thick devitrified layer 
(pp3) followed by a thinner devitrified layer (pp2), and (c) a thick zeolitic layer (pp1). These layers 
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are denoted in Figures 6.5.2 and 6.5.3. Note that the groundwater table occurs in the pp1 layer in 
Cross Section 2 and 3. 
In terms of flow and transport, the devitrified layers are similar to the vitric layers in the CHn 
(CRWMSM&O2000a, Section6). Consequently, transportinthePPisexpectedtobecharacterized 
by(a)arapidtransportphaseinthefracturesofthezeoliticpp4layer, followedby(b)slowertransport 
inthe devitrified pp3 and pp2 layers(whose behavior is akin toporous, rather than fractured, media), 
and (c) by rapid transport again once the pp1 layer is reached. 
The relative concentrations of the three radionuclides in the fractures of the PP layers along the 
z-axis in Cross Section 1 are shown in Figures IV.1 to IV.3 in Attachment IV. Figures IV.4 to IV.6 
show the radionuclide concentration in the fractures of the PP unit in Cross Section 2. 
The simulations confirm the expected transport pattern. Figures IV.1to IV.6show that pp4 (i.e., the 
top zeolitic layer) at both locations is breached in a short time, and then radionuclide transport is 
controlled by the devitrified layers. These layers are quite efficient in retarding transport even for 
the nonsorbing 99Tc (Figures IV.1 and IV.4), which takes over 1000 years to cross the devitrified 
layers. 
Once the advancing solute front reaches pp1 (i.e., the bottom zeolitic layer), transport is fast and 
practically unretarded, as evidenced by the constant concentration (indicated by the flatness of the 
relative concentration curve) in this layer in the transport of 237Np (Figures IV.2 and IV.5). It takes 
several thousand (<10,000) years to reach the pp1 layer, after which time the radionuclide front 
advances rapidly. 
Although the 239Pu front crosses the pp4 layer in a relatively short time, the devitrified layers appear 
to be very effective in retarding its transport. This is indicated by the steepness of the Pu relative 
concentration curve in pp3, and the fact that the Pu front does not reach the pp3 boundary even 
after 100,000 years (Figures IV.3 and IV.6). 
6.8.2.2 Synopsis of Important Findings 
At the location of Cross Sections 1 and 2, transport is practically uninhibited in the top zeolitic 
layer of the PP hydrogeologic unit, but is effectively retarded by the underlying devitrified layers. 
Once the radionuclide solute front reaches the bottom of the devitrified layers, transport becomes 
very fast because of the fast, fracture-dominated flow in the pp1 zeolitic layer. 
6.8.3 2-D Transport in PP, Cross Section 3 
6.8.3.1 Results and Discussion 
Although the PP hydrogeologic unit in Cross Section 3 consists of the same layers as in Cross 
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Sections 1 and 2, they differ in the relative thickness of the zeolitic and devitrified layers and in the 
total PP unit thickness. Thus, (a) pp4 is much thicker (than in Locations 1 and 2), (b) the devitrified 
layers are thinner, and (c) the combined thickness of the zeolitic pp4 and pp1 layers in Cross Section 
3 constitute over half the PP unit thickness (which is shorter than that in Cross Sections 1 and 2). 
The layers in the PP hydrogeologic unit in Cross Section 3 are shown in Figure 6.5.4. Because of 
the geologic differences, transport in the PP in Cross Section 3 is expected to be substantially faster 
than in Cross Sections 1 and 2, owing to the predominant presence of the zeolitic layers and the 
limited thickness of the devitrified layers. 
The relative concentrations of the three radionuclides in the fractures of the PP layers along the 
z-axis in Cross Section 3 are shown in Figures IV.7to IV.9in Attachment IV.The simulation results 
are entirely consistent with the expected transport behavior. The 99Tc front reaches the bottom of 
the PP hydrogeologic unit much faster than in Cross Sections 1 and 2 (Figure IV.7), after which 
time transport in the pp1 layer is very fast (denoted by the virtually constant concentration in this 
layer). 
A similar pattern emerges in the transport of 237Np, which reaches the bottom of the PP unit 
much earlier (<10,000 years) than in Cross Sections 1 and 2 (Figure IV.8), and exhibits constant 
concentration in the pp1. The 239Pu transport is marked by its strongly sorbing property. Although 
the relatively thick pp4 layer is crossed by the Pu front relatively quickly, the devitrified layers 
are very effective in retarding its advance (Figure IV.9). This is indicated by the steepness of the 
concentration curve in the devitrified layers, and the fact that radionuclides do not emerge from 
them until after 100,000 years. 
6.8.3.2 Synopsis of Important Findings 
At the location of Cross Section 3, the transport of 99Tc and 237Np is much faster than in Cross 
Sections 1 and 2 because of the greater thickness of the zeolitic layers relative to the devitrified 
layers. The 239Pu transport, however, is effectively retarded at this location because after 100,000 
years it had not yet reached the pp1 layer. 
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6.9 2-D TRANSPORT UNDERNEATH THE POTENTIAL REPOSITORY 
This section focuses on radionuclide transport in 2-D vertical cross sections that include all the 
hydrogeologic units from the potential repository horizon to the water table. Section 6.9 includes 
nine subsections. 
In Section 6.9.1 we address general issues. In Sections 6.9.2 and 6.9.3 we discuss the transport of 
99Tc, 237Np and 239Pu at Cross Section 1 for a (a) mean present-day infiltration (Figures V.1 to 
V.3, see Attachment V) and (b) high glacial infiltration (Figures V.4to V.6), respectively (see Table 
6.11). 
In Sections 6.9.4 and 6.9.5 we investigate transport at Cross Section 2 for a (a) mean present-day 
(Figures V.7 to V.9) and (b) high glacial infiltration (Figures V.10 to V.12), respectively. Similarly, 
in Sections 6.9.6 and 6.9.7 we investigate transport at Cross Section 3 for a (a) mean present-day 
(Figures V.13 to V.15) and (b) high glacial infiltration (Figures V.16 to V.19), respectively. 
In Section 6.9.8 we evaluate the effect of perched water bodies on transport at Cross Section 3 for a 
mean present-day infiltration. Finally, in Section 6.9.9 we discuss some imporant results and their 
implications. 
6.9.1 General Issues 
In Sections 6.5 through 6.8 we focused on the study of transport in individual hydrogeologic units. 
More specifically, we investigated the fate and migration of radionuclides that entered each of 
the three major hydrogeologic units underlying the potential repository horizon, and we identified 
mechanisms and geological properties that affect transport. 
6.9.1.1 Focus of the Study 
In the present section, we study radionuclide transport in composite 2-D sections covering the 
entire geologic profile from the potential repository to the groundwater table. The purpose of these 
simulationsis toevaluate theintegratedtransport performanceof all thehydrogeologic unitsbeneath 
the potential repository, accounting for changes in fracture aperture, frequency, active spacing, and 
saturation distribution (in the fractures and the matrix) across layer interfaces. 
6.9.1.2 Radionuclides Considered 
The transport of 99Tc, 237Np and 239Pu (Table 6.5) was studied. The transport model simulates 
continuous and time-invariant release at the location of the potential repository. The radionuclide 
concentration distribution in the profile is monitored over time. When occurring, sorption is 
described by a linear equilibrium equation (Equation 9, Section 6.2.3.1). 
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6.9.1.3 The 2-D FRACL Simulations 
Transport was studied in the three 2-D geological profiles of Cross Sections 1, 2 and 3 (see Section 
6.5). The FRACL code was used for the simulations, each of which needed less than a minute of 
execution time to complete. The parameters and the data sources for these simulations are listed in 
Tables 6.6 and 6.7. The DTN for the input and output data files is LB991220140160.009. 
6.9.1.4 Perched Water 
Perched water is not an important issue in Cross Sections 1 and 2, but can be more relevant in Cross 
Section 3, at which location perched water was encountered (CRWMS M&O, 1999d, Section 
6.2.2). Thus, the effect of perched water bodies was confined to a limited comparative study in 
Cross Section 3 (see Section 6.9.8), but was not considered in the rest of the simulations. 
The rationale for this approach is that the focus of the simulations in Section 6.9 was to investigate 
the worst-case scenario (shortest possible breakthrough times) and to provide the upper limit of 
the rate and extent of radionuclide transport. An additional reason is that there is very little direct 
information on the hydrogeologic properties and conditions that lead to the emergence of perched 
water in these low-permeability zones, i.e., the zeolitic CHn or the densely welded basal vitrophyre 
of the TSw (CRWMS M&O, 1999d, Section 6.2.2). The effect of perched water bodies, however, 
is thoroughly addressed in the 3-D site-scale simulations discussed in Sections 6.11 to 6.16. 
6.9.2 2-D Radionuclide Transport in Cross Section 1, Mean Present-Day Infiltration 
6.9.2.1 Results and Discussion 
A cross section of the 2-D domain in Cross Section 1, indicating the layers of all the hydrogeologic 
units involved in the transport, their elevation, and their thickness, was shown in Figure 6.5.2. Note 
that at this location the Bullfrog (BF) hydrogeologic unit is present. The total distance between the 
bottom of the potential repository and the water table at this location is about 350 m. 
The infiltration rate in these simulations was 6 mm/year, i.e., about the mean present-day infiltration 
(see Table 6.11). Figure V.1 in Attachment V shows the relative concentration profile of the non 
sorbing 99Tc over a period of 100,000 years. The 99Tc front takes several thousand (but <10,000) 
years to reach the water table . As expected (due to its different sorption behavior), the 237Np 
breakthrough at the water table takes longer than 10,000 (but <100,000) years (Figure V.2). The 
same figure clearly denotes the presence of the highly permeable (compared to the matrix) fractures 
in the zeolites, indicated by the near-constant concentration profile in ch6z and pp4. The strongly 
sorbing 239Pu does not advance past the ch1v layer, less than 60 m from the point of release, even 
after t = 100,000 years (Figure V.3). 
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6.9.2.2 Conceptual Model of Transport in Cross Section 1 
Figure 6.9.1 illustrates a conceptual model of transport in Cross Section 1 that incorporates 
the findings from Sections 6.5 through 6.9. Water-borne radionuclides enter the TSw formation 
through the bottom of the potential repository. Radionuclide transport in the TSw hydrogeologic 
unit is occurs mostly in the fractures (see Section 6.7). 
The vitric layers in the underlying CHn unit at this location (i.e., layers ch1v through ch5v) behave 
as porous (rather than fractured) media because of the parity of permeability in the matrix and in 
the fractures (CRWMSM&O 2000a, Section 6). Thus transport occurs in both the matrix and the 
fractures, and the contact times between the radionuclides and the media is longer. The vitric layers 
are effective transport barriers because of the increased sorption (for sorbing radionuclides) and 
retardation (see Section 6.7). Once the radionuclide reaches the zeolitic ch6z unit, flow becomes 
again fracture-dominated, and, consequently, so does transport. 
Transport in the pp4 layer, the top layer in the PP hydrogeologic unit, is controlled by its zeolitic 
nature, which leads to fractured-dominated flow and transport. The next two layers (i.e., pp3 and 
pp2) are devitrified and behave similarly to the vitric layers in the CHn unit. Transport in the thick 
zeolitic pp1 layer (the last layer in the PP unit) is again fractured-dominated, as is transport in the 
underlying layers of the BF unit (see Section 6.8). 
6.9.3 2-D Radionuclide Transport in Cross Section 1, High Glacial Infiltration 
The simulations discussed in Section 6.9.2 were repeated for an infiltration rate of 33.5 mm/year, 
i.e., the high glacial infiltration (See Table 6.11). As Figures V.4 to V.6 in Attachment V show, the 
effect on transport is significant. 
The breakthrough of the non sorbing 99Tc (Figure V.4) occurs much earlier, i.e., after less than 
1,000 years. The 237Np front reaches the groundwater in more than 10,000 years (Figure V.5). 
Despite an infiltration rate over 5 times that in the mean present-day case, the 239Pu front advances 
only slightly in the profile (to a distance of 82 m from the point of release), but is still far from 
reaching the groundwater at t = 100,000 years (Figure V.6). 
6.9.4 2-D Radionuclide Transport in Cross Section 2, Mean Present-Day Infiltration 
A cross section of the domain at this location, indicating the layers of all the hydrogeologic units 
involved in the transport, their elevation, and their thickness, is shown in Figure 6.5.3. The total 
distance between the bottom of the potential repository and the water table at this location is about 
350 m. The infiltration rate in the simulations was 6 mm/year, i.e., about the mean present-day 
infiltrations (see Table 6.11). 
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Figure 6.9.1. A conceptual model of transport in Cross Section 1. 
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Figure V.7inAttachment Vshows therelativeconcentration profile of 99Tc over aperiod of 100,000 
years. The 99Tc front takes several thousand (but <10,000) years to reach the water table . Note the 
near-constant concentration in the zeolitic layers of the CHn and the PP hydrogeologic units. As in 
Cross Section 1, the 237Np breakthrough at the water table takes longer than 10,000 (but <100,000) 
years (Figure V.8). Because of the relatively large thickness of the highly fractured TSw unit in 
Cross Section 2, the strongly sorbing 239Pu migrates much further than in Cross Section 1, reaching 
a distance of about 150 m from the release point (Figure V.9). It does not, however, advance past 
the ch1v layer after 100,000 years. 
6.9.5 2-D Radionuclide Transport in Cross Section 2, High Glacial Infiltration 
The simulations discussed in Section 6.9.4 were repeated for an infiltration rate of 33.5 mm/year. 
The increase in contaminant transport observed here is analogous to that observed in Cross Section 
1. 
The breakthrough of 99Tc (Figure V.10) occurs much earlier than for the mean present-day 
infiltration case, i.e., after several hundred years, while at 1,000 years its concentration at the 
water table equals that at the release point. This is the same behavior observed in the much shorter 
Cross Section 1 domain. The 237Np front reaches the groundwater in less than 10,000 years (Figure 
V.11), while the incremental advance of 239Pu is relatively small (about 180 m from the point 
of release) compared to the mean present-day infiltration case, but is still far from reaching the 
groundwater at t = 100,000 years (Figure V.12). 
6.9.6 2-D Radionuclide Transport in Cross Section 3, Mean Present-Day Infiltration 
A cross section of the domain at this location, indicating the layers of all the hydrogeologic units 
involved in the transport, their elevation, and their thickness, is shown in Figure 6.5.4. The total 
distance between the bottom of the potential repository and the water table at this location is about 
310 m. 
Inspection of the 99Tc profile in Figure V.13(see Attachment V) shows a drastically different profile 
from those in Cross Sections 1 and 2. The extensive zeolitic zones at this location result in very 
rapid transport, and the 99Tc front reaches the water table in significantly less time than 1,000 
years. Note the near-constant concentration in the extensive zeolitic layers of the CHn and PP 
hydrogeologic units. 
Similarly, the 237Np breakthrough at the water table takes substantially less than 10,000 (Figure 
V.14). Eventhe stronglysorbing 239Pu showsdrastically enhancedmigration, reachinga distanceof 
about255mfrom therelease point(FigureV.15). Thelargeportionsof near-constantconcentrations 
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indicate the substantial impact of zeolites on transport. Although Pu in Cross Section 3 advances 
much further than in either Cross Section 1 or 2, it does not migrate past the devitrified pp3 layer 
within 100,000 years. 
6.9.7 2-D Radionuclide Transport in Cross Section 3, High Glacial Infiltration 
The simulations discussed in Section 6.9.6 were repeated for an infiltration rate of 33.5 mm/year. 
Figure V.16 shows that, at t = 100 years, the 99Tc front has reached the upper boundary of the 
extremely permeable (and conducive to transport) zeolitic layer pp1. Thus,99Tc breakthrough at 
the water table is expected at a little more than 100 years. 
The 237Np breakthrough occurs at t < 1,000 years (Figure V.17), indicating a clear acceleration of 
transport over the climatic scenario of mean present-day infiltration. Under these conditions, even 
the strongly sorbing 239Pu exhibits a significantly enhanced migration and reaches the groundwater 
in less than 100,000 years (Figure V.18). 
6.9.8 2-D Radionuclide Transport in Cross Section 3 with Perched Water, 
Mean Present-Day Infiltration 
There is evidence to suggest that perched water occurs at the interface of the TSw and CHn units 
at location of Cross Section 3 (CRWMS M&O 1999d, Section 6.2.5). In this section, the effect 
of perched water on transport is investigated. As field data from this location are very limited, 
reasonable approximations (stated and justified in Sections 6.7.1.2 and 6.9.8.1) had to be made in 
the FRACL simulations. 
6.9.8.1 Representation of the Perched Water in the FRACL Simulations 
The fracture and matrix water saturations were set to 1 in the tsw38 and tsw39 layers, i.e., the layers 
immediately above the TSw-CHn interface. Although there are no supporting field measurements, 
this configuration corresponded to the prediction of the perched water depth from the simulations 
in CRWMS M&O (1999d, Section 6.2.5). Additionally, the fractures in the ch1z (the top zeolitic 
layer of CHn at this location) were assumed to be filled and to have the same (a) saturation and (b) 
transport properties with the matrix in the same layer. Thus, the ch1z layer was acting as a porous, 
rather than a fractured, medium. 
6.9.8.2 Results and Discussion 
The effect of the perched water body itself (i.e., the saturated tsw38 and tsw39 layers) on transport 
appears to be minimal, as is demonstrated by a comparison of the concentration profiles in the 
tsw38 and tsw39 layers of the perched and no-perched water regimes in Figure V.19 and V.13, 
respectively. On the other hand, the effect of the geological conditions that lead to the perched 
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water body, namely the filled fractures in ch1z, is dramatic and is more pronounced at earlier times. 
Figure V.19shows that, at t = 10 and t = 100 years, the edge of the 99Tc front has advanced about130 
m less than the front in Figure V.13, in which the perched water body is not considered (i.e., when 
the ch1z layer is treated as a fractured and unsaturated medium). Once the ch1z layer is breached, 
99Tc travels fast in the underlying fractured layers. At t = 1,000 years, the 99Tc concentration is 
beginning to appear at the water table , although (a) its arrival is delayed, and (b) its concentration 
is lower in all the layers below the tsw39 layer compared to those for no-perched water in Figure 
V.13. The concentration profiles of 99Tc for the perched and the no-perched water models (Figures 
V.19 and V.13, respectively) coincide for t  10,000 years. 
Becauseof itsstronger sorption, att= 10 years there is nodifference betweenthe 237Np distributions 
for the perched water regime in Figure V.20and the no-perched water model in Figure V.14. This is 
because the advancing front has not yet reached the ch1z layer. The maximum effect is observed at t 
= 100 years, at which time the front is more than 100 mabove its position for no-perched water. At t 
= 1,000 years, the front (a) has already breached the ch1z layer and (b) is at the same location as that 
for the no-perched water regime (i.e., the bottom of the pp3 layer), but (c) the 237Np concentrations 
in the fractured ch2z to ch6z layers are 150 times (or less) lower than that for no-perched water in 
Figure V.14. At t = 10,000 years, the 237Np distributions show differences in magnitude only in 
the bottom (above the water table ) two layers pp2 and pp1, with the perched water concentrations 
being lower. At t = 100,000 years, the distributions coincide. 
The concentration profile of strongly sorbing 239Pu in the perched water regime (Figure V.21)does 
not show any differences from those for no-perched water (Figure V.15)for t 1,000 years because 
the advancing front has not yet reached the ch1z layer. For t  10,000 years, the 239Pu fronts in 
Figures V.21 and V.14 are at about the same location, but the concentrations in the fractured ch2z 
to pp4 layers are lower in the perched water regime. 
6.9.8.3 An Important Point 
Note that these results were obtained by considering a single geologic layer acting as a permeability 
barrier (i.e., the ch1z layer acting as a porous, rather than fractured, medium). If this barrier involves 
more than one CHn and/or PP layers, then the additional retardation effect on transport is expected 
to be significant. 
6.9.9 Synopsis of Findings 
A review of the results in Sections 6.9.2 through 6.9.8 indicates that while the geological profiles 
in Cross Sections 1 and 2 afford good retardation of radionuclide transport (and especially of 
the strongly sorbing 239Pu), this is not the case in the domain of Cross Section 3 because of the 
preponderance of highly permeable (compared to the matrix) fractures of the zeolitic layers at this 
location. The enhancement of transport increases rapidly with a decreasingKd of the radionuclide, 
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but is far less important in the case of the strongly sorbing 239Pu. 
Increases in the infiltration rate, brought about by possible changes in climatic patterns, can have a 
substantial impact on breakthrough times, especially at the Cross Section 3 location. The effect of 
changes in infiltration becomes more pronounced with weaker-sorbing radionuclides. 
Conditions leading to the occurrence of perched water bodies can lead to significant retardation. 
Their effect appears to be more pronounced for weaker-sorbing radionuclides at earlier times. 
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6.10 3-D BUSTED BUTTE STUDIES 
The Busted Butte Unsaturated Zone Transport Test (UZTT) is a long-term experiment conducted 
in Busted Butte, Yucca Mountain (CRWMS M&O 1999e, Section 6.8) to investigate flow and 
transport issues in the UZ site-process models for Yucca Mountain, including 
1. The effect of heterogeneities on flow and transport under unsaturated conditions in the 
CHn hydrogeologic unit, particularly fracture-matrix interactions and permeability contrast 
boundaries; 
2. The migration behavior of colloids in the CHn layers; 
3. The validation of laboratory sorption results; 
4. Scalingeffects(from laboratorytofield tosite)on3-Dsite-scaleflowandtransport simulations. 
The site was selected because of the presence of a readily accessible interface of the TSw and CHv 
units, and the similarity of these layers to those beneath the potential repository horizon. The study 
of the Tsw/CHv interface is important because of the important role that the vitric layers of the CHv 
unit play in radionuclide retardation (see Section 6.7). The test proceeded in two phases, which 
differ in design, purpose, and experimental scales, among other factors. A detailed description of 
the tests can be found in CRWMS M&O (1999e, Section 6.8). 
The Busted Butte studies reported in this AMR were limited to numerical simulations of two sets 
of tests in the the first phase of the experiment, namely the Phase 1A and 1B tests (see discussion 
in Sections 6.9.1 and 6.9.2). The field work on these phases has been completed, but the analysis 
of the experimental results is not yet complete. 
6.10.1 Numerical Simulation of the Phase 1A Test 
6.10.1.1 Purpose 
The purpose of this modeling study was to predict the concentration and water saturation 
distributions after the injection of a non-reactive tracer into the ch1v and ch2v layers. Of the 
four tracers injected during the field experiment, only the injection of a non-sorbing Br solution 
was simulated because no other data were available at the time of this study. 
6.10.1.2 Procedure and Layout 
A schematic of the borehole layout in the Phase 1A test is shown in Figure VI.1 (see Attachment 
VI). The layout does not include distances because these were unavailable at the time of preparation 
of this report. The test involved injection rates of 10 mL/hr into boreholes 1 and 3 (located in the 
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ch1v layer of the CHn unit), and of 1 mL/hr into boreholes 2 and 4 (located in the ch2v layer of the 
CHn unit). Injections were conducted continuously for 285 days, starting April 2, 1998. 
Mineback of the Phase1A test block took place from January 15, 1999 to March 3, 1999. During 
mineback, assuccessivelayerswerebeingremoved,digitalphotographsundervisibleandultraviolet 
light were taken, rock samples were collected by augering, and the exposed plane was accurately 
surveyed. When the tracer distribution and moisture content data from this experiment become 
available, they will be used for the calibration of the simulation results discussed in the present 
section. 
Borehole 3 is located in the ch1v layer and is about 20 cm above the ch1v-ch2v interface. Borehole 
1 is also located in the ch1v layer, but is further away from the interface. Injection into boreholes 
2 and 4 is not expected to be strongly affected by the interface because of the very low injection 
rates into these boreholes. 
6.10.1.3 Conceptual and Numerical Model 
Forthis3-Dnumericalstudy, theunderlyinggeologicmodelconsideredahomogeneous, unfractured 
rock matrix with the properties of the ch1v and ch2v layers. The initial saturation distribution was 
based on in situ measurements (Table 6.9). The T2R3D code (V1.4, STN: 10006-1.4-00, see 
Section 3; Wu et al. 1996) was used for the simulation. Each borehole was simulated separately. 
The DTN of the input and output files for this simulation set is DTN LB991220140160.010. Table 
6.9 includes the input parameters for the the Phase 1A simulations. 
Three different sources of flow parameters were used in the simulations (Table 6.9): Source 1 
(hereafter referred to as S1A) was the UZ99 calibrated flow parameter set; Source 2 (referred to as 
S2A) was hydraulic property measurements from field-collected samples, and Source 3 (referred 
to as S3A) was the parameter set included in DTN: LB971212001254.001 (Table 6.9). 
6.10.1.4 Simulation Results and Discussion 
Figure VI.2 shows the distribution of the nonsorbing Br tracer on a 2-D cross section (parallel to 
the face of the rock surface) that includes the injection point (y = 1.5 m) corresponding to borehole 
3 at t = 285 days. These results are obtained using the S1A parameters for both the ch1v and ch2v 
layers (see Table 6.9). The observed flattening of tracer distribution occurs as the tracer moves 
preferentially laterally along the interface. 
When the S2A properties are used, the Br distribution on the same plane (Figure VI.3) follows 
a different, far more uniform pattern, which exhibits little flattening. This indicates that the 
permeability from core measurements is significantly smaller than that suggested from the S1A 
parameters. Predictions using the S3A parameters (see Table 6.9) are similar to the results from the 
run with S1A parameters because the hydraulic and transport properties are not very different in 
the two data sets (figure not shown, see Scientific Notebook YMP-LBNL-GSB-QH-1, p. 31-33). 
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Table 6.9. Input parameters for modeling the Phase 1A test of Busted Butte 
Parameters Source 
Test design, test implementation, tracers, 
injection rates, test duration, etc: 
CRWMS M&O 1999e, Section 6.8 
3-D grid (X:Y:Z = 3 m:3m:3m) SN: YMP-LBNL-GSB-QH-1, pages 5-35 
Data set S1A: UZ99 calibrated flow parameters 
in matrix of the ch1v and ch2v layers (porosity , 
permeability k,vanGenuchten andmparameters, 
residualsaturation Sr, watersaturation Sw, 
rock grain density s, tortuosity coefficient ) 
DTN: LB997141233129.001 
Data set S2A: Matrix porosity , permeability k, 
initial water saturation Sw, rock grain density s 
of the field samples 
DTNs: GS990308312242.007 and 
GS990708312242.008 
Data set S3A: VA97 calibrated flow parameters in 
matrix of the ch1v and ch2v layers (porosity , 
permeability k,vanGenuchten andmparameters, 
residualsaturation Sr, watersaturation Sw, 
rock grain density s, tortuosity coefficient ) 
DTN: LB971212001254.001 
Longitudinal dispersivity L = 0.1 m and transverse 
dispersivity T = 0.01 m in the matrix 
Scientific judgement in the absence of available 
data 
Br sorption coefficientKd = 0 m3/kg DTN: LB991220140160.019 (Boggs et al: 
1992, p: 3285) 
Br diffusion coefficientD0 = 2.03109 m2/s DTN: LB991220140160.019 (Cussler 1984, 
p: 147) 
Percolation flux: 1 mm/yr Scientific judgement 
The Br distribution in boreholes 1 and 4 for the S1A parameters (see Table 6.9) is shown in 
Figures VI.4 and VI.5, respectively. Both distributions exhibit similar symmetric, near-circular 
patterns, and indicate the dominance of capillary over gravitational forces. The extent of the tracer 
distribution is more limited in borehole 4 because of the smaller injection rate (1 mL/hr vs. 10 
mL/hr in Borehole 1). 
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6.10.2 Numerical Simulation of the Phase 1B Test 
6.10.2.1 Purpose 
The purpose of this modeling study was to predict the breakthrough curves of three tracers injected 
into the tsw39 layer. The three tracers were Br (nonsorbing), 2,6-difluorobenzoate (2,6-DFBA, 
nonsorbing, used to evaluate possible molecular size effects on transport) and Li+ (sorbing). Two 
parameter sets were used in the simulations: the S1A data set (see Section 6.10.1.1) and a modified 
S2B set, which included porosity and permeability data from core measurements, and all other 
parameters from the S1A data set (because no other measured parameters were available). Of the 
five tracers injected during the field experiment, only the three for which reliable data were available 
were simulated. 
6.10.2.2 Procedure and Layout 
In the Phase 1B field test, the tracers were injected into the lower portion of the Topopah 
Spring basal vitrophyre (Tptpv2 in the lithostratigraphic units; tsw39 in the UZ99 layers of 
the hydrogeologic units), which is a relatively low-permeability fractured rock. The design, 
configuration, and important dimensions of the Phase 1B test are shown in Figure VI.6, which 
depicts the injection/collection pair of boreholes 5 and 6. The layout of boreholes 7 and 8 is 
identical, and is not shown. 
Two such pairs were involved in the experiment, i.e., (a) boreholes 5 and 6, and (b) boreholes 7 and 
8. The tracer solution was injected at the location x = 1.30 m from the rock surface into boreholes 
5 and 7 at a rate of 10 mL/hr and 1 mL/hr, respectively. Injections began on May 12, 1998, and 
ceased on November 9, 1998 (borehole 5) and November 18, 1998 (borehole 7). Water samples 
from the collection boreholes 6 and 8 were obtained and analyzed regularly during the injection 
period. A detailed description of the experiment can be found in CRWMS M&O (1999e, Section 
6.8). 
6.10.2.3 Conceptual and Numerical Model 
The input parameters of flow and transport for the simulation of the Phase 1B test are listed in Table 
6.10. For this 3-D numerical study, the geologic model treated the domain as a homogeneous, 
unfractured rock matrix. Although this geologic layer is known to have fractures, the use of 
unfractured rock matrix as the domain model in the simulation was made possible by the system 
behavior during the injections, which did not show evidence of fracture flow. The DTN of the input 
and output files for this simulation is LB991220140160.010. 
6.10.2.4 Simulation Results and Discussion 
Breakthrough data (measured in borehole 6) for the three tracers discussed in Section 6.10.2.1 can 
be found in DTN: LA9909WS831372.001 and DTN: LA9909WS831372.002. As expected, peak 
concentrations are observed at x = 1.3 m from the rock face, i.e., directly beneath the injection point 
in borehole 5. 
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Table 6.10. Input parameters for modeling the Phase 1B test of Busted Butte 
Parameters Source 
Test design, test implementation, tracers applied, 
injection rates, sample collection duration, test 
duration, measured tracer concentration, etc: 
CRWMSM&O 1999e, Section6.8, and 
DTNs: LA9909WS831372.001 and 
LA9909WS831372.002 
3-D grid (XYZ = 4 m2 m2 m) SN: YMP-LBNL-GSB-QH-1, pp: 15-35 
S1A data set: UZ99 calibrated flow parameters 
in matrix of the ch1v and ch2v layers (porosity , 
permeability k,vanGenuchten andmparameters, 
residualsaturation Sr, watersaturation Sw, 
rock grain density s, tortuosity coefficient ) 
DTN: LB997141233129.001 
S2B data set: Matrix porosity , permeability k, 
initial water saturation Sw of the field samples 
DTNs: GS990308312242.007 and 
GS990708312242.008 
Longitudinal dispersivity L = 0.1 m and transverse 
dispersivity T = 0.01 m in the matrix 
Scientific judgement in the absence of available 
data 
Sorption coefficient of Br and 2,6-DFBA 
Kd = 0 m3/kg 
DTN: LB991220140160.019 (Boggs et al: 
1992, p: 3285, Benson and Bowman 1994, 
pp: 1123-1129) 
Sorption coefficient of Li+ Kd = 0.001 m3/kg CRWMS M& O (1999e, Table 37) 
Br diffusion coefficientD0 = 2.08109 m2/s 
Li+ diffusion coefficient D0 = 1.03109 m2/s 
DTN: LB991220140160.019 (Cussler 1984, 
p: 147) 
2,6-DFBA diffusion coefficientD0 = 7.61010 
m2/s 
DTN: LB991220140160.019 (Benson and 
Bowman 1994, p: 1125) 
Percolation flux: 1 mm/yr Scientific judgement 
No tracer breakthrough was detected in collection borehole 8 (CRWMS M&O 1999e, Section 
6.8) because of the small (1 mL/hr) injection rate into the overlying borehole 7. The measured 
concentrations indicated transport consistent with flow in the matrix (rather than in the fractures), 
which appeared to imbibe the injected solution quickly. 
The predicted Br breakthrough curves for the S1A and the S2B data sets at several locations 
in borehole 6 are shown in Figures VI.7 and VI.8, respectively. Because of symmetry about the 
x = 1:3 m axis, only the curves at x  1.3 m are shown in the figures. The figures show the 
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predicted relative pore-water tracer concentrations over time in the collection pads in borehole 
6. Visual inspection indicates that these results are in good agreement with the measured data 
(CRWMSM&O 1999e, Section 6.8.5.3.2). 
The differences between the two sets of Br curves and the even larger differences between the 
predicted saturation profiles (Figures VI.9 and VI.10 for the S1A and S2B data sets, respectively), 
were attributed to the significant differences in the values of porosity and permeability between the 
two data sets. For example, the S2B (measured) permeability of 3:061014 m2 was significantly 
larger than the S1A value of 5:46  1019 m2. 
The effect of solute size on dispersion can be evaluated by comparing the predicted breakthrough 
curves of 2,6-DFBA (Figure VI.11) and of Br (Figure VI.7) in borehole 6. The only difference 
between the two simulations was the value of the molecular diffusion coefficient D0, which was 
7:6  1010 m2/s for the large 2,6-DFBA molecule, and 2:08  109 m2/s for Br (Benson and 
Bowman 1994, p. 1125; Cussler 1984, p. 147). The higher relative concentrations of 2,6-DFBA 
at the same observation times resulted from lower diffusion into the matrix, as this process was 
hampered by the larger molecular size of 2,6-DFBA. These simulation results are consistent with 
laboratory studies of 3H and pentafluorobenzoate (PFBA) transport in columns (Hu and Brusseau 
1994). 
The breakthrough curves of the sorbing Li+ tracer follow a distinctively different pattern. This is 
caused by sorption, which results in maximum relative concentrations (in borehole 6) significantly 
lower than the ones observed in the non-sorbing Br and 2,6-DFBA. Predictions based on the 
measured Kd = 1 mL/g (CRWMS M&O 1999e, Table 36) in Figure VI.12 are consistently higher 
than the measured concentrations in CRWMSM&O (1999e, Section 6.8.5.3). In the same section, 
it is indicated that the Li+ Kd measurements are preliminary, and that more thorough sorption 
measurements are in progress. When Kd is increased to 2 mL/g, predictions are consistent with 
measurements (Figure VI.13). 
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6.11 3-D TRANSPORT SIMULATIONS 
In this section we study radionuclide transport in the entire Yucca Mountain system using largescale 
3-D grids. The development and features of the 3-D grids for this numerical modeling effort 
are documented in CRWMS M&O (1999h, Section 6) and further discussed in CRWMS M&O 
(1999d, Section 6.6). 
6.11.1 Climatic Conditions 
The three climatic scenarios investigated here are identical to those discussed in CRWMS M&O 
(1999d, Sections 6.1 and 6.6): present-day, monsoon and glacial. For each climatic scenario, a 
high, mean and low infiltration case was studied. The annual infiltration rates corresponding to 
each of the nine climatic cases are listed in Table 6.11, which also lists the DTN numbers of the 
data files involved in the EOS9 (V1.4, STN: 10007-1.4-00) flow simulations of each climatic case 
in CRWMS M&O (1999d, Section 6.6). 
6.11.2 Grids and Flow Simulations 
The input data files of the EOS9 (V1.4, STN: 10007-1.4-00, see Section 3) simulations listed in 
Table 6.11 were slightly modified. The modification involved a very minor rearrangement of the 
element order number, which moved the elements corresponding to the location of the potential 
repository near the bottom of the element file, and immediately above the top and bottom boundary 
elements of the 3-D domain. This modification was made because the release rate in the ensuing 
EOS9nT simulations was considered constant over time, a condition which necessitated treating 
the repository elements as internal boundary elements with time-invariant flow and concentration 
profiles. Moving them to the bottom of the element file made use of the ability of the TOUGH2 
family of codes to treat them (after a small change discussed at the end of this section) as inactive 
elements (i.e., elements that have time-invariant properties and conditions and do not contribute to 
mass and energy balances). 
Using the modified input files, all the EOS9 (V1.4, STN: 10007-1.4-00) simulations listed in Table 
6.11 were repeated to obtain the steady-state flow fields to be used in the EOS9nT simulations. The 
DTNs for the EOS9 input (modified) and output files is LB991220140160.011. A 2-D (plan view) 
of the grid at the potential repository level is shown in Figure 6.11.1. 
After each EOS9 simulation, the output files SAVEwere compared to those from the simulations 
using the unmodified grids to confirm that they were identical. Note that EOS9nT (V1.0, 
STN: 110065-1.11MEOS9NTV1.0-00) shares identical flow solution routines with EOS9, and 
confirmatory tests confirmed the identity of the flow solutions predicted by both EOS9 and EOS9nT 
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Table 6.11. Percolation fluxes (mm/year) for different climatic regimes and the corresponding 
EOS9 flow simulations used in the 3-D site scale radionuclide transport studies 
Value Present-Day Infiltration Glacial Infiltration Monsoon Infiltration 
Lower 1.2013 mm/yr 2.4042 mm/yr 4.5956 mm/yr 
bound DTN: LB990801233129.001 DTN: LB990801233129.007 DTN: LB990801233129.013 
Mean 4.5956 mm/yr 17.9614 mm/yr 12.3589 mm/yr 
DTN: LB990801233129.003 DTN: LB990801233129.009 DTN: LB990801233129.015 
Upper 11.2408 mm/yr 33.5185 mm/yr 20.1222 mm/yr 
bound DTN: LB990801233129.005 DTN: LB990801233129.011 DTN: LB990801233129.017 
: The percolation fluxes and the corresponding flow fields are from the DTNs at the same table location. 
(YMP-LBNL-GJM-3, p: 742). It was decided, however, to use the EOS9 module in the TOUGH2 
flow simulations to ensure complete compatibility with the results in CRWMS M&O (1999d, 
Section 6.6). For the EOS9nT simulations, the 3-D grids from the EOS9 simulations were used, 
after making the volume of the first repository element negative. This rendered all the following 
repository elements and the top and bottom boundary elements inactive, thus maintaining their 
properties and conditions constant throughout the simulations. 
6.11.3 Radionuclides Considered 
Three radionuclides are considered: 99Tc (non sorbing), 237Np (moderately sorbing) and 239Pu 
(strongly sorbing). Their properties are listed in Table 6.5. The radionuclides are released at the 
gridblocks corresponding to the location of the potential repository. For the large scale simulations, 
all the important members in the decay chains of 237Np and 239Pu were considered, according to 
the decay equations (Pigford et al: 1980) 
237Np !233 U !229 Th (Eq. 28) 
239Pu !235 U !231 Pa (Eq. 29) 
Note that only the most important members of the radioactive chain members are included in these 
equations, which omit daughters with short half lives. The properties of the daughters of 237Np 
and 239Pu are listed in Table 6.12. As alpha is the decay mode of all the members in the 237Np and 
239Pu chains,  = 0 (Equation 27) in all the simulations because the daughters are ejected from 
grain surfaces due to recoil (Faure 1977, pp: 288-289). 
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Figure 6.11.1. 2-D (plan view) of the UZ model grid design at the potential repository level 
(DTN: LB990701233129.001). 
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Table 6.12. Properties of the daughter products of radioactive decay in the transport simulations 
Radionuclide D0 (m2/s) T1=2 (years)y  = ln2 
T1=2 
(s) Decay modey 
233U 7.1231010 1.59105 1.38141013  
229Th 7.1231010 7.90103 2.78031012  
235U 6.081010 7.08108 3.10231017  
231Pa 6.081010 3.25104 6.75831013  
: DTN: LB991220140160.019 
y: From Lide (1992, pp: 11-122, 11-123, 11-124) 
6.11.4 Important Geologic Features 
As will be clearly shown in the ensuing Sections 6.12 through 6.16, the role of faults in the 3-D sitescale 
transport model is very important because faults provide fast pathways for the radionuclide 
migration to the water table . In the EOS9 and EOS9nT simulations, the faults are represented as 
thin vertical domains characterized by large permeabilities. More detailed description of the faults, 
their properties and their role in water flow can be found in CRWMS M&O (1999d, Sections 6.3 
and 6.6), CRWMSM&O (2000d, Sections 6.4) and CRWMSM&O (2000e, Sections 6.2 and 6.3). 
6.11.5 Transport Simulation Options 
All the 3-D simulations were conducted by using the De Hoog et al: (1982) implementation of the 
Laplace transform formulation of EOS9nT. This was selected because of the speed and accuracy 
of this formulation, its ability to provide information over the whole spectrum of the simulation 
period, and its ability to drastically reduce numerical diffusion. The resulting matrices were very 
well behaved, requiring no more that 10-15 conjugate gradient iterations to reduce residuals to 
below the 1011 level in a matrix of order of about 200,000. Thus, simulations were very fast and 
efficient, requiring 1,800-2,200 seconds of execution time to cover a simulation period of 1,000,000 
years. 
EOS9nT allows the simultaneous solution of the concentration profiles of any number of radionuclides. 
Thus, all three parents (99Tc, 237Np, 239Pu) were considered simultaneously in the runs. 
Similarly, and exploiting the fact that EOS9nT allows the tracking of any daughter products, the 
solutions for each of the parent radionuclides and its two daughters in the decay Equations 28 and 
29 were obtained simultaneously. In the perched water model# 2 and the no-perched water models, 
five radionuclides (99Tc, 237Np, 239Pu, 235U and 231Pa) were considered together. 
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6.12 3-D SIMULATIONS OF 99Tc TRANSPORT 
In this section we investigate the transport of 99Tc by means of EOS9nT 3-D site-scale simulations 
representing the entire UZ system of Yucca Mountain. Section 6.12 includes four subsections. 
In Section 6.12.1 we address the issue of the perched water model assumed in the simulations. 
In Section 6.12.2 we discuss the transport of the non-sorbing 99Tc for three levels of present-day 
infiltration. The results of this study are shown in Figures 6.12.1 to 6.12.17. In Section 6.12.3 we 
study the transport of 99Tc for three levels of monsoon infiltration (Figure 6.12.18). Finally, in 
Section 6.12.4 we study the transport of 99Tc for three levels of glacial infiltration (Figure 6.12.19). 
6.12.1 Perched-Water Model 
The grids, flow fields and conditions discussed in Section 6.11.2 correspond to the #1 conceptual 
model of perched water (CRWMS M&O 1999d, Section 6.2). This is the permeability barrier 
model, which uses the calibrated perched water parameters for fractures and matrix in the northern 
part of the model domain, and modified property layers (including the tsw38, tsw39, ch1z and ch2z 
layers) where the lower basal vitrophyre of the TSw is above the zeolites of the CHn. A detailed 
discussion of this perched water model can be found in CRWMSM&O (1999d, Section 6.2). 
6.12.2 99Tc Transport Under Present-Day Infiltration 
The DTNs of the input and output files for the three present-day infiltration scenarios are listed 
in Table 6.13. The input parameters used in the EOS9nT simulations of 3-D transport of the 
nonsorbing 99Tc are listed in Table 6.14. 
6.12.2.1 Breakthrough Curves 
As the 99Tc concentration in the potential repository and in the bottom boundary elements 
(corresponding to the water table ) remain constant over time, the breakthrough concept was based 
on the normalized release rate R, which is defined as 
R = 
Mass release rate at the groundwater boundary [MT1] 
Mass release rate at the potential repository [MT1] 
The normalized release rate at the potential repository in Figure 6.12.1 shows a very strong 
dependence on the infiltration regime. 
As the infiltration rate increases from low to mean, the t10 time, defined as the time at which R = 
0.1, decreases from about 10,000 years to about 300 years. The t50, defined as the time at which 
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Table 6.13. DTNs of input and output files of the 3-D site-scale transport simulations 
Item DTN 
EOS9 input & output files for 3-D UZ flow simulations 
(3 perched-water models, 3 infiltration 
regimes) 
LB991220140160.011 
EOS9nT input & output files for the 3-D transport 
simulations of radioactive solutes (#1 perchedwater 
model, present-day infiltration) 
LB991220140160.012 
EOS9nT input & output files for the 3-D transport 
simulations of radioactive solutes (#1 perchedwater 
model, monsoon infiltration) 
LB991220140160.013 
EOS9nT input & output files for the 3-D transport 
simulations of radioactive solutes (#1 perchedwater 
model, glacial infiltration) 
LB991220140160.014 
EOS9nT input & output files for the 3-D transport 
simulations of radioactive solutes (#2 perchedwater 
model, present-day infiltration) 
LB991220140160.015 
EOS9nT input & output files for the 3-D transport 
simulations of radioactive solutes (no-perchedwater 
model, present-day infiltration) 
LB991220140160.016 
EOS9nT input & output files for the 3-D transport 
simulations of radioactive colloids (#1 perchedwater 
model, present-day infiltration) 
LB991220140160.017 
R =0.5, decreases from about 45,000 years to about 4,000 years. Furtherincrease of infiltration to 
high present-day levels leads to a decrease of t10 to about 45 years, and of t50 to 1,000 years. The 
t10 and t50 of 99Tc, 237Np and 239Pu for three levels of the three climatic scenarios (present-day, 
monsoon and glacial) are listed in Table 6.15. It should be kept in mind that the term R is relative, 
and these findings are only important if the magnitude of the release rate at the potential repository 
becomes significant. 
Figure 6.12.1 also shows that the maximum attainable R increases with the infiltration rate. This is 
expected because lower infiltration results in lower velocities and longer travel times, thus higher 
radioactive decay. 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
101 102 103 104 105 106 
Time (years) 
Mean 
High 
Low 
Tc-99 Transport 
Present-Day Infiltration 
0.1 fraction line 
0.5 fraction line 
Figure 6.12.1. Normalized relative release R of 99Tcat the water table for varying present-day climatic scenarios 
(DTN: LB991220140160.012, data submitted with this AMR) 
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Table 6.14. Input parameters for the EOS9nT 3-D site-scale simulations of solute transport 
(#1 perched-water model) 
Parameters Source 
Transfer coefficientKi = 1 Conventionally used value 
Tortuosity  '  DTN: LB991220140160.019 and 
DTN: LAIT831341AQ96.001, 
Grathwohl (1998, pp: 2835), Farrell 
and Reinhard (1994, p: 64) 
Longitudinal dispersivity L = 1 m in the 
fractures, 0.1 m in the matrix 
Scientific judgement in the absence of 
available data 
Properties and characteristics of the geologic 
units, steady-state pressures, water 
saturations and flow fields 
Table 6.11 
Sorption coefficients Kd for Tc, Np, Pu, U, 
Th, Pa 
DTN: LB991220140160.019 and 
DTN: LAIT831341AQ96.001 
Fracture porosity  = 0.99 A reasonable estimate that allows limited 
sorption in the fractures. 
6.12.2.2 Transport-Controlling Features 
In the study of the radionuclide transport, we use the relative mass fraction XR, defined as 
XR = X
X0 
= C 
C0 
= CR 
where the subscript 0 denotes the value of the subscripted parameter in the water released from 
the potential repository. For mean present-day infiltration, the distribution of the 99Tc XR in the 
aqueous phase in the fractures and in the matrix in the gridblocks directly above the TSw-CHn 
interface (i.e., at the bottom of the TSw, corresponding to the tsw39 layer) is given in Figures 6.12.2 
through 6.12.9 for t = 100, 1,000, 10,000 and 100,000 years. Note that the XR distributions in 
Figures 6.12.2 through 6.12.9 do not correspond to a plan view from a horizontal cross section, but 
follow the uneven topography of the bottom of the tsw39 layer. The XR distributions of 99Tc in 
the aqueous phase in the fractures and in the matrix immediately above the water table at the same 
times are given in Figures 6.12.10 through 6.12.17. 
Fromtheinspectionofthesefigures, itbecomesapparentthattransportintheRTMisbothdominated 
and controlled by the faults. From the distribution of the fracture XR at the bottom of the TSw at 
a time t = 100 years (Figure 6.12.2), it is evident that, immediately above the TSw-CHn interface 
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Table 6.15. Radionuclide travel times to the water table 
Infiltration 99Tc 237Np 239Pu + 235U + 231Pa 
Level t10 t50 t10 t50 t10 t50 
PD Low 10,000 45,000 220,000 >1,000,000 600,000 >1,000,000 
PD Mean 300 4,000 10,000 120,000 40,000 250,000 
PD High 45 1,000 1,700 22,000 12,000 90,000 
My Low 920 3,500 17,000 70,000 60,000 280,000 
M Mean 50 1,000 1,400 21,000 14,000 75,000 
M High 25 400 650 9,000 8,500 50,000 
Gz Low 2,200 9,000 40,000 200,000 105,000 1,000,000 
G Mean 23 500 800 10,000 10,000 60,000 
G High 10 160 260 2,000 5,100 38,000 
: PD = Present-day; y: M = Monsoon ; z: G = Glacial 
(i.e., in the tsw39 layer), Splay G of the Solitario Canyon fault is the main transport-facilitating 
feature. Once contamination reaches the interface, it moves primarily in an easterly direction, 
moving with the draining water that hugs the downward sloping (in this direction) low-permeability 
TSw-CHn interface. The importance of this fault as a transport conduit is confirmed by the XR 
distribution in Figure 6.12.10. As shown in this figure, 99Tc begins to register a faint signature at 
the water table in the general location of the Solitario Canyon Splay G at the relatively early time 
of t = 100 years. 
The Ghost Dance fault splay identified in Figure 6.12.2 is the next most important transportfacilitating 
feature in the tsw39 layer, and is also important at the water table (Figure 6.12.10). It is 
remarkable that, though it facilitates downward migration, this fault as modeled appears to act as a 
barrier to the lateral migration of radionuclides. This is evidenced both at the bottom of the TSw 
(Figures 6.12.2 through 6.12.9), and also at the water table (Figures 6.12.12 through 6.12.17). 
The Sundance fault and the Drill Hole Wash fault are also important transport-facilitating geologic 
features. The Drill Hole Wash fault appears to act as a barrier to lateral radionuclide migration 
across it, while providing pathways for relatively fast transport to the water table . Even at t = 
100,000 years, very limited migration is observed across it in the tsw39 layer (Figures 6.12.8 and 
6.12.9) and at the water table (Figures 6.12.16 and 6.12.17). 
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Figure 6.12.2. Distribution of the relative mass fraction XR of 99Tc in the fractures of the tsw39 layer at t = 
100 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with this 
AMR). 
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Figure 6.12.3. Distribution of the relative mass fraction XR of 99Tc in the matrix of the tsw39 layer at t = 100 years 
for mean present-day infiltration (DTN: LB991220140160.012, data submitted with this AMR). 
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Figure 6.12.4. Distribution of the relative mass fraction XR of 99Tc in the fractures of the tsw39 layer at t = 
1,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
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Figure6.12.5.DistributionoftherelativemassfractionX R of 99Tcin thematrixofthetsw39layer att=1,000years 
for mean present-day infiltration (DTN: LB991220140160.012, data submitted with this AMR). 
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Figure 6.12.6. Distribution of the relative mass fraction XR of 99Tc in the fractures of the tsw39 layer at t = 
10,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
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Figure 6.12.7. Distribution of the relative mass fraction XR of 99Tc in the matrix of the tsw39 layer at t = 10,000 
years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with this 
AMR). 
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Figure 6.12.8. Distribution of the relative mass fraction XR of 99Tc in the fractures of the tsw39 layer at t = 
100,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
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Figure 6.12.9. Distribution of the relative mass fraction XR of 99Tc in the matrix of the tsw39 layer at t = 100,000 
years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with this 
AMR). 
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Figure 6.12.10. Distribution of the relative mass fraction XR of 99Tc in the fractures immediately above the 
groundwater at t = 100 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
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Figure 6.12.11. Distribution of the relative mass fraction XR of 99Tc in the matrix immediately above the groundwater 
table at t= 100 years for amean present-day infiltration (DTN: LB991220140160.012, data 
submitted with this AMR). 
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Figure 6.12.12. Distribution of the relative mass fraction XR of 99Tc in the fractures immediately above the 
groundwater at t = 1,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
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Figure 6.12.13. Distribution of the relative mass fraction XR of 99Tc in the matrix immediately above the groundwater 
table at t = 1,000 years for a mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
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Figure 6.12.14. Distribution of the relative mass fraction XR of 99Tc in the fractures immediately above the 
groundwater at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
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Figure 6.12.15. Distribution of the relative mass fraction XR of 99Tc in the matrix immediately above the groundwater 
table at t = 10,000 years for a mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
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Figure 6.12.16. Distribution of the relative mass fraction XR of 99Tc in the fractures immediately above the 
groundwater at t = 100,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
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Figure 6.12.17. Distribution of the relative mass fraction XR of 99Tc in the matrix immediately above the groundwater 
table at t = 100,000 years for a mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
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The main Ghost Dance fault does not play an important role in transport in the tsw39 layer, as the 
99Tc does not reach the fault at this level even after 100,000 years (Figures 6.12.8 and 6.12.9). This 
fault (identified in Figure 6.12.14) is more important at the water table , where it evidently acts 
as a barrier to transport across it while facilitating downward migration into the groundwater. Its 
presence in Figures 6.12.14 and 6.12.17 is denoted by the sharp contrast between the non-moving 
boundary of the concentration front along the fault and the adjacent uncontaminated rock mass. 
This boundary has the shape of the main Ghost Dance fault (see Figures 6.11.1) 
6.12.2.3 Transport Patterns 
Of particular interest is the emerging transport pattern, which indicates that radionuclide transport 
to the groundwater is faster in the southern part of the potential repository, where it is also areally 
concentrated. This appears to be counterintuitive and in conflict with expectations, based on the 
properties of the layers beneath the potential repository. It would be reasonable to expect that the 
general area of fastest, largest and most extensive transport would be in the northern part of the 
potential repository site, where the highly conductive fractures of the zeolitic CHz layers occur. 
Such an expectation appears to be supported by the 2-D studies of transport in vertical cross sections 
discussed in Section 6.9. 
The 3-D site-scale simulations indicate that the opposite occurs, i.e., radionuclide transport is 
significantlyslowerinthenorthern partdespitethepreponderanceofthezeolitic CHzhydrogeologic 
units. The relatively large permeability contrast between the matrix and the fractures in the CHz 
unit does not appear to lead to the expected fast fracture-dominated flow (compared to that in the 
vitric CHv units in the south) and to a correspondingly fast advective transport. 
There are four reasons for this transport pattern. The first reason is the infiltration and percolation 
distributions. A review of the infiltration pattern (Figure 6.12.18) at the surface, the percolation flux 
at the repository level (Figure 6.12.19) and the percolation flux at the groundwater level (Figure 
6.12.20) indicates that they closely reflect the transport patterns in Figures 6.12.2 through 6.12.17. 
Thus, the water flow pattern dictates the advective transport pattern. In the #1 perched-water model 
of these studies, the maximum water flow within the footprint of the potential repository is in its 
southern part. 
The presence of the highly conductive (a) Splay G of the Solitario Canyon fault and (b) Ghost 
Dance fault splay are the second reason (and related to the percolation patterns) for the dominance 
of the southern part of the potential repository as the pathway of transport, despite the vitric CHv 
layers having fewer fractures (than the overlying TSw) and acting as porous (rather than fractured) 
media (with relatively lower water velocities). The permeability of the fractures in the faults can be 
as high as hundreds of darcies (CRWMS M&O 2000a, Section 6; Bodvarsson et al. 1999, p: 15), 
i.e., orders of magnitude larger. The resulting fast advective transport is the reason for the transport 
pattern observed in Figures 6.12.2 through 6.12.17. 
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Figure 6.12.18. Mean present-day infiltration rates at the surface (CRWMS M& O 1999d, Section 6.6, DTN: 
LB990801233129.003). 
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Figure 6.12.19. Percolation fluxes at the potential repository level (CRWMS M& O 1999d, Section 6.6, DTN: 
LB990801233129.003). 
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Figure 6.12.20. Percolation fluxes at the water table level (CRWMS M& O 1999d, Section 6.6, DTN: 
LB990801233129.003). 
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This may be further facilitated by the contraction of the areal extent of the vitrified tuffs (the 
third reason), whose vertical distribution shows a funnel-type structure in the southern part of the 
potential repository. Thus, as depth from the potential repository increases, an increasing portion of 
the water flow occurs through the zeolites, in which the fractured dominated flow (and consequenty, 
transport) is fast. Figure 6.12.21 shows the areally diminishing extent of the vitrified tuffs with 
depth (DTN: MO9910MWDISMMM.003). In this figure, the zeolites are indicated by the yellow 
color in the layers of the CHn and PP hydrogeologic units, while the vitric tuffs are indicated by a 
purple color. Note also the contrast at the interface of the TSw and CHn units (layers tsw39 and 
ch1 in Figure 6.12.21). 
The fourth reason is the low-permeability zones at the TSw-CHn interface in the northern part of 
the potential repository in the #1 perched water model (CRWMS M&O, 1999d, Sections 6.2 and 
6.6). These zones are barriers to drainage, and lead to low water velocities and perched water 
bodies. Radionuclides move slowly through the perched water before reaching the underlying 
highly permeable zeolite fractures; hence the delay in transport. 
Note that the importance of faults and perched water bodies in transport are directly dependent on 
the underlying geologic and perched water conceptual models. In the simulations discussed in this 
section, the TSPA geologic model and the #1 perched water model (Table 6.13) were assumed. It 
is reasonable to expect that changing geologic and perched water models may lead to substantially 
different results, given the sensitivity of transport to these geologic features. 
The fourth reason is the low-permeability zones at the TSw-CHn interface in the northern part of 
the potential repository in the #1 perched water model (CRWMS M&O, 1999d, Sections 6.2 and 
6.6). These zones are barriers to drainage, and lead to low water velocities and perched water 
bodies. Radionuclides move slowly through the perched water before reaching the underlying 
highly permeable zeolite fractures; hence the delay in transport. 
Note that the importance of faults and perched water bodies in transport are directly dependent on 
the underlying geologic and perched water conceptual models. In the simulations discussed in this 
section, the TSPA geologic model and the #1 perched water model (Table 6.13) were assumed. It 
is reasonable to expect that changing geologic and perched water models may lead to substantially 
different results, given the sensitivity of transport to these geologic features. 
6.12.2.4 Transport Processes and Mechanisms 
Theimportance of fracturesinthe transport becomes evidentin Figure 6.12.2, which shows theareal 
distribution of the 99Tc XR in the aqueous phase in the tsw39 layer at t = 100 years. Compared 
to the distribution of XR in the matrix (Figure 6.12.3), which shows practically no 99Tc presence, 
it is evident that fractures are the main pathways of transport at this relatively early stage. Figure 
6.12.2 clearly shows distinctive transport patterns corresponding to the geologic features discussed 
in Section 6.12.2.2. 
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Figure 6.12.21. Mineralogy model plots of % zeolites (DTN: MO9910MWDISMMM.003). Zeolites are indicated 
by the purple color, and vitric tuffs are denoted by the yellow color. 
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As time progresses, the same pattern persists, although the differences in the XR distribution 
between the fractures and the matrix become less pronounced with time. This is evidenced at t = 
1,000 years (Figures 6.12.4 and 6.12.5), where the matrix 99Tc XR is significant, but substantially 
lower than the fractureXR of 99Tc. It is obvious that the 99TcXR distribution in the matrix follows 
the XR distribution in the fractures, indicating that diffusion from the fractures into the matrix 
is the main mechanism for the 99Tc presence in the matrix. The distinctive transport patterns, 
corresponding to identifiable geologic features, are now even more pronounced. At t = 10; 000 
years, XR is still higher in the fractures (Figure 6.12.6) than in the matrix (Figure 6.12.7), but 
the differences are smaller. Finally, at t = 100; 000 years, XR differences between the fractures 
(Figure 6.12.8) and the matrix (Figure 6.12.9) can be barely distinguished by visual inspection of 
the figures. 
The XR distribution immediately above the water table further attests to the importance of 
fractures for transport. For mean present-day infiltration, the fracture XR immediately above the 
water table shows evidence of measurable transport at t = 100 years (Figure 6.12.10), while the 
corresponding matrix XR shows no evidence of 99Tc (Figure 6.12.11). At t = 1; 000 years, XR is 
significant in fractures and denotes the geological features that facilitate transport (Figure 6.12.12), 
but the corresponding matrix XR is just beginning to show faint signs of 99Tc presence (Figure 
6.12.13). 
At t = 10,000 years, the differences between the matrix and the fracture XR (Figures 6.12.14 and 
6.12.15) lessen. The general observation is that the matrixXR distribution follows the same pattern 
as fracture XR distribution, but lags in time. Their patterns confirm the earlier observation that 
matrix diffusion from the fractures into the matrix is the main mechanism for the 99Tc presence 
in the matrix. The distinctive transport patterns, corresponding to the faults discussed in Section 
6.12.2.2, are now even more pronounced. At t = 100; 000 years, only small XR differences 
between the fractures (Figure 6.12.16) and the matrix (Figure 6.12.17) persist. 
6.12.2.5 Comparison to the Semianalytical 2-D FRACL Predictions 
The fracture XR distributions above the water table at t = 1,000 and t = 10,000 years in Figures 
6.12.12 and 6.12.14 provide confirmation of the travel times predicted by the 2-D semianalytical 
solutions in Section 6.9. From Figures V.1, V.7, V.13 and V.19 (see Attachment V), it appears 
that, for mean present-day infiltration, 99Tc transport through the fractures and matrix (but not 
accounting for faults) takes over 1,000, but less than 10,000 years, to reach the water table . 
The fracture XR in Figures 6.12.12 and 6.12.14 are consistent with this prediction. Figure 6.12.12 
shows limited 99Tc presence in the fractures, all of which is attributed to transport through the 
faults. Figure 6.12.12 shows that the Splay G of the Solitarion Canyon Fault is the earliest and 
most significant contributor of 99Tc in the fractures at the water table. At t = 10,000 years (Figure 
6.12.14), the fracture XR shows an extensive distribution, which is consistent with 99Tc arrivals 
through the bulk of the fractures in addition to contributions from faults. 
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Note that the observation of faster transport in the southern part of the potential repository from the 
EOS9nT 3-D site-scale simulations does not contradict the FRACL 2-D predictions, which appear 
to indicate faster transport in the northern part (despite the presence of permeability conditions that 
lead to the formation of perched water bodies). There are several reasons for this. 
TheFRACLpredictionsandtheEOS9nTpredictionsdonotdescribethesameproblem. TheFRACL 
problems involve a thin 2-D cross section at a representative location. The FRACL semianalytical 
model cannot account for 3-D processes (such as flow diversion, focusing, and advective transport 
from outside its narrow 2-D domain) and the effects of faults. The FRACL and EOS9nT results 
would be comparable if the same limited 2-D domain were simulated for the same infiltration rate. 
In the dual permeability approach of the EOS9nT simulations, the matrix and fracture components 
of a fractured rock are represented by a fracture subdomain and a matrix subdomain. As simulated, 
theFRACLresultsapproximate transportataverticalcolumnof theEOS9nT3-Ddomain(involving 
a singlefracture and asingle matrix system) at the locations of Cross Sections 1, 2 and 3 (see Section 
6.5). Note that the two are not fully comparable because the effects of 3-D flow and transport in the 
EOS9nT domain columns and the areal differences of infiltration and percolation (Figures 6.12.18 
to 6.12.20). 
FRACL describes transport in the fracture-matrix system of Cross Sections 1, 2 and 3 (i.e., 2-D 
domains such as that in Figure 6.9.1) without accounting for the 3-D effects of the faults. It is these 
fault effects that are first noticed in the transport patterns of Figures 6.12.2 to 6.12.17, from which 
it is not possible to separate the transport component through the bulk matrix and fractures and 
the effects of lateral advective transport. Thus, Figures 6.12.1 to 6.12.17 do not provide sufficient 
information to ascertain that, excluding the effects of the faults, bulk transport through the fractures 
and matrix is faster in the southern part of the potential repository. 
6.12.3 99Tc Transport Under Monsoon Infiltration 
The DTNs of the input and output files for the three monsoon infiltration scenarios are listed in 
Table 6.13. The monsoon infiltration rate is higher than that for present-day infiltration of the same 
level (Table 6.11). The simulation results are consistent with the observations made in Section 
6.12.2. 
The higher infiltration rates result in lower t10 and t50 values (Table 6.15) than those for presentday 
infiltration. Thus, for low, mean, and high monsoon infiltration, the t10 is 920, 50 and 15 
years, respectively (Figure 6.12.22). For the same infiltration regimes, the corresponding t50 is 
3,500, 1,000, and 400 years. These times are significantly smaller than the ones for the presentday 
infiltration scenario (Figure 6.12.1), indicating faster transport through the system and earlier 
appearance of 99Tc at the water table . 
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Because transport is faster than under present-day infiltration, travel times to the water table are 
shorter and thus the amount of 99Tc lost to radioactive decay is smaller. This is evident in Figure 
6.12.22, in which the maximum attainable R values are shown (a) to increase with the infiltration 
rate and (b) to be higher and closer to each other than those for present-day infiltration (Figure 
6.12.1). 
6.12.4 99Tc Transport Under Glacial Infiltration 
The DTNs of the input and output files for the three glacial infiltration scenarios are listed in Table 
6.13. Thehigh and mean glacial infiltration are higher than the present-day and monsoon infiltration 
of the same level (Table 6.11), and result in lower t10 and t50 values (Table 6.15). 
Figure 6.12.23 shows that the t10 values for high and mean glacial infiltration are only 10 
(extrapolated from the figure) and 23 years, respectively, while the corresponding t50 values are 160 
and 500 years. As in the case of monsoon infiltration (Figure 6.12.18), the maximum attainable R 
for high and mean glacial infiltration is almost 1, indicating fast transport through the 3-D system. 
The t10 and t50 values for low glacial infiltration are 2,200 and 9,000 years respectively. 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
101 102 103 104 105 106 
Time (years) 
Mean 
High 
Low 
Tc-99 Transport 
Monsoon Infiltration 
0.1 fraction line 
0.5 fraction line 
Figure 6.12.22. Normalized relative release R of 99Tc at the water table for varying monsoon climatic scenarios 
(DTN: LB991220140160.013, data submitted with this AMR). 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
101 102 103 104 105 106 
Time (years) 
Mean 
High 
Low 
Tc-99 Transport 
Glacial Infiltration 
0.1 fraction line 
0.5 fraction line 
Figure 6.12.23. Normalized relative release R of 99Tc at the water table for varying glacial climatic scenarios 
(DTN: LB991220140160.014, data submitted with this AMR). 
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6.13 3-D TRANSPORT OF 237Np AND ITS DAUGHTERS 
In this section we investigate the transport of 237Np by means of EOS9nT 3-D site-scale simulations 
of the entire UZ system of Yucca Mountain. Section 6.13 includes three subsections. 
In Section 6.13.1 we discuss the transport of the moderately-sorbing 237Np and its daughters for 
three levels of present-day infiltration. The results of this study are shown in Figures 6.13.1 to 
6.13.2, and in Figures VII.1 to VII.24 of Attachment VII. In Section 6.13.2 we study the transport 
of 237Np for three levels of monsoon infiltration (Figure 6.13.3). Finally, in Section 6.13.3 we study 
the transport of 237Np for three levels of glacial infiltration (Figure 6.13.4). 
6.13.1 Transport of 237Np and its Daughters Under Present-Day Infiltration 
The grids, flow fields and conditions discussed in Section 6.11.2 corresponded to the #1 conceptual 
model of perched water(CRWMSM&O1999d, Sections 6.2 and 6.6) and are used in the simulation 
of all infiltration regimes. The parameters used in the EOS9nT simulations of 3-D transport of the 
moderately sorbing 237Np are listed in Table 6.14. The DTN of the input and output files for the 
three present-day infiltration scenarios is DTN: LB991220140160.012 (Table 6.13). 
6.13.1.1 Breakthrough Curves 
The moderate sorption of 237Np results in retardation of its transport through the UZ system, as the 
normalized release rate R at the water table in Figure 6.13.1 indicates. A comparison of this figure 
to that for the non sorbing 99Tc (Figure 6.12.1) reveals a drastically different pattern. Thus, the 
moderate sorption of 237Np is sufficient to effect a large increase in t10 and t50 compared to those 
for the non-sorbing 99Tc (Table 6.15). 
Increased infiltration rate leads to faster transport and shorter travel times to the repository. When 
infiltration increases from mean to high, t10 and t50 are reduced to 1,700 and 22,000 years, 
respectively. Reduction of infiltration to the low present-day level results in analogous increase of 
t10 and t50 to 220,000 and over 1,000,000 years, respectively. 
Because of significant retardation, the maximum attainable R varies over a larger value range and 
does not necessarily reach a plateau within the simulation period. At t = 1,000,000 years, R for 
mean and low infiltration is 0.86 and 0.42, respectively, and the maximum possible values for either 
infiltration are not yet reached. At the same time, the R for high infiltration is approaching its 
maximum at R = 0:95. 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
101 102 103 104 105 106 
Time (years) 
Mean 
High 
Low 
Np-237 Transport 
Present-Day Infiltration 
0.1 fraction line 
0.5 fraction line 
Figure6.13.1.NormalizedrelativereleaseRof 237Npatthewatertableforvaryingpresent-day climaticscenarios 
(DTN: LB991220140160.012, data submitted with this AMR). 
6.13.1.2 Daughter Contributions 
The effect of daughter generation on radionuclide transport was investigated by accounting for the 
contributions of 237Np and its two daughters (233U and 229Th) to the release rate at the water table 
. The relative flux fraction MR of each member of the chain, defined as 
MR = 
Flux of the member of the237Np chain at the water table 
Sum of fluxes of all members of the 237Np chain at the water table 
; 
is shown in Figure 6.13.2. The MR of both 233U and 229Th increase monotonically with time, 
and at t = 1,000,000 years, they reach values of 0.02 and 105, respectively. Contributions of the 
daughters are obviously rather insignificant and can be safely ignored. 
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10-9 
10-8 
10-7 
10-6 
10-5 
10-4 
10-3 
10-2 
10-1 
100 
101 102 103 104 105 106 
Time (years) 
Mean Present-day Infiltration 
Np-237 
U-233 
Th-229 
Figure 6.13.2. Relative flux fractions MR of the members of the 237Np ! 233U ! 229Th in the release at 
the water table over time for a mean present-day infiltration (DTN: LB991220140160.012, data 
submitted with this AMR). 
6.13.1.3 Transport Mechanisms and Patterns 
Theimportance of fractureson the 237Np transport becomesevidentinFigure VII.1(see Attachment 
VII), which shows the areal distribution of XR (see Section 6.12.2.2) in the aqueous phase in the 
fractures immediately above the TSw-CHn interface (i.e., in the tsw39 layer) at t = 100 years 
(under mean present-day infiltration). The contrast with the distribution of XR in the aqueous 
phase of the matrix (Figure VII.2), which shows no discernible difference from the backgroundXR 
= 0, is dramatic. 
Of particular interest is the distribution of the relative sorbed or filtered concentration FR [ML3], 
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defined as 
FR = F 
X0 
; 
where X0 is the species mass fraction in the water released from the potential repository. Figure 
VII.3 shows a sizable 237Np FR distribution, which has an areal extent significantly larger than 
that of the fracture XR at the same time, and denotes geologic features (i.e., the section of the Drill 
Hole Wash fault shown in Figure VII.3) that do not appear in the fracture XR (Figure VII.1). 
Figures VII.1 through VII.3 indicate the efficiency of the matrix as a 237Np sink. The small 
amounts of 237Np that diffuse from the fractures into the matrix are immediately sorbed and are 
thus removed from the matrix aqueous phase. The XR in the matrix aqueous phase shows no 
discernible signs of 237Np presence because its magnitude is so low that it cannot be differentiated 
from the zero backgound level when using a linear XR scale. The logarithmic scale of relative 
sorbed concentrations in Figure VII.3 shows the extent of 237Np presence in the matrix. 
Figures VII.4 to VII.6 show the fracture XR distribution, the matrix XR, and the matrix FR in the 
tsw39 layer of 237Np at t = 1,000 years. Note the very large differences in the areal extents of the 
237Np footprints in these three figures. The effect of the Drill Hole Wash fault, clearly denoted 
in its entirety by the FR distribution in Figure VII.6, is absent from the fracture and matrix XR 
distributions in Figures VII.4 and Figures VII.5, respectively. 
The fracture XR, matrix XR, and the matrix FR at t = 10,000 years are shown in Figures VII.7 to 
VII.9, respectively; the distribution of these parameters at t = 100,000 years is shown in Figures 
VII.10 to VII.12. Compared to the fracture XR, matrix XR levels appear to be particularly low. 
This is caused by sorption onto the matrix. 
From Figures VII.1 to VII.12, we deduce that matrix diffusion from the fractures into the matrix, 
and subsequent sorption onto the matrix grains are the main mechanisms for 237Np removal from 
the fractures and transport retardation. As the relative sorbed concentration distributions indicate, 
matrixdiffusion leadstotheremovalofsubstantialcontaminantmassfrom thefastflowingfractures. 
The fracture XR of 237Np is substantially lower than that of 99Tc at the same locations and times 
(Section 6.12) and further confirms this observation. 
The XR distribution immediately above the water table provides another indication of the 
importance of fractures. For mean present-day infiltration, the fracture and matrix XR immediately 
above the water table show practically no signs of 237Np at t = 100 years (Figures VII.13 and 
VII.14), but the corresponding matrix FR (Figure VII.15) is easily detectable and demonstrates the 
effectiveness of sorption in radionuclide removal from the solution. At t = 1,000 years, the XR 
distribution in the fractures (Figure VII.16) and in the matrix (Figure VII.17) remain practically 
unchanged from those at t = 100 years (Figures VII.13 and VII.14). On the other hand, the matrix 
FR in Figure VII.18 exhibits large values, and clearly identifies all the transport-facilitating faults 
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discussed in Section 6.13.2.2. 
The fracture XR, matrix XR and matrix FR distributions of 237Np at t = 10,000 years are shown in 
Figures VII.19 to VII.21; the same distributions at t = 100,000 years are shown in Figures VII.22 
to VII.24. The fracture XR is beginning to register above background at t = 10,000 (Figure VII.19) 
and reaches a significant level at t = 100,000 years (Figure VII.22). The matrix XR has at last 
become differentiable from the background at t = 100,000 (Figure VII.23). The matrix FR at t = 
10,000 years and t = 100,000 years in Figures VII.21 and VII.24, respectively, show that 237Np is 
sorbed onto the rocks over a large area, which increases over time. Comparison of the XR (matrix 
and fracture) to the matrix FR distributions provides further evidence of the efficiency of the matrix 
as a 237Np sink, which leads to the significant retardation (over that of the non-sorbing 99Tc, see 
Figure 6.12.1) indicated in Figure 6.13.1. 
6.13.1.4 Transport-Controlling Features 
Review of Figures VII.1 through VII.24 (see Attachment VII), and comparison tothe corresponding 
99Tcfigures(Figures6.12.2through6.12.17)indicatethattransportisbothdominatedandcontrolled 
by the same faults identified and discussed in Section 6.12.1.2. Thus, Splay G of the Solitario 
Canyon fault is the main transport-facilitating feature and leads to the early appearance of 237Np in 
the tsw39 layer and at the water table. Once 237Np reaches the TSw-CHn interface, it is transported 
along the eastward-sloping and relatively impermeable interface with the draining water. 
The Ghost Dance fault splay appears to play a more significant role in 237Np transport than in the 
99Tc transport. This fault is very clearly identified in Figures VII.1, VII.4, VII.7 and VII.22 as a 
conduit of very fast transport to the water table . The Sundance fault is the next fault (in terms 
of time at which contributions to transport become significant), followed by the Drill Hole Wash 
fault, and finally the main Ghost Dance fault. These faults appear to act as barriers to the lateral 
migration of radionuclides across them, as the fracture and matrix XR indicate. Note, however, 
that the sorbed 237Np distributions straddle the faults, especially at long times. Of interest is the 
observation that at t  10,000 years, the FR distribution appears to have reached the main Solitario 
Canyon fault both in the tsw39 layer and at the water table . This can have important implications 
in the long-term transport of 237Np, given its long half-life (2:14  106 years). 
As in the case of 99Tc transport, radionuclide transport to the groundwater is faster in the southern 
part of the potential repository, where it is also areally concentrated. This is caused by (a) the 
infiltration and percolation patterns, (b) the fast conduit to transport provided by the faults (and 
especially the Splay G of the Solitario Canyon fault and the Ghost Dance fault splay); (c) the 
permeability barriers to flow (and, consequently, to transport) in the northern part, where perched 
water bodies occur and through which water is forced to flow slowly; and (d) the distribution of the 
vitric CHv layers. A detailed discussion on the subject of transport pattern can be found in Section 
6.12.2.3. 
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6.13.1.5 Comparison to the 99Tc Transport 
The obvious difference between the 99Tc and the 237Np transport is sorption. This results in (a) the 
universally lower (than 99Tc) concentrations of 237Np in the fractures and in the matrix at the same 
times, and (b) the slower breakthroughs indicated by Figures VII.13 through VII.24 and Table 6.15. 
6.13.1.6 Comparison to the Semianalytical 2-D FRACL Predictions 
The fracture XR distributions of 237Np above the water table at t = 10,000 and t = 100,000 years in 
Figures VII.19 and VII.22 (obtained from the EOS9nT simulations) are generally consistent with 
the travel times predicted by the 2-D semianalytical FRACL solutions in Section 6.9. Figures V.2 
and V.8 (see Attachment V) show that, for mean present-day infiltration, 237Np transport through 
the fractures and matrix (but not accounting for faults) in Cross Sections 1 and 2 (See Section 6.5) 
takes over 10,000 years, but less than 100,000 years, to reach the water table. Figure VII.19 shows 
only limited, fault-related transport at 10,000 years. At t = 100,000 years, Figure VII.22 shows 
a fracture XR distribution consistent with 237Np arrivals through the bulk of the fractures (i.e., 
fractures not related to the faults), in addition to the earlier fault contributions. 
The transport of 237Np in Column 3 (Figures V.14 and V.20) does not appear to be consistent with 
the results of the 3-D simulations. The main reason for this apparent discrepancy is the inability of 
the 2-D FRACL semianalytical model to account for 3-D effects on flow and transport. A detailed 
discussion on the subject can be found in Section 6.12.2.5. Note that caution should be exercized 
in comparing the EOS9nT and FRACL results for the reasons discussed in Section 6.12.2.5. 
6.13.2 237Np Transport Under Monsoon Infiltration 
The DTN of the input and output files for the three monsoon infiltration scenarios is DTN: 
LB991220140160.013 (Table 6.13). The higher monsoon infiltration rates (compared to those 
in present-day regimes, see Table 6.11) lead to the faster transport indicated in Figure 6.13.3, 
compared to that shown in Figure 6.13.1. The corresponding shorter t10 and t50 values are listed 
in Table 6.15. 
The t10 for low, mean, and high monsoon infiltration is 17,000, 1,400, and 650 years, respectively. 
The corresponding t50 are 70,000, 21,000, and 9,000 years, respectively. These times are 
significantly lower than the ones for the present-day infiltration scenario, as the faster transport 
through the system would warrant. Because transport is faster than under present-day infiltration, 
radioactive decay of the released 237Np has a less pronounced effect in the reduction of the R at a 
given time. 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
101 102 103 104 105 106 
Time (years) 
Mean 
High 
Low 
Np-237 Transport 
Monsoon Infiltration 
0.1 fraction line 
0.5 fraction line 
Figure 6.13.3. Normalized relative release R of 237Np at the water table for varying monsoon climatic scenarios 
(DTN: LB991220140160.013, data submitted with this AMR). 
6.13.3 237Np Transport Under Glacial Infiltration 
The DTN of the input and output files for the three glacial infiltration scenarios is DTN: 
LB991220140160.014 (Table 6.13). The high and mean glacial infiltration infiltration rates are 
the highest in the three regimes (Table 6.11) and result in the breakthrough pattern shown in Figure 
6.13.4. The corresponding shorter t10 and t50 values are listed in Table 6.15. 
The t10 for low, mean, and high glacial infiltration is 40,000, 800 and 260 years, respectively. The 
corresponding t50 are 200,000, 10,000, and 3,000 years, respectively. For high and mean glacial 
infiltration, the t10 and t50 times are the shortest in the three infiltration regimes. 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
101 102 103 104 105 106 
Time (years) 
Mean 
High 
Low 
Np-237 Transport 
Glacial Infiltration 
0.1 fraction line 
0.5 fraction line 
Figure 6.13.4. Normalized relative release R of 237Np at the water table for varying glacial climatic scenarios 
(DTN: LB991220140160.014, data submitted with this AMR). 
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6.14 3-D TRANSPORT OF 239Pu AND ITS DAUGHTERS 
In this section we investigate the transport of 239Pu by means of EOS9nT 3-D site-scale simulations 
of the entire UZ system of Yucca Mountain. Section 6.14 includes two subsections. 
In Section 6.14.1 we discuss the transport of the strongly sorbing 239Pu and its daughters for three 
levels of present-day infiltration. The results of this study are shown in Figures 6.14.16.14.2, 
and in Figures VIII.1 to VIII.24 of Attachment VIII. In Section 6.14.2 we study the transport of 
239Pu and its daughters for three levels of monsoon infiltration and three levels of glacial infiltration 
(Figures 6.14.3 to 6.14.6). 
6.14.1 Transport of 239Pu and its Daughters Under Present-Day Infiltration 
The grids, flow fields, and conditions discussed in 6.11.2 corresponded to the #1 conceptual model 
of perched water (CRWMSM&O 1999d, Sections 6.2 and 6.6) and are used in the simulation of all 
infiltrationregimes. TheparametersusedintheEOS9nTsimulationsof 3-Dtransportofthestrongly 
sorbing 239Pu are listed in Table 6.14. The DTN of the input and output files for the three presentday 
infiltration scenarios is DTN: LB991220140160.012 (Table 6.13). The distribution coefficients 
Kd of the 239Pu daughters (i.e., 235U and 231Pa) can be found in DTN: LAIT831341AQ96.001 (see 
Table 6.14). 
6.14.1.1 Breakthrough Curves 
The normalized release rate R at the water table for present-day infiltration is shown in Figure 
6.14.1. If the contributions of the daughter products (i.e., 235U and 231Pa) are not accounted for, 
R does not reach the 0.1 level even after 1,000,000 years of continuous release. This is due to the 
strong sorption of 239Pu. 
The picture changes dramatically, however, if the daughter contributions are included in the 
computations. The R of the sum of the parent and daughter contributions exhibits a delayed 
breakthrough. Thus, t10 is 12,000, 40,000, and 600,000 years for high, mean, and low present-day 
infiltration. The corresponding t50 values are 90,000, 250,000, and over 1,000,000 years (Table 
6.15). Given the long half life of 239Pu and the much longer half life of 235U (see Tables 6.5 and 
6.12), the daughter contributions are very important and cannot be neglected with impunity under 
the high infiltration regime. The daughter contributions are even more important under the wetter 
monsoon and glacial conditions (see Figures 6.13.3 to 6.13.6). 
6.14.1.2 Daughter Contributions 
Therelativefluxfractions MR forpresent-dayinfiltrationareshowninFigure6.14.2. Theinteresting 
realization is that the 239Pu contribution to the release rate starts declining rapidly after 1,000 years, 
and 235Uis by farthe dominantspecies aftert 10,000 years. Lowerinfiltration ratesareassociated 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
101 102 103 104 105 106 
Time (years) 
Pu-239 Transport 
Present-Day Infiltration 
0.1 fraction line 
0.5 fraction line 
Pu-239 only 
Mean infiltration 
High infiltration 
Low infiltration 
Pu-239+U-235+Pa-231 
Mean infiltration 
High infiltration 
Low infiltration 
Figure6.14.1.NormalizedrelativereleaseRof 239Puatthewatertableforvaryingpresent-day climaticscenarios 
(DTN: LB991220140160.012, data submitted with this AMR). 
with the earlier emergence of 235Uas the dominant species released atthe water table . For example, 
at t = 10,000 years, water table releases consist mostly (over 95%) of 235U under low present-day 
infiltration conditions. This is expected because, under a low infiltration regime, less 239Pu 
reaches the water table on account of strong sorption. Note that the 231Pa contribution is negligible 
because of the very long half life of 235U. 
6.14.1.3 Transport Mechanisms and Patterns 
The importance of fractures on the 239Pu transport is evident in Figure VIII.1 (see Attachment 
VIII), which shows the areal distribution of XR in the aqueous phase in the fractures in the tsw39 
layer at t = 100 years (under mean present-day infiltration). The contrast with the distribution of 
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10-9 
10-8 
10-7 
10-6 
10-5 
10-4 
10-3 
10-2 
10-1 
100 
101 102 103 104 105 106 
Time (years) 
Present-day Infiltration 
Pu-239 
Mean 
High 
Low 
Pa-231 
Mean 
High 
Low 
U-235 
Mean 
High 
Low 
Figure 6.14.2. Relative flux fractions MR of the members of the 239Pu ! 235U ! 231Pa decay chain 
in the release at the water table over time for varying present-day climatic conditions (DTN: 
LB991220140160.012, data submitted with this AMR). Note that the 231Pa contribution is negligible 
because of the very long half life of 235U. 
XR in the matrix (Figure VIII.2), which shows no discernible difference from the background XR 
= 0, is dramatic. The same difference between the XR in the fractures and matrix in the tsw39 
layer is observed at t = 1,000 years (Figure VIII.4 and VIII.5), t = 10,000 years (Figure VIII.7 and 
VIII.8), and t = 100,000 years (Figure VIII.10 and VIII.11). 
As inthe case of 237Np, the distribution of matrix FR at t = 100 years showsa sizable 239Pu presence 
sorbed onto the matrix of the tsw39 layer (Figure VIII.3). The area of non-zero FR is significantly 
larger than that of the fracture XR footprint at the same time. The same pattern persists as time 
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increases (see Figures VIII.6, VIII.9 and VIII.12), with the fracture XR distribution showing only 
slight expansion and the FR distribution continuously expanding. 
The transport pattern is similar above the water table (Figures VIII.13 to VIII.24), where (a) 
the fracture XR shows faint signs of 239Pu presence (in the vicinity of Splay G of the Solitario 
canyon fault distribution), which remains practically unchanged over time, (b) the matrix XR does 
not register any measurable 239Pu presence (for a linear XR scale), and (c) the footprint of the 
measurable FR distribution keeps expanding. 
Figures VIII.1 through VIII.24 indicate the efficiency of the matrix as a 239Pu sink. 239Pu diffusion 
from the fractures into the matrix is followed by immediate sorption and thus removal from the 
matrix aqueous phase. The XR in the matrix aqueous phase shows no discernible signs of 239Pu 
presence because of the very strong sorption of 239Pu. The logarithmic scale of the FR distributions 
allows delineation of the extent of the measurable 239Pu presence sorbed onto the matrix. 
6.14.1.4 Transport-Controlling Features 
Review of Figures VIII.1 through VIII.24 (see Attachment VIII) and comparison to the corresponding 
237Np figures (Figures VII.1 to VII.24) indicate that transport is both dominated by the faults 
identified and discussed in Sections 6.12.1.2 and 6.12.1.3. Thus, Splay G of the Solitario Canyon 
fault is the main transport-facilitating feature and leads to the early appearance of 239Pu in the tsw39 
layer and above the water table . 
The Ghost Dance fault splay appears to play a significant role. This fault is very clearly identified 
in Figures VIII.7 and VIII.10 as a conduit of very fast transport to the water table . The Sundance 
fault is the next fault (in terms of time at which contributions to transport become significant). 
The Drill Hole Wash fault does not appear to have any contributions in the fracture or matrix XR 
distributions at any time in either the tsw39 layer or at the water table , but is discernible in the FR 
distributions at late times. 
The main Ghost Dance fault becomes discernible in the FR distributions at t  10,000 in tsw39, 
and marginally so above the water table at t = 100,000. Note that at t  10,000 years, the FR 
distribution appears to have reached the main Solitario Canyon fault both in the tsw39 layer and 
above the water table . 
6.14.1.5 Comparison to the 99Tc and 237Np Transport 
The obvious difference between the transport of 239Pu and those of 99Tc and 237Np is the strong 
sorption of 239Pu. This results in (a) 239Pu relative concentrations XR in the fractures and the 
matrix that are universally lower than those for 99Tc (Figures 6.12.2 to 6.12.17) and 237Np (Figures 
VII.1 to VII.24 in Attachment VII) at the same times, and (b) no arrival at the water table of 
significant 239Pu amounts even after t = 100,000 years (see Figure 6.14.1). Note that the matrixXR 
of 239Pu (at any location and time) does not show any discernible difference from the background 
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zero concentration. 
The strong sorption of 239Pu results in fracture and matrix XR distributions that do not change 
significantly over time. This is observed in both the tsw39 layer and immediately above the water 
table. This is not the case in the weaker-sorbing 237Np, in which these distributions increase 
measurably over time. The sorbed concentrations of 239Pu in tsw39 or above the water table at 
any time are lower than the corresponding ones for 237Np. This is because the strong sorption of 
239Pu removes a large portion of the radionuclide mass in the overlaying layers, leading to lower 
concentrations in the underlying layers, and hence lower sorbed concentrations. 
6.14.1.6 Comparison to the Semianalytical 2-D FRACL Predictions 
The fracture XR distributions of 239Pu above the water table at t = 100,000 years in Figures 6.14.1 
and VIII.22 indicate no breakthrough (other than the fast transport in the faults) at this time. This 
is consistent with the predictions of the 2-D semianalytical model in Section 6.9 (see Attachment 
V, Figures V.3, V.9, V.15, and V.21). 
6.14.2 239Pu Transport Under Monsoon and Glacial Infiltration 
The DTNs of the input and output files for the three monsoon and glacial infiltration scenarios 
are LB991220140160.013 and LB991220140160.014 (Table 6.13). The faster transport depicted 
in Figures 6.14.3 and 6.14.4 is the result of the higher monsoon and glacial infiltration rates, 
respectively. 
The changes in the climatic conditions lead to breakthrough curves that follow the same pattern 
established in the Tc and Np transport. Thus, higher infiltration corresponds to faster breakthroughs 
(Table6.15). Thedaughtercontributions undermonsoonandglacialconditionsareshowninFigures 
6.14.5 and 6.14.6, respectively. As in the present-day infiltration regime, 235U becomes by far the 
dominant species released at the groundwater after about 7,000 years, and the contribution of 239Pu 
becomes practically negligible after 10,000 years. Lower infiltration rates are also associated with 
(a) earlier significant contributions of 235U to releases at the groundwater table and (b) a faster, 
steeper and larger decline of the 239Pu contributions. The 231Pa contribution is negligible. 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
101 102 103 104 105 106 
Time (years) 
Pu-239 Transport 
Monsoon Infiltration 
0.1 fraction line 
0.5 fraction line 
Pu-239 only 
Mean infiltration 
High infiltration 
Low infiltration 
Pu-239+U-235+Pa-231 
Mean infiltration 
High infiltration 
Low infiltration 
Figure 6.14.3. Normalized relative release R of 239Pu at the water table for varying monsoon climatic scenarios 
(DTN: LB991220140160.013, data submitted with this AMR). 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
101 102 103 104 105 106 
Time (years) 
Pu-239 Transport 
Glacial Infiltration 
0.1 fraction line 
0.5 fraction line 
Pu-239 only 
Mean infiltration 
High infiltration 
Low infiltration 
Pu-239+U-235+Pa-231 
Mean infiltration 
High infiltration 
Low infiltration 
Figure 6.14.4. Normalized relative release R of 239Pu at the water table for varying glacial climatic scenarios 
(DTN: LB991220140160.014, data submitted with this AMR). 
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10-9 
10-8 
10-7 
10-6 
10-5 
10-4 
10-3 
10-2 
10-1 
100 
101 102 103 104 105 106 
Time (years) 
Monsoon Infiltration 
Pu-239 
Mean 
High 
Low 
Pa-231 
Mean 
High 
Low 
U-235 
Mean 
High 
Low 
Figure 6.14.5. Relative mass fluxes MR of the members of the 239Pu ! 235U ! 231Pa decay chain 
in the release at the water table over time for varying monsoon climatic conditions (DTN: 
LB991220140160.013, data submitted with this AMR). 
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10-9 
10-8 
10-7 
10-6 
10-5 
10-4 
10-3 
10-2 
10-1 
100 
101 102 103 104 105 106 
Time (years) 
Glacial Infiltration 
Pu-239 
Mean 
High 
Low 
Pa-231 
Mean 
High 
Low 
U-235 
Mean 
High 
Low 
Figure 6.14.6. Relative mass fluxes MR of the members of the 239Pu ! 235U ! 231Pa decay chain 
in the release at the water table over time for varying glacial climatic conditions (DTN: 
LB991220140160.014, data submitted with this AMR). 
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6.15 EFFECTS OF VARIOUSPERCHED-WATER 
REGIMES ON 3-D TRANSPORT 
Three conceptual perched water models were defined and studied in CRWMS M&O (1999d, 
Sections 6.2 and 6.6). Here we investigate the effect of differences in the three perched water 
models on radionuclide transport under mean present-day conditions. The DTNs of the input and 
output files for the #2 perched water model (involvingflow bypassing) and for the no perched water 
model are listed in Table 6.13. The parameters used in the EOS9nT simulations are listed in Tables 
6.16 and 6.17. 
For reference, we show in Figure 6.15.1 the normalized release rate of the important radionuclides 
for the #1 perched water model under mean present-day infiltration (summarized from Sections 
6.12 to 6.14). Figures 6.15.2 and 6.15.3 show the R for the same radionuclides under the same 
climatic conditions and for the other two perched water models. 
Table 6.16. Input parameters for the EOS9nT 3-D site-scale simulations of solute transport 
(#2 perched-water model, mean present-day infiltration) 
Parameters Source 
Transfer coefficientKi = 1 Conventionally used value 
Tortuosity  '  DTN: LB991220140160.019 and 
DTN: LAIT831341AQ96.001, 
Grathwohl (1998, pp: 28-35), Farrell 
and Reinhard (1994, p: 64) 
Longitudinal dispersivity L = 1 m in the 
fractures, 0.1 m in the matrix 
Scientific judgement in the absence of 
available data 
Properties and characteristics of the geologic 
units, steady-state pressures, water 
saturations and flow fields 
DTN: LB990801233129.004 
Sorption coefficients Kd for Tc, Np, Pu, U, 
Th, Pa 
DTN: LB991220140160.019 and 
DTN: LAIT831341AQ96.001 
Fracture porosity  = 0.99 A reasonable estimate that allows limited 
sorption in the fractures. 
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Table 6.17. Input parameters for the EOS9nT 3-D site-scale simulations of solute transport 
(no-perched-water model, mean present-day infiltration) 
Parameters Source 
Transfer coefficientKi = 1 Conventionally used value 
Tortuosity  '  DTN: LB991220140160.019 and 
DTN: LAIT831341AQ96.001, 
Grathwohl (1998, pp: 28-35), Farrell 
and Reinhard (1994, p: 64) 
Longitudinal dispersivity L = 1 m in the 
fractures, 0.1 m in the matrix 
Scientific judgement in the absence of 
available data 
Properties and characteristics of the geologic 
units, steady-state pressures, water 
saturations and flow fields 
DTN: LB990801233129.004 
Sorption coefficients Kd for Tc, Np, Pu, U, 
Th, Pa 
DTN: LB991220140160.019 and 
DTN: LAIT831341AQ96.001 
Fracture porosity  = 0.99 A reasonable estimate that allows limited 
sorption in the fractures. 
The grids, flow fields and conditions discussed in 6.10.2 corresponded to the #1 conceptual model 
of perched water (CRWMS M&O 1999d, Sections 6.2 and 6.6). This is the permeability barrier 
model, which uses the calibrated perched water parameters for fractures and matrix in the northern 
part of the model domain, and modified property layers (including the tsw38, tsw39, ch1z and ch2z 
layers) where the lower basal vitrophyre of the TSw is above the zeolites of the CHn. A detailed 
discussion of this perched water model can be found in CRWMSM&O (1999d, Section 6.2.2). 
The differences between the breakthrough curves from the #1 and the #2 perched water models 
(Figures 6.15.1 and 6.15.2, respectively) are very small. For all practical purposes, the two models 
result in the same transport behavior. 
A different picture emerges from Figure 6.15.3 of the no-perched water model, which exhibits a 
somewhat slower breakthrough. The t10 are 400, 17,000, and 45,000 years for 99Tc, 237Np, and 
the 239Pu chain members. The corresponding t50 for the same radionuclides are 6,000, 140,000, 
and 300,000 years, respectively. 
Note that caution should be exercized in attempting to compare these EOS9nT results (obtained 
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from a 3-D site-scale simulations) to the 2-D FRACL predictions in Section 6.9 because the latter 
cannot account for 3-D effects such as flow under varying perched water scenarios. A discussion 
on this subject can be found in Section 6.12.2.5. 
1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
101 102 103 104 105 106 
Time (years) 
Tc-99 
Np-237 
Pu-239 only 
Pu-239+U-235+Pa-231 
Mean Present-Day Infiltration 
Perched Water Model #1 
0.1 fraction line 
0.5 fraction line 
Figure6.15.1.Normalizedrelativereleasesatthewatertable formeanpresent-dayinfiltration andthe#1perched 
water model (DTN: LB991220140160.012, data submitted with this AMR). 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
101 102 103 104 105 106 
Time (years) 
Tc-99 
Np-237 
Pu-239 
Pu-239+U-235+Pa-231 
Mean Present-Day Infiltration 
Perched Water Model #2 
0.1 fraction line 
0.5 fraction line 
Figure6.15.2.Normalizedrelativereleasesatthewatertable formeanpresent-dayinfiltration andthe#2perched 
water model (DTN: LB991220140160.015, data submitted with this AMR). 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
101 102 103 104 105 106 
Time (years) 
Tc-99 
Np-237 
Pu-239 
Pu-239+U-235+Pa-231 
Mean Present-Day Infiltration 
No Perched Water Model 
0.1 fraction line 
0.5 fraction line 
Figure6.15.3.Normalizedrelativereleasesatthewatertableformeanpresent-dayinfiltrationandtheno-perched 
water model (DTN: LB991220140160.016, data submitted with this AMR). 
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6.16 3-D SITE-SCALE TRANSPORT OF Pu COLLOIDS 
In this section, we study the transport of true colloids in the entire Yucca Mountain system using 
large-scale 3-D grids. The infiltration regime is that of mean present-day. In these simulations, 
the flow field and the 3-D grid are identical to the ones discussed in the sections on transport of 
dissolved species under the same climatic conditions (Sections 6.11 to 6.14). 
Section 6.16 includes eight subsections. In Section 6.16.1 we discuss the colloidal forms considered 
in the simulations. In Section 6.16.2 we present the mathematical model of filtration used in 
EOS9nT, and discuss its parameters for the four colloids of various sizes (450 nm, 200 nm, 100 nm 
and 6 nm) we discuss in the ensuing sections. In Section 6.16.3 we list the four cases of colloid 
transport of the four colloids we investigated. 
In Section 6.16.4 we study colloid transport for irreversible filtration. In Section 6.16.5 we 
investigate colloid transport with kinetic filtration and fast colloid declogging (detachment). The 
results of this study are shown in Figure 6.16.1, in Figures IX.1 to IX.24 of Attachment IX, and in 
Figures X.1 to X.24 of Attachment X. In Section 6.16.6 we discuss colloid transport with kinetic 
filtration and slow colloid declogging (Figure 6.16.2). In Section 6.16.7 we evaluate the importance 
of fractures in colloid transport with kinetic filtration and fas colloid declogging (Figure 6.16.3). 
Finally, inSection6.16.8we discusssome important observationsfrom thecolloidstudies inSection 
6.16. 
6.16.1 Colloidal Forms and Properties 
As there are indications that colloid-assisted transport (i.e, transport by pseudocolloids) in the UZ 
of Yucca Mountain will not be significant because of the low concentrations of naturally occurring 
colloids such as clays (CRWMSM&O 1999f, Section 6), only true colloids were considered in the 
simulation. Those were taken to have the properties of PuO2 and are subject to radioactive decay. 
Fourcolloidsofdifferentsizeswereconsidered. Theirsizesandtheiraccessibilityfactorsweretaken 
from CRWMSM&O (1999f, Table 1, Section 6), and are shown in Table6.18. The parameters used 
in the EOS9nT simulations of 3-D transport of the colloids are listed in Table 6.19. The DTN of the 
input and output files for the three present-day infiltration scenarios is DTN: LB991220140160.017 
(Table 6.13). 
6.16.2 Colloid Filtration Model and Coefficients 
Pore-size exclusion (strainingfiltration) was described usingthe accessibilityfactorsshown inTable 
6.18. The linear kinetic model of colloid filtration described by Equation 15 was used in the simu- 
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Table 6.18. Properties of the four colloids in the EOS9nT simulations 
Parameter 450 nm 200 nm 100 nm 6 nm 
Diffusion coefficient* 
D0 (m2/s) 
9.53 10-13 2.15 10-12 4.29 10-12 7.15 10-11 
Velocity adjustment 
factory f 
1.5 1.2 1.1 1.0 
Accessibility factorz 
fc in the TSw 
0.05 0.10 0.20 0.65 
Accessibility factorz 
fc in the CHv 
0.45 0.50 0.55 0.80 
Accessibility factorz 
fc in the CHz 
0.20 0.25 0.25 0.65 
: From DTN: LB991220140160.019 
y: Reasonable estimates, see p: 54 
z: From AMR U0070, Table 1 
lations. The forward kinetic coefficient + was computed from Equation 16, in which the velocity 
coefficientsareasshowninTable6.18, and  iscomputedusingEquation2ofHarveyandGarabedian 
(1991), which, in our nomenclature, is
 = 1:5 
1   
dm 
c c ; (Eq. 30) 
where dm is the particle size of the medium grains or the fracture aperture [L], c is the singe 
collector efficiency, and 
c = 0:9 kB T 
w dc dm u2=3 
+ 1:5dc 
dm 2 
+ (c  ) g d2c
18  u 
(Eq. 31) 
in which kB is the Boltzman constant, dc is the colloid diameter [L], T is the absolute temperature, 
and all other terms remain as previously defined. The clogging (forward) kinetic coefficients + 
are computed internally in EOS9nT. 
No information exists on the kinetic declogging (reverse) coefficient . To alleviate the problem, 
 in the EOS9nT coefficients was entered as a fraction of +. We believe that this is a sounder 
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Table 6.19. Input parameters for the EOS9nT 3-D site-scale simulations of colloid transport 
(# 1 perched-water model, mean present-day infiltration) 
Parameters Source 
Transfer coefficientKi = 1 Conventionally used value 
Tortuosity  '  DTN: LB991220140160.019 and 
DTN: LAIT831341AQ96.001, 
Farrell and Reinhard (1994, p: 64) 
Longitudinal dispersivity L =0.5 m in the 
fractures, 0.05 m in the matrix 
Scientific judgement in the absence of 
available data 
Properties and characteristics of the geologic 
units, steady-state pressures, water 
saturations and flow fields 
DTN: LB990801233129.003 (see Table 
6.11) 
Colloid density c = 11,640 kg/m3 (PuO2) Lide (1992, p: 4-83) 
Forward kinetic filtration (clogging) coeffi- 
cient +: from Equations 6, 30 and 31, parameters 
computed at 25 oC 
Harvey and Garabedian, p: 180, Equation 
6, 1991 
Backward (reverse) kinetic filtration (declogging) 
coefficient  = 100+; 0.1+; 0 
Reasonable estimates bracketing the 
range of  
Fracture porosity  = 0.99 A reasonable estimate that allows limited 
colloid filtration (attachment) in the 
fractures. 
approach than the constant  employed in CRWMSM&O (1999f, Section 6) because it maintains 
dependence on the flow velocity. Because the kinetic coefficient + is a linear function of the flow 
velocity, dependence of  on velocity is conceptually sounder than the constant value approach. 
6.16.3 The Colloid Transport Simulation Cases 
The following four cases were investigated: 
1.  = 0. This corresponds to a case of no declogging, in which colloids, once filtered, do not 
detach from the pore/fracture walls. 
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2. =+ = 100. This corresponds to strong kinetic declogging and will provide an estimate of 
maximum colloidal transport. 
3. =+ = 0:1. This corresponds to weak kinetic declogging and approaches equilibrium 
filtration behavior. 
4. Same as in Case 2, but the fractures are assumed to have the same colloidal transport properties 
as the corresponding matrix. This study provides an estimate of the importance of fractures 
in the transport of colloids. Note that the change in the filtration properties affects only 1% of 
the fracture pore volume (because  = 0.99 in the fractures, see Equation 30). 
6.16.4 Colloid Transport Case 1 
The results of this simulation indicate no colloid breakthrough at any time. This is consistent with 
the underlying clogging-only model. 
6.16.5 Colloid Transport Case 2 
6.16.5.1 Breakthrough Curves 
Figure 6.16.1 shows the relative release rate R of the four colloids at the water table . Two 
observations appear particularly important. The first is the very fast breakthrough of the larger 
colloids (characterized by a rapid rise of the breakthrough curve), the rapidity of which increased 
slightly with the colloid size. The t10 for the three larger colloids is only about 15 years, and 30 
years for the 6 nm colloid; t50 is about 60 years for the 450 nm and the 200 nm colloid, about 
80 years for the 100 nm colloid, and 1,200 years for the 6 nm colloid. The second observation is 
that, counter to expectations, the smallest colloid (6 nm) exhibits the slowest breakthrough. This 
behavior results from a combination of the following factors: 
1. The larger transport velocity of larger colloids, which, by virtue of their size, can only move 
in the center of pores/fractures where velocities are larger than the average water velocity. In 
this case, the 450 nm colloid moves at 1.5 times the water velocity (i.e., f = 1:5, see Equation 
16 in Section 6.2.4.1). 
2. The inability of larger colloids to penetrate into the matrix from the fractures because of size 
exclusion. Thus, the colloid mass in the fractures is not reduced through colloidal diffusion 
and/or hydrodynamic dispersion, and practically all of it moves exclusively in the fractures. 
The 6 nm colloid is capable of diffusing into the matrix, a process which in Figure 6.16.1 
manifests itself by the substantially slower breakthrough, the milder rise of the curve, and its 
lower maximum R value. 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
100 101 102 103 104 105 106 
Time (years) 
dc=450 nm 
dc=200 nm 
dc=100 nm 
dc=6 nm 
Mean Present-Day Infiltration 
Case 2 
0.1 fraction line 
0.5 fraction line 
Figure 6.16.1. Normalized release at the water table in Case 2 of colloidal transport for mean present-day 
infiltration (DTN: LB991220140160.017, data submitted with this AMR). 
6.16.5.2 Transport Mechanisms and Patterns of the 6 nm Colloid 
The importance of fractures on the transport of the 6 nm colloid (Co0060) is evident in Figure IX.1 
(see Attachment IX), which shows the areal distribution ofXR in the aqueous phase in the fractures 
in the tsw39 layer at t = 10 years (under mean present-day infiltration). Despite the very early time, 
the colloid concentration in the fracture is substantial, and it approaches the release concentration 
(XR = 0.965) at its maximum. 
The reasons for the significant presence (in terms of areal extent and level of concentration) of 
the 6 nm colloid are that (a) diffusion into the matrix is limited because of its relatively large size 
(compared to solutes) and pore-exclusion, and (b) the tsw39 layer is above the TSw-CHn interface, 
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where significant filtration occurs. Note that the distribution pattern of the fracture XR in Figure 
IX.1 indicates that the colloids (transported in the fractures) accumulate at the TSw-CHn interface 
and, unable to cross it, move along the sloping interface in an easterly direction. This transport is 
more pronounced in the 6-nm colloid than in the solutes (see Sections 6.11 to 6.14, and Attachments 
VII and VIII). 
In contrast to Figure IX.1, the matrix XR in Figure IX.2 shows no discernible difference from the 
background at the same time. In Figure IX.3, the distribution of matrix FR at t = 10 years shows a 
sizable presence of the 6 nm colloid filtered onto the matrix of the tsw39 layer. As in the case of 
sorbing solutes, the area of nonzero FR (Figure IX.3) is larger than that of the fractureXR footprint 
(Figure IX.3) at the same time, and shows presence of filtered 6 nm colloids at locations where 
there appear to be no colloids suspended in the aqueous phase in the fractures. 
At t = 100 years, the fracture XR in Figure IX.4 is significant over a large area (larger than that for 
solutes at the same time) and is at its maximum value over a large portion of this area. Although the 
matrix XR (Figure IX.5) does not register a measurable difference from the UZ background, the 
matrix FR (Figure IX.6) shows a significant presence of the 6 nm colloid over an area larger than 
that covered by the fracture XR (Figure IX.4). Note that the matrix FR distribution indicates more 
filtration in the northern part of the potential repository. This is consistent with the permeability 
barriers that result in the perched water bodies at this location. 
A comparison of the matrix FR of the 6 nm colloid (Figure IX.6) to that of the dissolved 239Pu 
(Figure VIII.3) shows a drastically different pattern. While the matrix FR distribution of 239Pu 
shows concentration of sorption in the southern part of the potential repository, the FR of the 6 
nm colloid shows filtration in both the northern and the southern part, i.e., colloids and sorbing 
radioactive solutes (Sections 6.12 to 6.15) are not similarly affected under the #1 perched water 
model. The reason for the different behavior is attributed to (a) the lower diffusion of the colloid 
into (and the lack of its sorption onto) the matrix (thus the faster transport of larger amounts to the 
TSw-CHn interface), (b) the lack of sorption and (b) the combined effects of pore-size exclusion 
and filtration at the interface that are quantitatively larger than the effects of sorption of the limited 
amounts of the dissolved 239Pu (Figure VIIi.3). 
The fracture XR, matrix XR, and matrix FR distributions at t = 1,000 years and t = 10,000 years 
are shown in Figures IX.7 to IX.12, and they follow the same pattern. The matrix XR registers 
measurable deviations from background at t = 1,000 years (Figure IX.8), and it shows extensive 
areas of relatively high concentrations at t = 10,000 years (Figure IX.11). At t = 10,000 years, the 
concentration in the fractures exceeds that in the water released from the potential repository (i.e., 
XR = 1.07 in tsw39). This is caused by pore-exclusion (straining) at the TSw-CHn interface, which 
leads to the accumulation of the 6 nm colloid in the tsw39. 
Transport at the water table is shown in Figures IX.13 to IX.24, and follows patterns analogous to 
those in the tsw39 layer. The high concentrations at the water table at early times (t  100 years) 
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are noteworthy. The matrix XR begins to show signs of colloid presence at t = 1000 years, and 
shows highly localized areas of large concentration at t = 10,000 years. The nonzero area of the 
matrix FR is consistently larger than that for fracture XR. 
Note that the fractureXR above the water table exceeds that in the water released from the potential 
repository, and the differences between the two increases with time. At t = 10,000 years, the 
maximum fracture XR > 2, i.e., the concentration of the 6 nm colloid in the fractures above the 
water table is more than double that in the water released at the potential repository. This occurs 
becauseof thefasttransport of thecolloidsinthefractures (wherelimitedattachment occurs because 
of the large fracture porosity, i.e.,  = 0.99) and their accumulation. This accumulation is caused 
by the very significant pore-size exclusion and kinetic (physical-chemical) filtration at the water 
table , which prevent colloids from entering the saturated zone while allowing water to flow into it. 
This occurs because the saturated zone behaves as a porous (rather than a fractured) medium with 
the properties of the TSw matrix. 
Review of Figures IX.1 through IX.24 indicates that transport of the 6 nm colloid is dominated by 
the faults identified and discussed in Sections 6.12 to 6.14. Diffusion from the fractures into the 
matrix is delayed for the reasons discussed earlier, but the areal extent and the magnitude of the 
filtered concentration (indicated by the FR distribution) indicates that its effect is sizable. 
6.16.5.3 Transport Mechanisms and Patterns of the 450 nm Colloid 
The fracture XR, matrix XR and matrix FR distributions of the 450 nm colloid (Co450) in the 
tsw39 and above the water table are shown in Figures X.1X.24 (see Attachment X). These figures 
correspond to the same times discussed in the 6 nm colloid. 
Comparison of the Figures in Attachment Xto those for the 6 nm colloid in Attachment IX indicates 
that fractures are far more important to the transport of the 450 nm colloid. Supporting evidence is 
provided by (a) the larger areal extent and values of the fractureXR, (b) the smaller areal extent and 
lower values of the matrix FR, and (c) the substantial delay in the appearance of 450 nm colloids 
in the matrix aqueous phase, when compared to the 6 nm case. 
Thus, the fracture XR in Figure X.4 (t = 100 years) indicates contributions from the whole area (at 
least) of the potential repository, and shows a much larger footprint than the corresponding 6 nm 
figure (Figure IX.4). Additionally, the maximum XR exceeds 1 (= 1.40) because of accumulation 
behind the TSw-CHn interface caused by straining (pore-size exclusion). Because of its larger size, 
the straining is more pronounced in the 450 nm colloid, rather than in the 6 nm colloid, and leads 
to higher concentrations at earlier times behind the interface (see Figures X.4, X.7 and X.10). The 
same phenomenon occurs above the water table (Figures X.13, X.16, X.19 and X.29), where it 
is far more pronounced, and the fracture XR reaches values as high as 72. Note that, while this 
indicates a significant colloid accumulation, it does not necessarily mean clogging and decrease in 
permeability (at least for a long time) if the concentrations of the colloid waste form are sufficiently 
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low. The reasons for this behavior at the water table were discussed in Section 6.16.5.2. 
Compared to the 6 nm colloid, the 450 nm colloid exhibits consistently lower matrix FR values 
over smaller areas (see Figures X.3, X.6, X.9, X.12, X.15, X.18, X.21, X.24). This is consistent 
with the expectation of lower diffusion from the fractures into the matrix and increased straining 
because of its larger size. 
6.16.6 Colloid Transport Case 3 
The change in the magnitude of the reverse kinetic filtration coefficient  (as a fraction of +) 
has a rather dramatic effect on colloid transport (Figure 6.16.2). This case is closer to equilibrium 
filtration and results in a breakthrough that occurs at a time about three orders of magnitute larger 
than that of Case 2 (see Figure 6.16.1). Thus, t10 is 12,000 years for the 450nm, the 200 nm and 
the 100 nm colloids, and infinity for the 6 nm colloid; t50 is infinity for all colloids because the 
maximum normalized release rate at the water table never exceeds 0.3. 
Repeating the pattern discussed in Section 6.16.5, the larger three colloids reach the groundwater 
first. The 6 nm colloid reaches the groundwater slightly later, but it has a substantially different 
R curve, with a maximum value that is only one third that for the 450 nm colloid. This stems 
from both larger diffusion (compared to that of the larger colloids) into the matrix and the resulting 
slower transport, which allows radioactive decay to reduce the colloid mass. Note that the R of the 
6 nm colloid reaches a plateau at only about R = 0.097, i.e., it does not even attain the 0.1 level. 
6.16.7 Colloid Transport Case 4 
Setting the fracture filtration properties equal to those of the matrix results leads to the transport 
scenario depicted inFigure 6.16.3. Theeffect of limited diffusion on transport (because of pore-size 
exclusion and filtration) becomes more obvious in this case. Thus, the 6 nm colloids are the first to 
reach the groundwater, the 450 nm are the last, and the first arrival times of the rest increase with 
their diameter. 
The reason for this study was to obtain a measure of the relative importance of the fractures in 
UZ colloid transport. The t50 of the three larger colloids is about 1,000 years, and 2,000 years 
for the smallest colloid. Given that the significant difference between Figure 6.16.3 and 6.16.1 is 
due solely to assigning matrix filtration properties to only 1% of the pore volume of the fractures, 
the significant retardation of the colloids gives a measure of the importance of fractures and their 
relative contribution to the total colloid transport through the UZ system. 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
100 101 102 103 104 105 106 
Time (years) 
dc=450 nm 
dc=200 nm 
dc=100 nm 
dc=6 nm 
Mean Present-Day Infiltration 
Case 3 
0.1 fraction line 
0.5 fraction line 
Figure 6.16.2. Normalized release at the water table in case 3 of colloidal transport for mean present-day 
infiltration (DTN: LB991220140160.017, data submitted with this AMR). 
6.16.8 Uncertainties and Limitations 
While the results in this section provide some elucidation of colloid transport, caution should be 
exercised in the interpretation of the simulation results. The reason for this notice of restraint is 
the realization of the substantial knowledge gaps that hamper the study of colloid behavior. 
Thus, the tremendous variation in behavior with the change in the kinetic declogging coefficient  
should only serve to indicate the sensitivity of transport to . Similarly, the change in transport 
behavior when 1% of the fracture volume is given the attributes of the matrix should be viewed as 
indicative and qualitative, rather than quantitative and predictive. In essence, the sensitivity of the 
model to these parameters is evidenced by the change in t10 of the larger colloids from 15 years to 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
100 101 102 103 104 105 106 
Time (years) 
dc=450 nm 
dc=200 nm 
dc=100 nm 
dc=6 nm 
Mean Present-Day Infiltration 
Case 4 
0.1 fraction line 
0.5 fraction line 
Figure 6.16.3. Normalized release at the water table in case 4 of colloidal transport for mean present-day 
infiltration (DTN: LB991220140160.017, data submitted with this AMR). 
about 12,000 years to infinity as the value of  changes from 100+ (fast declogging) to 0.1+ 
(slow declogging) to 0 (no declogging). 
There are significant uncertainties in colloid modeling. It is not known if the applicability limits of 
thecurrently availablekinetic models, developedfrom theoretical principles (Herziget al: 1970)and 
tested inuniform sandy laboratory experiments (vandeWeerd and Leijnse 1997) or small-scale field 
tests (Harvey and Garabedian 1991), are not breached under the UZ conditions at YuccaMountain. 
The affinity of colloids for air-water interfaces can have a significant effect on their transport. The 
limitations of the equations for the prediction of the forward kinetic filtration (clogging coefficient) 
have not been tested under the UZ conditions, and the subject of kinetic declogging coefficient has 
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barely been raised (let alone studied). Additionally, it is unclear how representative the current sizeexclusion 
(straining filtration) models are. Additional challenges and uncertainties are discussed 
in detail in Section 6.1.3. 
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6.17 ALTERNATIVEMODELS 
In this section, we investigate an alternative conceptual model and its effect on transport. This 
conceptual model assumes no diffusion. All simulations in this section assume a mean present-day 
infiltration. 
Section 6.17 includes two subsections. In Section 6.17.1 we study solute transport using the 
alternative conceptual model of no diffusion. The results of this study appear in Figure 6.17.1. In 
Section 6.17.2 we investigate colloid transport under the alternative model. 
6.17.1 Solutes 
As shown in Sections 6.11 to 6.15, the main mechanism of radionuclide retardation in the UZ is 
diffusion from the fracture into the matrix. This process transfers radionuclides from the fractures 
(the pathways of fast flow and the main conduits of transport) to the matrix, where their transport 
is retarded because of the much slower water velocities and matrix sorption. 
In this section we investigate an alternative conceptual model that does not allow diffusion into the 
matrix. Thus, there is no mechanism for radionuclide removal from the fractures other than the 
relatively small sorption on the fracture walls. For non- and moderately sorbing radionuclides, this 
means that there is no means of retardation, and the contaminants in the fractures are transported 
virtually unhindered to the groundwater. 
For mean present-day infiltration, the breakthrough curves in Figure 6.17.1 confirms this expectation. 
The nonsorbing 99Tc and the moderately sorbing 237Np move unhindered in the fractures, and 
their breakthrough curves to t = 50 years practically coincide. Transport in this case is extremely 
fast, and their t10 and t50 are about 5 and 30 years, respectively. The early behavior (i.e., to t = 
100 years) reflects fracture transport exclusively, and the identity of the breakthrough curves of 
99Tc and 237Np results from the absence of diffusion into the matrix and the limited 237Np sorption 
onto the fracture walls, which is insufficient to have a measurable effect on transport. Note that the 
breakthrough curves reach a plateau at t = 50 years. The flat portion of the breakthrough curves 
indicates a constant radionuclide release rate at the water table , all of which is attributable to 
fracture flow. 
The effects of the matrix become evident for t > 100 years, when matrix flow (and the contaminants 
it transports) begins to arrive at the water table . The arrival of matrix flow is indicated by the rising 
portion of the breakthrough curve after the fracture-associated R plateau. The nonsorbing 99Tc is 
not retarded and arrives at the water table earlier than the moderately sorbing 237Np. The phase of 
constant 237Np release from fracture flow lasts from 50 to about 2,000 years, after which time the 
matrix flow (and the 237Np it transports) arrive at the water table . 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
10-1 100 101 102 103 104 105 106 
Time (years) 
Tc-99 
Np-237 
Pu-239 
Pu-239+U-235+Pa-231 
0.1 fraction line 
Mean present-day infiltration 
No matrix diffusion 
0.5 fraction line 
Figure6.17.1.Normalized relativereleasesofradioactive solutesatthewatertable fortheno-diffusionalternative 
model(meanpresent-dayinfiltration, #1perchedwatermodelDTN:LB991220140160.012, data 
submitted with this AMR). 
The picture is somewhat different for the strongly sorbing 239Pu. The limited sorption on the 
fracture walls (attained by setting  = 0.99 in the fractures) is sufficiently high to retard transport 
in the fractures. If only 239Pu is considered, the fracture release rate reaches a plateau at about 300 
years, i.e., a very short time considering its half-life. Its constant (and at R = 0.52, very significant) 
value indicates only fracture contributions to the release at the water table , as the matrix acts as sink 
for the 239Pu in the matrix flow. Thus, there is no matrix contribution to the groundwater release 
of 239Pu in the first 106 years. 
Accounting for the 239Pu daughters leads to matrix contributions to the water table after t = 10,000 
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years. These are attributed (almost exclusively) to the release of the 235U daughter (see Section 
6.13), which sorbs less strongly and has a longer half-life than 239Pu. 
The results of this study emphasize the importance of diffusion from the fractures into the matrix as 
the main mechanism for retardation of radionuclide transport. When this process is not considered 
in the simulations, very fast travel times are observed, and radionuclides reach the water table in 
less than 10 years. 
6.17.2 Colloids 
For the conditions of Case 2 (see Section 6.16.6), the breakthrough curves for no diffusion in Figure 
6.17.2 arequite similar tothe onesobtained when colloid diffusionis considered (see Figure 6.16.1). 
This was expected because (a) colloid diffusion is smaller than molecular diffusion because of the 
larger colloid size, and (b) size exclusion (straining) effects at the interfaces of different layers 
further limit entry through diffusion into the matrix (especially for larger colloids). 
The early portions (to 70 years) of the breakthrough curves for the 450, 200 and 100 nm colloids 
are identical, indicating the same filtration behavior. Colloid straining is the reason for the larger 
t10 (= 15 years) and t50 (= 100 years for the 6 nm colloid, 60 years for the 450, 200, and 100 nm 
colloids) compared to those for solutes. These times are practically the same as those observed 
for the 450 and 200 nm colloids in Figure 6.15.1, indicating the limited importance of diffusion to 
larger colloids. 
Comparison of the curves in Figures 6.17.2 and 6.16.1 shows the increasing importance of diffusion 
as the colloid sizedecreases. Thus, inclusionof diffusion leadsto limitedretardation of the transport 
of the 100 nm colloid, but the effect is more pronounced in the case of the 6 nm colloid. Its t10 and 
t50 are reduced from 300 and 1,500 years to 15 and 100 years, respectively. 
Notethatthecolloidbreakthroughcurvesdonotexhibittheplateaus(denotingpurefracturetransport 
with no matrix contribution) of the solute curves in Figure 6.17.1, but rather a section of milder 
slope. This is attributed to the slower transport in the fractures (as a result of straining at the 
hydrogeologic layer interfaces) and the resulting evolution of concentrations larger than that in the 
water released from the potential repository. Hence the concentration gradients keep increasing 
over time, and do not reach a steady-state as in solutes. 
The conclusion drawn from this study is that diffusion is less significant in the transport of colloids 
than insolutetransport. Its effect, however,becomes increasingly important for adecreasing colloid 
size. 
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1.0 
0.8 
0.6 
0.4 
0.2 
0.0 
10-1 100 101 102 103 104 105 106 
Time (years) 
450 nm 
200 nm 
100 nm 
6 nm 
0.1 fraction line 
Mean present-day infiltration 
No matrix diffusion 
0.5 fraction line 
Figure 6.17.2. Normalized relative releases of radioactive colloids at the water table for the no-diffusion alternative 
model (mean present-day infiltration, #1 perched water model, Case 2 conditions  DTN: 
LB991220140160.017, data submitted with this AMR). 
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7. CONCLUSIONS 
7.1 SUMMARY OF MODELING ACTIVITY 
In Section 6.4 modeling activity focused on the validation and calibration of the RTM using the 
2-D semianalytical FRACL code and the 3-D numerical EOS9nT code. Wefirst validated the RTM 
by comparing the predictions of both codes to the analytical solution of Sudicky and Frind (1982). 
We then calibrated the RTMby using FRACL to analyze field data of Cl distribution in the UE-25 
UZ#16 borehole, and compared the FRACL results to the predictions from a 3-D simulation using 
the T2R3D code. Finally, we calibrated the RTm by using EOS9nT to analyze field data of Cl 
distribution in the ESF, and compared the results of the 3-D site-scale simulation to the T2R3D 
predictions for the same grid and conditions. 
Modeling activity in Sections 6.6, 6.7 and 6.8 involved the application of the FRACL code to 
simulate the transport of the radioactive solutes 99Tc (nonsorbing), 237Np (moderately sorbing) 
and 239Pu (strongly sorbing) in three vertical cross sections that are representative of the individual 
hydrogeologic units (i.e., TSw, CHn and PP) present at the site of the potential repository. The 
focus of these studies was to determine the important processes and the effect of differences in 
geology on the transport of radionuclides with different transport and decay properties. 
Modeling activity in Section 6.9 involved the application of the FRACL code to simulate the 
transport of 99Tc, 237Np and 239Pu in three vertical cross sections covering the entire geologic 
profile from the potential repository to the groundwater table. The purpose of these simulations is 
to evaluate the integrated transport performance of all the hydrogeologic units beneath the potential 
repository. 
The modeling activity in Section 6.10 involved the application of the T2R3D code to predict the 
concentration and water saturation distributions after the injection of various tracers into the ch1v 
and ch2v layers. The studies were numerical simulations of two sets of tests in the the first phase of 
an experiment conducted in Busted Butte, Yucca Mountain (CRWMS M&O 1999e, Section 6.8). 
The field work on these phases has been completed, but the analysis of the experimental results is 
not yet complete. 
Modeling in Section 6.11 involved the application of TOUGH2 V1.4 Module EOS9 V1.4 (STN: 
10007-1.4-01) to obtain the flow fields in the 3-D site-scale YM domains to be used in subsequent 
transport simulations. Flow fields for a total of nine climatic scenarios were obtained. 
In Sections 6.12 to 6.14, modeling activity involved the application of EOS9nT to study the 
transport of 99Tc, 237Np, and 239Pu in the entire Yucca Mountain system using large-scale 3-D 
grids. Additionally, (a) the contributions of the daughters of 237Np and 239Pu to transport to the 
water table and (b) the effects of varying infiltration were modeled. Modeling in Section 6.15 
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involved the EOS9nT code and focused on the effects of various perched water table bodies to the 
transport of 99Tc, 237Np, and 239Pu and their important daughters. 
The modeling activity in Section 6.16 involved the application of EOS9nT to study the transport 
of four true colloids of different sizes and properties in the entire Yucca Mountain system using 
large-scale 3-D grids. Modeling using the EOS9nT code in Section 6.17 aimed at evaluating the 
YM UZ system performance under a different conceptual model that does not consider diffusion. 
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7.2 AMR CONCLUSIONS 
The following conclusions can be drawn from this study: 
1. Thetransfer coefficientKi maybe important inthe migration of strongly sorbingradionuclides 
(such as 239Pu), as lower Ki values enhance transport. 
2. Increasing matrix tortuositycoefficient(   1) valueslead toincreasedmatrix diffusion, lower 
relative concentrations and delayed breakthroughs in the fractures, and larger concentrations 
and sorption in the matrix. 
3. The importance of the longitudinal dispersivity L in accurately predicting the transport of 
radionuclides increases with the sorption affinity of the radionuclide (i.e., with the distribution 
coefficient Kd). 
4. Transport in the TSw hydrogeologic unit is strongly dependent on the thickness of the unit 
(measured from the bottom of the potential repository) and its spatial variability over the area 
of the potential repository. 
5. Transport in the CHn hydrogeologic unit is strongly dependent on the spatial variability of the 
distributionof thevitric and zeolitic layersoverthe areaof thepotential repository. Occurrence 
of zeolitic layers leads to fast advective transport due to flow focusing caused by the large 
fracture permeability (compared to that in the matrix). The parity of the fracture and matrix 
permeabilityinthevitriclayersleadstobehaviorakintothatofaporous(ratherthanafractured) 
medium. The vitric layers of the CHn hydrogeologic unit are shown to be effective barriers 
to radionuclide transport, and their effectiveness increases with the sorptive tendencies of the 
radionuclides. 
6. Radionuclide transport appears to be practically uninhibited in the top zeolitic layers (pp4) of 
the PP hydrogeologic unit, but is effectively retarded by the underlying devitrified layers. The 
retardation is a function of the relative thickness of the zeolitic and devitrified layers. 
7. Resultsfrom2-DsemianalyticFRACLsimulationsoftransportfromthebottomofthepotential 
repository to the water table show that the times to reach the water table from the release point 
are (a) 1,000 years or more for 99Tc, (b) 10,000 or more for 237Np, and (c) over 100,000 years 
for 239Pu. The arrival times are consistent at three different locations within the domain of the 
potential repository. Note that these 2-D simulations predict fracture and matrix transport, but 
do not account for the possible effects of faults. 
8. The2-DFRACLsimulationsindicatethatincreasinginfiltrationratesleadtofasterradionuclide 
transport to the water table. The largest increase was observed for the non-sorbing 99Tc, and 
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the smallest for the strongly sorbing 239Pu. 
9. The 2-D FRACL simulations indicate that conditions leading to the emergence of perched 
water bodies (i.e., permeability barriers) in the #1 perched water model lead to retardation of 
radionuclide transport. The effect is more pronounced in less strongly sorbing radionuclides 
(such as 99Tc and 237Np) at relatively early times and is less important for stronger-sorbing 
radionuclides and longer times. 
10. 3-D site-scale simulations using EOS9nT indicate that, under the #1 perched water model, 
radionuclide transport from the bottom of the potential repository to the water table is both 
dominated and controlled by the faults. These provide fast pathways to downward migration 
to the water table, but also limit lateral transport past them. 
11. The 3-D site-scale EOS9nT simulations indicate that radioactive solutes from the potential 
repository move faster and reach the water table earlier and over a larger area in the southern 
part of the potential repository. This appears to be counterintuitive, as it would be reasonable 
to expect that the general area of fastest, largest, and most extensive transport would be in 
the northern part of the potential repository site, where the highly conductive fractures of the 
zeolitic CHn layers occur. There are four reasons for this transport pattern. 
12. The first reason is the infiltration and percolation distributions. A review of the infiltration 
pattern at the surface, the percolation flux at the repository level and the percolation flux at 
the groundwater level indicates that they closely reflect the transport patterns discussed in 
Conclusion (11). Thus, the water flow pattern dictates the advective transport pattern. In the 
#1 perched-water model of these studies, the maximum water flow within the footprint of the 
potential repository is in its southern part. 
The presence of the highly conductive (a) Splay G of the Solitario Canyon fault and (b) 
Ghost Dance fault splay are the second reason (and related to the percolation patterns) for the 
dominance of the southern part of the potential repository as the pathway of transport, despite 
the vitric CHv layers having fewer fractures (than the overlying TSw) and acting as porous 
(rather than fractured) media (with relatively lower water velocities). Once contamination 
migrating through the Splay G of the Solitario Canyon fault reaches the TSw-CHn interface, 
it moves primarily in an easterly direction, moving with the draining water that hugs the 
downward sloping (in this direction) low-permeability interface. 
Additionally, the Sundance fault, the Drill Hole Wash fault, and the main Ghost Dance fault 
are transport-facilitating geologic features. Of these, the Drill Hole Wash fault and the main 
Ghost Dance fault act as barriers to the northward and eastward radionuclide movement, while 
providing pathways for relatively fast transport to the water table. 
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The transport pattern discussedin Conclusion (11) may befurther facilitated by the contraction 
of the areal extent of the vitrified tuffs (the third reason), whose vertical distribution shows 
a funnel-type structure in the southern part of the potential repository. Thus, as depth from 
the potential repository increases, an increasing portion of the water flow occurs through the 
zeolites, in which the fracture-dominated flow (and, consequently, transport) is fast. The 
fourth reason is the low-permeability zones at the TSw-CHn interface in the northern part of 
the potential repository in the #1 perched water model. These zones are barriers to drainage, 
and lead tolow water velocities and perched water bodies. Radionuclides move slowly through 
the perched water before reaching the underlying highly permeable zeolite fractures; hence 
the delay in transport. 
13. Fractures are the main pathways of radionuclide transport. Diffusion from the fractures into 
the matrix is the main retardation process in radionuclide transport. By sorbing onto the 
matrix into which they diffuse, the migration of sorbing radionuclides is retarded. The same 
process leads to retardation in the fractures by resulting in larger concentration gradients (thus 
enhanced diffusion) between the liquid phases in the fractures and in the matrix. 
14. The importance of faults and perched water bodies in transport is directly dependent on the 
underlying geologic and perched water conceptual models. It is reasonable to expect that 
changing geologic and perched water models may lead to substantially different results, given 
thesensitivityoftransporttothesegeologicfeatures. Thisrealizationunderlinestheimportance 
of representative conceptual models. 
15. From the 3-D EOS9nT simulations we determine that, under present-day climatic conditions 
(infiltration of 6 mm/year) and the #1 perched water model, the t10 (see definition in Section 
6.12) of the non-sorbing 99Tc for low, mean and high infiltration is 10,000, 300, and 45 years, 
and the t50 (see definition in Section 6.12) is 45,000, 4,000 and 1,000 years, respectively. 
Under the same conditions, the t10 of the moderately sorbing 237Np for low, mean and high 
infiltration is 220,000, 10,000, and 1,700 years, and the corresponding t50 is over 1,000,000, 
120,000, and 22,000 years, respectively. The contributions of the 237Np daughters to releases 
at the water table are trivial and can be safely ignored. 
16. In the 3-D site-scale simulation of transport of the strongly sorbing 239Pu, the members of 
the decay chain may have to be considered (i.e., 239Pu, 235U, and 231Pa) if the 239Pu release 
rate at the repository is significant. Although the t10 for 239Pu transport is always larger than 
1,000,000 years, 235U becomes the main contributor in the radionuclide release at the water 
table after 10,000 years (at most) because of its weaker sorption onto the matrix and its longer 
half-life. The contributions of 231Pa are not important. Under present-day climatic conditions 
and the #1 perched water model, the t10 of the members of the 239Pu chain for low, mean and 
high infiltration is computed from the 3-D simulations as 600,000, 40,000, and 12,000 years, 
and the t50 is >1,000,000, 250,000, and 9,000 years, respectively. 
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17. The 3-D site-scale simulations indicate that a change in the future climatic conditions can have 
a significant effect on transport. Increasing infiltration (as the climatic regime changes from 
present-day to monsoon and glacial conditions and its level changes from low to mean to high) 
leads to faster radionuclide transport to the water table. The acceleration in transport increases 
with decreasing sorption. 
Thus, for the extreme case of high glacial infiltration (about 33.5 mm/year), the t10 of the 
non-sorbing 99Tc is reduced to about 10 years, and t50 is 160 years. For the same infiltration, 
the t10 and t50 of 237Np are reduced to 260 and 2,000 years, respectively, while the t10 and 
t50 of 239Pu are reduced to 5,100 and 38,000 years, respectively 
18. The 3-D site-scale simulations indicate that, for a mean present-day infiltration, radionuclide 
transport does not appear to be significantly affected by the conceptual model used to describe 
the perched water bodies, as the three models studied (i.e., the #1 perched water model, the #2 
perched water model and the no-perched water model, see CRWMS M&O 1999d, Sections 
6.2 and 6.6) show similar results. 
19. Thepredictions of radionuclide transport obtained using the 2-Dsemianalytical FRACLmodel 
are generally consistent with those from the 3-D site-scale numerical model. Note that caution 
should be exercized in the comparison of these results because of the conceptual differences 
between the 2-D and the 3-D problems. Thus, FRACL is capable of providing a good firstorder 
estimate of radionuclide concentration distributions and travel times from the bottom 
of the potential repository to the water table at a particular narrow cross section of the UZ. 
Further refinements, accounting for faults and the effects of 3-D systems and phenomena, can 
then be obtained from the 3-D EOS9nT simulations. 
20. For a mean present-day infiltration and a given kinetic clogging (forward filtration) coefficient 
+, the transport of radioactive true colloids is strongly influenced by the kinetic declogging 
(reverse filtering) coefficient . When no declogging is allowed, no colloids reach the 
groundwater. Low values of  (i.e., slow declogging) lead to long travel times to the water 
table (and thus significant retardation). For =+ = 0:1, t10 is 12,000 years for the 450, 200 
and 100 nm colloids, and infinity for the 6 nm colloid; t50 is infinity for all colloids because 
the maximum normalized release rate at the water table never exceeds 0.3. 
Large values of  lead to a dramatically different behavior, with very fast travel times of the 
radioactive colloids to the water table. For =+ = 100, the t10 is 15 years for the 450 nm, 
the 200 nm and the 100 nm colloids, and 30 years for the 6 nm colloids. The t50 is about 60 
years for the 450 nm and 200 nm colloids, about 80 years for the 100 nm colloid, and 1,200 
years for the 6 nm colloid. The extreme sensitivity of colloid filtration (deposition) on  and 
the dearth of any representative information on its value in the various UZ hydrogeologic units 
underline the need for attention to this subject. 
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21. Foragiven , thecolloid sizehas asignificanteffecton transport. Giventhefactthat fractures 
are the main transport conduit in YM, the inability of larger colloids to diffuse into the matrix 
because of smaller D0 values and size exclusion (straining) result in faster transport to the 
groundwater. Smaller colloidal particles can diffuse easier into the matrix, and their transport 
is thus retarded. 
22. Size exclusion (straining) at the interfaces of different hydrogeologic layers leads to colloid 
concentrations immediately above the interface that can be significantly higher than that in the 
water released from the potential repository. This phenomenon is more pronounced in larger 
colloids. 
23. Assuming an alternative conceptual model of no diffusion from the fractures into the matrix, 
thetransport ofradioactivesolutes tothewater tableis dramatically accelerated, and t10 and t50 
canbeas low as 5 and 30 years, respectively. Acharacteristic plateau marks theperiod between 
constant steady-state fracture release and the arrival at the water table of the radionuclide front 
in the fracture flow. 
The analysis of the alternative model indicates that diffusion is less significant in colloid 
transport than in solute transport. Its effect, however, becomes increasingly important as the 
colloid size decreases. 
This document and its conclusions may be affected by technical product input information that 
requires confirmation. Any changes to the document or its conclusions that may occur as a result 
of completing the confirmation activities will be reflected in subsequent revisions. The status of 
the input information quality may be confirmed by review of the DIRS Database. 
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INTENTIONALLY LEFT BLANK 
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WE/88/34. Luxembourg, Luxembourg: Commission of the European Communities. 
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Approximation. Journal of the Association of Computing Machinery, 23 (1), 8996. 
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Operating Contractor) 1999a. M&O Site Investigations. Activity Evaluation. Las Vegas, 
Nevada: CRWMS M&O. ACC: MOL.19990317.0330. 
CRWMS M&O 1999b. M&O Site Investigations. Activity Evaluation. Las Vegas, 
Nevada: CRWMS M&O. ACC: MOL.19990928.0224. 
CRWMS M&O 1999c. Analysis & Modeling Development Plan (DP) for U0060 , 
Radionuclide Transport Models under Ambient Conditions, Rev. 00. TDP-NBS-HS- 
000013. Las Vegas, Nevada: CRWMS M&O. ACC: MOL.19990830.0381. 
CRWMS M&O 1999d. UZ Flow Models and Submodels. MDL-NBS-HS-000006. Las 
Vegas, Nevada: CRWMS M&O. ACC: MOL.19990721.0527. URN-0030. 
CRWMS M&O 1999e. Unsaturated Zone and Saturated Zone Transport Properties. 
ANL-NBS-HS-000019. Las Vegas, Nevada: CRWMS M&O. URN-0038. 
CRWMS M&O 1999f. UZ Colloid Transport Model. ANL-NBS-HS-000028. Las 
Vegas, Nevada: CRWMS M&O. URN-0031. 
CRWMS M&O 1999g. Enhanced Design Alternative (EDA) II Repository Layout for 10 
cm/s Ventilation Plan. Las Vegas, Nevada: CRWMS M&O. ACC: 
MOL.19990409.0102.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 191 March 2000 
CRWMS M&O 1999h. Development of Numerical Grids for UZ Flow and Transport 
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MOL.19990721.0517. 
CRWMS M&O 2000a. Calibrated Properties Model. MDL-NBS-HS-000003. Las 
Vegas, Nevada: CRWMS M&O. ACC: MOL.19990721.0520. URN-0028. URN-0053. 
CRWMS M&O 2000b. Drift-Scale Coupled Processes (DST and THC Seepage) Models. 
MDL-NBS-HS-000001. Las Vegas, Nevada: CRWMS M&O. ACC: 
MOL.19990721.0523. URN-0054. 
CRWMS M&O 2000c. Seepage Calibration Model and Seepage Testing Data. MDLNBS-
HS-000004. Las Vegas, Nevada: CRWMS M&O. ACC: MOL.19990721.0521. 
CRWMS M&O 2000d. Analysis of Hydrologic Properties Data. ANL-NBS-HS- 
000002. Las Vegas, Nevada: CRWMS M&O. ACC: MOL.19990721.0519. URN- 
0055. 
CRWMS M&O 2000e. Geologic Framework Model (GFM3.1) Analysis Model Report. 
Las Vegas, Nevada: CRWMS M&O. 
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Dyer, J.R. 1999. Revised Interim Guidance Pending Issuance of New U.S. Nuclear 
Regulatory Commission (NRC) Regulations (Revision 01, July 22, 1999), for Yucca 
Mountain, Nevada. Letter from J.R. Dyer (DOE) to D.R. Wilkins (CRWMS M&O), 
September 9, 1999, OL&RC:SB-1714, with enclosure, Interim Guidance Pending 
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Dzombak, D.A. and Morel, F.M.M. 1990. Surface Complexation Modeling: Hydrous 
Ferric Oxide. New York, New York, John Wiley & Sons. TIC: 224089.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 192 March 2000 
EPRI 1999. Colloids in Saturated and Partially-Saturated Porous Media: Approaches 
to the Treatment of Colloids in Yucca Mountain Total System Performance Assessment. 
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Solids, Sediments, and Soil under Unsaturated Conditions. 2: Kinetics. Environmental 
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Sorption/Desorption and Dissolution Kinetics. Kluwer Academic Publishers, Boston, 
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Harvey, R.W. and Garabedian, S.P. 1991. Use of Colloid Filtration Theory in Modeling 
Movement of Bacteria through a Contaminated Sandy Aquifer. Environmental Science 
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Effect of Specific Surface Area on Radionuclides Sorption on Crushed Crystalline Rock. 
Material Resources Society Symposium Proceedings, 465, 789796. Pittsburgh, 
Pennsylvania: Materials Resources Society of America. TIC: applied for. 
Hu, Q. and Brusseau, M.L. 1994. Effect of Solute Size on Diffusive-Dispersive 
Transport in Porous Media. Journal of Hydrology, 158, 305317. Amsterdam, The 
Netherlands: Elsevier Science Publishers. TIC: applied for. 
Hu, Q. and Brusseau, M.L. 1995. The Effect of Solute Size on Transport in Structured 
Porous Media. Water Resources Research, 31 (7), 16371646. Washington, D.C.: 
American Geophysical Union. TIC: applied for.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 193 March 2000 
Hu, Q. and Brusseau, M.L. 1996. Transport of Rate-Limited Sorbing Solutes in an 
Aggregated Porous Medium: A Multiprocess Non-Ideality Approach. Journal of 
Contaminant Hydrology, 24 (1), 5373. Amsterdam, The Netherlands: Elsevier Science 
Publishers. TIC: applied for. 
Ibaraki, M. and Sudicky, E.A. 1995. Colloid-Facilitated Contaminant Transport in 
Discretely Fractured Media: 1. Numerical Formulation and Sensitivity Analysis. Water 
Resources Research, 31 (12), 29452960. Washington, D.C.: American Geophysical 
Union. TIC: 245719. 
Jacobsen, O.H.; Moldrup, P.; Larsen, C.; Konnerup, L.; and Peterson, L.W. 1997. 
Particle Transport in Macropores of Undisturbed Soil Columns. Journal Of 
Hydrology, 196, 185203. Amsterdam, The Netherlands: Elsevier Science Publishers. 
TIC: applied for. 
Jahnke, F.M. and Radke, C.J. 1987. Electrolyte Diffusion in Compacted 
Montmorillonite Engineered Barriers. Coupled Processes Associated With Nuclear 
Waste Repositories, 287297. Orlando, Florida: Academic Press. TIC: applied for. 
James, S.C. and Chrysikopoulos, C.V. 1999. Transport of Polydisperse Colloid 
Suspensions in a Single Fracture. Water Resources Research, 35 (3), 707718. 
Washington, D.C.: American Geophysical Union. TIC: 245938. 
Johansson, H.; Byegard, J.; Skarnemark, G.; and Skalberg, M. 1997. Matrix Diffusion 
of Some Alkali and Alkaline Earth Metals in Granitic Rock. Material Resources Society 
Symposium Proceedings, 465, 871878. Pittsburgh, Pennsylvania: Materials Resources 
Society of America. TIC: applied for. 
Johansson, H.; Siitari-Kauppi, M.; Skalberg, M.; and Tullborg, E.L.. 1998. Diffusion 
Pathways in Crystalline Rock-Examples from sp-Diorite and Fine-Grained Granite. 
Journal of Contaminant Hydrology, 35, 4153. Amsterdam, The Netherlands: Elsevier 
Science Publishers. TIC: applied for. 
Kaplan, D.I. and Serne, R.J. 1995. Distribution Coefficient Values Describing Iodine, 
Neptunium, Selenium, Technetium, and Uranium Sorption to Hanford Sediments. PNL- 
10379. Richland, Washington: Pacific Northwest National Laboratory. TIC: applied 
for. 
Kersting, A.B.; Efurd, D.W.; Finnegan, D.L.; Rokop, D.J.; Smith, D.K.; and Thompson, 
J.L. 1999. Migration of Plutonium in Ground Water at the Nevada Test Site. Nature, 
397, 5659. London, England: Macmillan Magazines. TIC: 243597. 
Kretzschmar, R.; Robarge, W.P.; and Amoozegar, A. 1995. Influence of Natural 
Organic Matter on Colloid Transport through Saprolite. Water Resources Research, 31 
(3), 435445. Washington, D.C.: American Geophysical Union. TIC: applied for.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 194 March 2000 
Kretzschmar, R.; Barmettler, K.; Grolimund, D.; Yan, Y.; Borkovec, M.; and Sticher, H. 
1997. Experimental Determination of Colloid Deposition Rates and Collision 
Efficiencies in Natural Porous Media. Water Resources Research, 33 (5), 11291137. 
Washington, D.C.: American Geophysical Union. TIC: applied for. 
Lide, D.R. 1992. CRC Handbook of Chemistry and Physics. 73rd Edition. Boca Raton, 
Florida: CRC Press. TIC: 3595. 
Liu, H.H.; Doughty, C.; and Bodvarsson, G.S. 1998. An Active Fracture Model for 
Unsaturated Flow and Transport in Fractured Rocks. Water Resources Research, 34 
(10), 26332646. Washington, D.C.: American Geophysical Union. TIC: 243012. 
McCarthy, J.F. and Zachara, J.M. 1989. Subsurface Transport of Contaminants. 
Environmental Science and Technology, 23 (5), 496502. Washington, D.C.: American 
Chemical Society. TIC: 224876. 
McGraw, M.A. and Kaplan, D.I. 1997. Colloid Suspension Stability and Transport 
Through Unsaturated Porous Media. PNNL-11565. Richland, Washington: Pacific 
Northwest National Laboratory. TIC: applied for. 
Moridis, G. J. 1992. Alternative Formulations of the Laplace Transform Boundary 
Element (LTBE) Numerical Method for the Solution of Diffusion-Type Equations. 
Boundary Element Technology VII, 815833. Boston, Massachusetts: Computational 
Mechanics Publications. TIC: applied for. 
Moridis, G. J. 1999. Semianalytical Solutions for Parameter Estimation in Diffusion 
Cell Experiments. Water Resources Research, 35 (6), 17291740. Washington, D.C.: 
American Geophysical Union. TIC: 246266. 
Moridis, G.J., and Pruess, K. 1995. Flow and Transport Simulations Using T2CG1, a 
Package of Conjugate Gradient Solvers for the TOUGH2 Family of Codes. Report LBL- 
36235. Berkeley, California: Lawrence Berkeley National Laboratory. TIC: 220015. 
Moridis, G.J. and Pruess, K. 1998. T2SOLV: An Enhanced Package of Solvers for the 
TOUGH2 Family of Reservoir Simulation Codes. Geothermics, 27 (4), 415444. 
Amsterdam, The Netherlands: Elsevier Science Publications. TIC: applied for. 
Moridis, G.J. and Bodvarsson, G.S. 1999. Semianalytical Solutions of Radioactive or 
Reactive Tracer Transport in Layered Fractured Media. LBNL-44155. Berkeley, 
California: Lawrence Berkeley National Laboratory. TIC: applied for. 
Moridis, G.; Wu, Y.; and Pruess, K. 1999. EOS9nT: A TOUGH2 Module for the 
Simulation of Flow and Solute/Colloid Transport. Report LBL-42351. Berkeley, 
California: Lawrence Berkeley National Laboratory. TIC: applied for.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 195 March 2000 
Mualem, Y. 1976. A New Model for Predicting the Hydraulic Conductivity of 
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189196. La Grange Park, Illinois: American Nuclear Society. ACC: 
NNA.19930625.0031. 
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T.; Leung, D.; Masuda, S.; Muraoka, S.; and Ting, D. 1980. Migration of Radionuclides 
through Sorbing Media, Analytical Solutions. Report LBL-11616. Berkeley, California: 
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NUREG/CR-4645, Report LBL-20700. Berkeley, California: Lawrence Berkeley 
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Management, Proceedings of the Fourth Annual International Conference, Las Vegas, 
Nevada, 15091516. LaGrange Park, Illinois: American Nuclear Society. TIC: 226357.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 196 March 2000 
Sakthivadivel, R. 1969. Clogging of Granular Porous Medium by Sediment. Report No. 
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and Groundwater Systems. Soil Science Society America of Journal, 62, 354361. 
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Sudicky, E.A.; Frind, E.O. 1982. Contaminant Transport in Fractured Porous Media: 
Analytical Solutions for a System of Parallel Fractures. Water Resources Research, 18 
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of Selenium in Tuff. Journal of Contaminant Hydrology, 35, 7789. Amsterdam, The 
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van Genuchten, M. 1980. A Closed-Form Equation for Predicting the Hydraulic 
Conductivity of Unsaturated Soils. Soil Science Society of America Journal, 44 (5), 
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Experiments in a Granite Fracture. Journal of Contaminant Hydrology, 21, 269279. 
Amsterdam, the Netherlands: Elsevier Science Publishers. TIC: 245730.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 197 March 2000 
Vilks, P.; Frost, L.H.; Bachinski, D.B. 1997. Field-Scale Colloid Migration 
Experiments in a Granite Fracture. Journal of Contaminant Hydrology, 26, 203214. 
Amsterdam, the Netherlands: Elsevier Science Publishers. TIC: 245732. 
Viswanathan, H.S.; Robinson, B.A.; Valocchi, A.J.; and Triay, I.R. 1998. A Reactive 
Transport Model of Neptunium Migration from the Potential Repository at Yucca 
Mountain. Journal of Hydrology, 209, 251280. Amsterdam, the Netherlands: Elsevier 
Science Publishers. TIC: 243441. 
Wan, J., and J.L. Wilson. 1994. Colloid Transport in Unsaturated Porous Media. 
Water Resources Research, 30 (4), 857864. TIC: 222359. 
Wan, J. and Tokunaga, T.K. 1997. Film Straining of Colloids in Unsaturated Porous 
Media: Conceptual Model and Experimental Testing. Environmental Science and 
Technology, 31 (8), 24132420. Washington, D.C.: American Chemical Society. TIC: 
234804. 
Wemheuer, R.F. 1999. First Issue of FY00 NEPO QAP-2-0 Activity Evaluations. 
Interoffice correspondence from R.F. Wemheuer (CRWMS M&O) to R.A. Morgan 
(CRWMS M&O), October 1, 1999, LV.NEPO.RTPS.TAG.10/99-155, with attachments, 
Activity Evaluation for Work Package #1401213UM1. ACC: MOL.19991028.0162. 
van de Weerd, H. and Leijnse, A. 1997. Assessment of the Effect of Kinetics on Colloid 
Facilitated Radionuclide Transport in Porous Media. Journal of Contaminant 
Hydrology, 26, 245256. Amsterdam, the Netherlands: Elsevier Science Publishers. 
TIC: 245731. 
Wu, Y.S.; Ritcey, A.C.; and Bodvarsson, G.S. 1999. A Modeling Study of Perched 
Water Phenomena in the Unsaturated Zone at Yucca Mountain. Journal of Contaminant 
Hydrology, 38 (1-3), 157184. Amsterdam, the Netherlands: Elsevier Science 
Publishers. TIC: 244160. 
Wu, Y.S.; Ahlers, C.F.; Fraser, P.; Simmons, A.; and Pruess, K. 1996. Software 
Qualification of Selected TOUGH2 Modules. Report LBL-39490. Berkeley, California: 
Lawrence Berkeley National Laboratory. ACC: MOL.19970219.0104. 
Software Cited 
Software Code: TOUGH2 V1.4 Module EOS9 V1.4. STN: 10007-1.4-01. 
Software Code: TOUGH2 V1.11 Module EOS9nT V1.0. CSCI: 10065- 
1.11MEOS9NTV1.0-00. 
Software Code: T2R3D V1.4. STN: 10006-1.4-00. 
Software Code: FRACL V1.0. STN: 10191-1.0-00.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 198 March 2000 
Software routine: xtrqct1.f V1.0. STN: 10213-1.0-00. 
Software routine: xtrqct2.f V1.0. STN: 10214-1.0-00. 
Software routine: xtract2a.f V1.0. STN: 10215-1.0-00. 
Software routine: xtract2b.f V1.0. STN: 10216-1.0-00. 
Software routine: xtract5.f V1.0. STN: 10217-1.0-00. 
Software routine: xtract6.f V1.0. STN: 10218-1.0-00.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 199 March 2000 
8.2 CODES, STANDARDS, REGULATIONS AND PROCEDURES 
64 FR (Federal Register) 8640. Disposal of High-Level Radioactive Waste in a Proposed 
Geologic Repository at Yucca Mountain. Proposed rule 10 CFR (Code of Federal 
Regulations) 63. Readily available. 
AP-3.10Q, Rev. 1, ICN 1. Analyses and Models. Washington, D.C.: U.S. Department of 
Energy, Office of Civilian Radioactive Waste Management. ACC: 
MOL.19991019.0467. 
AP-SI.1Q, Rev. 2, ICN 2. Software Management. Washington, D.C.: U.S. Department 
of Energy, Office of Civilian Radioactive Waste Management. ACC: 
MOL.19991214.0627. 
DOE 1998a. Quality Assurance Requirements and Description. DOE/RW-0333P, REV 
8. Washington D.C.: DOE OCRWM. ACC: MOL.19980601.0022. 
QAP-2-0, Rev. 5. Conduct of Activities. Las Vegas, Nevada: CRWMS M&O. ACC: 
MOL.19980826.0209.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 200 March 2000 
8.3 SOURCE DATA, LISTED BY DATA TRACKING NUMBER 
GS950608312272.001. Chemical Data for Pore Water from Tuff Cores of USW NRG-6, 
NRG7/7A, UZ-14 AND UZ-N55, and UE-25 UZ#16. Submittal date: 05/30/1995. 
GS990308312242.007. Laboratory And Centrifuge Measurements Of Physical And 
Hydraulic Properties Of Core Samples From Busted Butte Boreholes UZTT-BB-INJ-1, 
UZTT-BB-INJ-3, UZTT-BB-INJ-4, UZTT-BB-INJ-6, UZTT-BB-COL-5 and UZTT-BBCOL-
8. Submittal date: 03/22/1999. 
GS990708312242.008. Physical and Hydraulic Properties of Core Samples from Busted 
Butte Boreholes. Submittal date: 07/01/1999. 
LAIT831341AQ96.001. Radionuclide Retardation. Measurements of Batch Sorption 
Distribution Coefficients for Barium, Cesium, Selenium, Strontium, Uranium, Plutonium, 
and Neptunium. Submittal date: 11/12/1996. 
LAJF831222AQ98.007. Chloride, Bromide, and Sulfate Analyses of Salts Leached from 
ECRB-CWAT#1, #2, and #3 Drill core. Submittal date: 09/09/1998. 
LA9909JF831222.010. Chloride, Bromide, Sulfate, and Chlorine-36 Analyses of ESF 
Pore Waters. Submittal date: 09/29/1999. 
LA9909JF831222.012. Chloride, Bromide, and Sulfate Analyses of Porewater Extracted 
from ESF Niche 3566 (Niche #1) and ESF 3650 (Niche #2) Drillcore. Submittal date: 
09/29/1999. 
LA9909WS831372.001. Busted Butte UZ Transport Test: Phase I Collection Pad Extract 
Concentrations. Submittal date: 09/29/1999. 
LA9909WS831372.002. Busted Butte UZ Transport Test: Phase I Collection Pad Tracer 
Loading And Tracer Concentrations. Submittal date: 09/30/1999. 
LA9909WS831372.011. Preliminary Measured Sorption Coefficients. Submittal date: 
10/13/1999. 
LB971212001254.001. DKM Base Case Parameter Set For UZ Model with Mean 
Fracture Alpha, Present Day Infiltration, and Estimated Welded, Non-Welded and 
Zeolitic FMX. Submittal date: 12/12/1997. 
LB990501233129.001. Fracture Properties for the UZ Model Grids and Uncalibrated 
Fracture and Matrix Properties for the UZ Model Layers for AMR U0090, "Analysis of 
Hydrologic Properties Data." Submittal date: 08/25/1999.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 201 March 2000 
LB990701233129.002. 3-D Model Calibration Grid for Calculation of Flow Fields using 
#3 Perched Water Conceptual Model (Non-Perched Water Model). Submittal date: Will 
be submitted with AMR. 
LB990501233129.004. 3-D UZ Model Calibration Grids for AMR U0000, "Development 
of Numerical Grids of UZ Flow and Transport Modeling." Submittal date: 9/24/1999 
LB990801233129.001. TSPA Grid Flow Simulations for AMR U0050, "UZ Flow 
Models and Submodels." (Flow Field #1). Submittal date: 11/29/1999. 
LB990801233129.003. TSPA Grid Flow Simulations for AMR U0050, "UZ Flow 
Models and Submodels." (Flow Field #3). Submittal date: 11/29/1999. 
LB990801233129.004. TSPA Grid Flow Simulations for AMR U0050, "UZ Flow 
Models and Submodels." Submittal date: 11/29/1999. 
LB990801233129.005. TSPA Grid Flow Simulations for AMR U0050, "UZ Flow 
Models and Submodels." (Flow Field #5). Submittal date: 11/29/1999. 
LB990801233129.007. TSPA Grid Flow Simulations for AMR U0050, "UZ Flow 
Models and Submodels." (Flow Field #7). Submittal date: 11/29/1999. 
LB990801233129.009. TSPA Grid Flow Simulations for AMR U0050, "UZ Flow 
Models and Submodels." (Flow Field #9). Submittal date: 11/29/1999. 
LB990801233129.011. TSPA Grid Flow Simulations for AMR U0050, "UZ Flow 
Models and Submodels." (Flow Field #11). Submittal date: 11/29/1999. 
LB990801233129.013. TSPA Grid Flow Simulations for AMR U0050, "UZ Flow 
Models and Submodels." (Flow Field #13). Submittal date: 11/29/1999. 
LB990801233129.015. TSPA Grid Flow Simulations for AMR U0050, "UZ Flow 
Models and Submodels." (Flow Field #15). Submittal date: 11/29/1999. 
LB990801233129.017. TSPA Grid Flow Simulations for AMR U0050, "UZ Flow 
Models and Submodels." (Flow Field #17). Submittal date: 11/29/1999. 
LB990801233129.019. TSPA Grid Flow Simulations for AMR U0050, "UZ Flow 
Models and Submodels." Flow Field #19: Present Day Mean Infiltration Map for Non- 
Perched Water Conceptual Model. Submittal date: will be submitted with AMR. 
LB991131233129.003. Analytical and Simulation Results of Chloride and Chlorine-36 
Analysis. Submittal date: Will be submitted with AMR U0050 (CRWMS M&O, 1999d) 
LB997141233129.001. Calibrated Base Case Infiltration 1-D Parameter Set for the UZ 
Flow and Transport Model, FY99. Submittal date: 07/21/1999.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 202 March 2000 
8.4 OUTPUT DATA, LISTED BY DATA TRACKING NUMBER 
LB991220140160.001. Model Validation using EOS9nT Input and Output file. 
Submittal date: Will be submitted with AMR. 
LB991220140160.002. Model Validation using FRACL Input and Output files. Will be 
submitted with AMR. 
LB991220140160.003. Model Calibration of Chloride in UZ-16 using FRACL Input and 
Output files. Will be submitted with AMR. 
LB991220140160.004. Model Calibration of Chloride in the ESF using FRACL Input 
and Output files. Will be submitted with AMR. 
LB991220140160.005. Model Prediction of Transport in TSw using FRACL Input and 
Output files. Will be submitted with AMR. 
LB991220140160.006. Model Prediction of Sensitivity Studies in tsw35 using FRACL 
Input and Output files. Will be submitted with AMR. 
LB991220140160.007. Model Prediction of Transport in CHn using FRACL Input and 
Output files. Will be submitted with AMR. 
LB991220140160.008. Model Prediction of Transport in PP using FRACL Input and 
Output files. Will be submitted with AMR. 
LB991220140160.009. Model Prediction of Transport Underneath Repository using 
FRACL Input and Output files. Will be submitted with AMR. 
LB991220140160.010. Model Prediction of Busted Butte Using T2R3D Input and 
Output files. Will be submitted with AMR. 
LB991220140160.011. Model Prediction of 3-D Flow using T2R3D Input and Output 
files. Will be submitted with AMR. 
LB991220140160.012. Model Prediction of 3-D Transport, Present-Day Infiltration, #1 
Perched Water Model, using EOS9nT Input and Output files. Will be submitted with 
AMR. 
LB991220140160.013. Model Prediction of 3-D Transport, Monsoon Infiltration, #1 
Perched Water Model, using EOS9nT Input and Output files. Will be submitted with 
AMR. 
LB991220140160.014. Model Prediction of 3-D Transport, Glacial Infiltration, #1 
Perched Water Model, using EOS9nT Input and Output files. Will be submitted with 
AMR.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 203 March 2000 
LB991220140160.015. Model Prediction of 3-D Transport, Present-Day Infiltration, #2 
Perched Water Model, using EOS9nT Input and Output files. Will be submitted with 
AMR. 
LB991220140160.016. Model Prediction of 3-D Transport, Present-Day Infiltration, No 
Perched Water Model, using EOS9nT Input and Output files. Will be submitted with 
AMR. 
LB991220140160.017. Model Prediction of 3-D Colloid Transport, Present-Day 
Infiltration, #1 Perched Water Model, using EOS9nT Input and Output files. Will be 
submitted with AMR. 
LB991220140160.018. Model Prediction of 3-D Site-Scale Radionuclide Transport, 
Present-Day Infiltration, #1 Perched Water Model, using EOS9nT Input and Output files. 
Will be submitted with AMR. 
LB991220140160.019. Parameter values taken and/or computed from information in the 
scientific literatures. These parameter values are used for radionuclide transport analysis. 
Will be submitted with AMR.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 204 March 2000 
INTENTIONALLY LEFT BLANK

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 205 March 2000 
ATTACHMENTS

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 206 March 2000 
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Title:Radionuclide Transport Models Under Ambient Conditions U0060 
ATTACHMENTI 
DISCUSSION OF THE EOS9nT AND FRACL MODELS 
MDL-NBS-HS-000008 REV00 I-1 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
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MDL-NBS-HS-000008 REV00 I-2 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
I.1 THE EOS9nT AND FRACL MODELS 
I.1 TREATMENTOF SPACEAND TIME IN THE MODELS 
I.1.1 Treatment of Space 
The space derivatives in the transport equations of EOS9nT (the numerical 3-D model) are 
discretized following the Integrated Finite Difference method of the TOUGH2 family of codes 
(Pruess 1991). For unconditional monotonicity, upstream weighting is always employed in 
EOS9nT. No space discretization is needed in FRACL, as the solutions are analytical in space. 
I.1.2 Treatment of Time 
FRACL, the 2-D semianalytical model, employs Laplace transforms for the treatment of the time 
derivative. The Laplace space solutions are then inverted numerically to obtain the solution in time. 
EOS9nT allows both conventional timestepping and Laplace transform formulations. 
Using the conventional timestepping approach of TOUGH2 (Pruess 1991), time in EOS9nT is 
discretized using a first-order, fully implicit finite-difference approximation. Radioactive decay 
can be computed either at the middle or the end of the timestep. The residuals are determined, and 
the elements of the Jacobian matrix are computed following the approach described in detail by 
Pruess (1987;1991). The Jacobian is then solved using a set of preconditioned conjugate gradient 
solvers available in TOUGH2 (Moridis and Pruess 1995;1998). The evolution of the timestep size 
in the flow component of EOS9nT is internally controlled by the Newtonian convergence criteria 
(Pruess 1991). 
The timestep size in the n transport equations is specific to each tracer, and is controlled by inputs 
which place limitations on its magnitude based on (a) the user-defined maximum allowed grid 
Courant number and (b) the maximum allowable fraction of the half-life (T1=2) (if radioactive) 
of tracer . It must be pointed out that the fully implicit formulation of EOS9nT with upstream 
weighting does not place any limitations on the Courant number. This is a consideration only in 
explicit schemes. A user-defined maximum allowed Courant number in EOS9nT is a means of 
setting an upper boundary to the timestep magnitude in the transport equations. 
Under transient flow conditions, the time-stepping process in EOS9nT is shown in Figure I.1, in 
which tf is the timestep in the flow equation and tt; is the timestep in the transport equation 
of tracer . A total of n + 1 separate simulation times are independently tracked in EOS9nT (one 
for the flow equation and n for the n tracer transport equations. 
After the flow solution at t + tf is obtained, the water saturations, flow velocities and flow rates 
MDL-NBS-HS-000008 REV00 I-3 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
across the element interfaces are recorded. The time is then reset to t in the transport equation 
of tracer , and the maximum allowable tt; is determined from limitations on the grid Courant 
number and the tracer half life. The tracer transport in the tf interval is simulated using a total 
of k generally unequal time steps, where k  tf =tt;. The process is repeated for all n 
independently-tracked tracers. The time step sizes of the various tracers are not generally equal. 
As the flow field becomes invariant, the size of the tf in TOUGH2 increases, and convergence is 
achieved after a single Newtonian iteration. When this occurs, EOS9nT prints the steady state flow 
solution and continues solving the tracer equations. The time step in the solute transport equations 
becomes uniform and equal to the shortest of the tt;;  = 1; : : : ; n after the flow has reached a 
steady state. 
EOS9nT also allows tracer transport simulations when the initial flow field is time-invariant. In 
this case, EOS9nT solves the flow field only once in order to obtain the constant water saturations, 
flow velocities and flow rates across the element interfaces. After printing the flow data, only the 
tracer transport equations are solved. 
The Courant number limitations may result in a situation where the smallest gridblock controls the 
tt;i, and may result in inefficient simulations and excessive computational times. To partially 
alleviate this problem, EOS9nT determines the tt; from limitation on the Courant numbers at 
gridblocks at which the changes inX are within 5%of the maximum change. This allows timestep 
adjustment by tracking amoving front, and limits Courant number considerations toelements where 
measurable changes occur. 
Figure I.1. Timestepping in EOS9nT. 
MDL-NBS-HS-000008 REV00 I-4 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
I.2 THE LAPLACE TRANSFORM FORMULATIONIN EOS9nT 
I.2.1 Applicability 
This is a EOS9nT option in problems in which the flow field is invariant and solutions are required 
at very large times, the Courant and half-life limitations in conventional timesteping may result in 
tt;i which are too short for an efficient simulation, thus requiring impractically long execution 
times. 
Application of the Laplace space formulation demands strict linearity of (or ability to linearize the) 
problem. Thus, the Laplace formulation in EOS9nT can be invoked under the following conditions: 
(a) The flow field is time-invariant. 
(b) Sorption (physical and/or chemical) follows a linear equilibrium or linear kinetic isotherm. 
(c) Colloid filtration is governed by a linear equilibrium or linear kinetic model. 
(d) Colloid-assisted solute transport is not considered. 
I.2.2 Advantages of the Laplace Transform Formulation 
The major advantage of this formulation is that it eliminates the need for time discretization. It 
yields solutions semi-analytical in time and numerical in space by solving the transformed PDEs 
in the Laplace space, and numerically inverting the solution vectors. Concerns over the effects of 
the numerical treatment of the time dependency on accuracy and stability, which necessitate a large 
number of small time steps between successive observation times in conventional timestepping 
solutions, are rendered irrelevant because time is no longer a consideration. An unlimited time step 
size is thus possible without loss of accuracy or stability. 
Additionally, the Laplace transform formulation significantly reduces numerical dispersion by 
practically eliminating the error associated with the treatment of the time derivative. Sudicky 
(1989, pp: 1844-1845) reported very accurate solutions with grid Peclet numbers in excess of 33 
(more than an order of magnitude larger than the maximum recommended value of 2), and indicated 
that much coarser grid can be employed without loss of accuracy. 
I.2.3 The Laplace Space Transport Equations in EOS9nT 
In its most general form, the Laplace transform of the derivative of the accumulation terms of a 
daughter product  from the decay of parent j (i.e. the left-hand side) in Equation 26 (after the 
incorporation of Equations (3), (7) and (8), see Section 6.3) yields 
MDL-NBS-HS-000008 REV00 I-5 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Lf
dM 
dt 
+ M  j mrMjg 
= h h  bX + (1  ) s bFi(s + )  j mr cMj 
 [ h X;0 + (1  ) s F;0] ; 
(Eq. I.1) 
where s is the Laplace space parameter, ^ = Lfg, Lfg denotes the Laplace transform of the term 
within the brackets, and the subscript 0 of X and F denotes their values at t = 0. 
From a slight manipulation of the equations in Moridis and Bodvarsson (1999), 
bF =  bX +  ; (Eq. I.2) 
where 
 = 
8>
>>>>>>>>>>>>>><>
>>>>>>>>>>>>>>:
w for LE sorption, 
u for LKP or LIP sorption, 
v for LKC sorption, 
w + u for combined LE and LKP/LIP sorption, 
w + v for combined LE and LKC sorption, 
u + v for combined LKP/LIP and LKC sorption, 
(Eq. I.3) 
 = 
8>
>>>>>>>>>>>>>><>
>>>>>>>>>>>>>>:
0 for LE sorption, 
u1 for LKP or LIP sorption, 
v1 for LKC sorption, 
u1 for combined LE and LKP/LIP sorption, 
v1 for combined LE and LKC sorption, 
u1 + v1 for combined LKP/LIP and LKC sorption, 
(Eq. I.4) 
w = KdKi ; u = kp KdKi  
s +  + p kp 
; v = k+
c Ki  
s +  + kc 
; (Eq. I.5) 
and 
u1 = Fp;0 
s +  + p kp 
; v = Fc;0 
s +  + kc 
; (Eq. I.6) 
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Title:Radionuclide Transport Models Under Ambient Conditions U0060 
where the 0 subscript of Fp and Fc denotes their values at t = 0. For non-radioactive substances, 
 = 0, and Equation I.1 through I.6 applyunchanged. The Moridisand Bodvarsson(1999)equation 
bF = p bC +  ; is equivalent to Equation I.2 for p =  . The  term is directly incorporated in the 
 expression, as seen from Equations I.3 and I.5. 
For colloids, the term (1  ) s bF in Equation 8 is replaced by c b, where 
b = 
 
z }| { + K  
s +  +  bX + 
 
z }| { 0 
s +  +  
: (Eq. I.7) 
Thus, Equation I.2 applies after substituting  for F. The 0 subscript in Equation I.6 and I.7 
denotes the value at t = 0. This formulation allows simulation of radioactive true colloids. For 
pseudocolloids,  = 0 in Equation I.7. 
Taking Laplace transform in the right-hand side of Equation 26 (Section 6.3) and combining it with 
Equation I.1 yields 
M bX  
1 
Vn Xm 
Anm hFnm bX  D r bXi= H  j mr cMj ; (Eq. I.8) 
where 
M = [ h  + (1  ) s ](s + ) (Eq. I.9) 
D =  D + (1  ) s s Ds  ; (Eq. I.10) 
H = n h X;0 + (1  ) s [1   (s + i)] Fi;0 + bQo ; (Eq. I.11) 
bQ = Lfqg = 8<: 
qw Xq;=s for a source, 
qw ( bX)n for a sink, 
(Eq. I.12) 
qw is the water mass injection or withdrawal rate, and Xq; is the mass fraction of tracer i in 
the injected stream. In EOS9nT the terms cMj are saved from the simulation of the parent, and 
are subsequently used in the computation of the distribution of any parent. Equations I.8 through 
I.12 apply to both solute and colloid transport by employing the appropriate  and  values, i.e., 
Equations I.3 through I.6 for solutes, or Equation I.7 for colloids. 
MDL-NBS-HS-000008 REV00 I-7 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
I.2.4 Implications for UZ Transport Simulations 
One of the obvious advantages that the Laplace transform formulation affords is that, in the Laplace 
space, it completely linearizes all the kinetic transport equations, which are nonlinear in time for 
conventional timestepping. Thus, the Laplace transform formulation does not increase the order 
of the matrix to be solved. For an implicit solution in conventional timestepping, each kinetic 
equation must be solved separately, in addition to the general transport equation. Thus, the order 
of the matrix increases linearly with the number of kinetic equations. 
For example, to obtain the concentration distribution of a species that follows simultaneously two 
separate kinetic sorption isotherms (combined sorption) in a particular porous medium, the solution 
of a matrix of order 3Ne would be needed, where Ne is the number of elements into which the 
domain is subdivided. Because of the linearity of equations (I.2) to (I.7), the order of the matrix in 
the Laplace space formulation is only Ne. Additionally, the Laplace transforms alleviate accuracy 
problems which may arise from the inaccurate time-weighting of the radioactive decay. More 
specifically, in conventional timestepping, it is not known a-priori whether the mass accumulation 
is correctly represented by using its value at the midpoint or at the end of the timestep. 
I.2.5 The Laplace Space Solutions 
Equation I.8is the Laplacespaceequation of transport inEOS9nT. Theresultingalgebraic equations 
may be written in a general matrix form as:
T ~bX = ~B
; (Eq. I.13) 
where T is the coefficient matrix, ~bX is the vector of the unknowns, and ~B
is the composite vector 
of knowns. 
The Laplace space equations in FRACL are also of the form of the matrix Equation I.13. The 
computation of T and ~B
necessitates values for the s parameter of the Laplace space. These are 
provided by two numerical inversion schemes: the Stehfest algorithm (Stehfest 1970a, b) and the 
De Hoog et al: (1982) method. 
MDL-NBS-HS-000008 REV00 I-8 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
I.3 NUMERICAL INVERSION METHODS OF THE LAPLACE SPACESOLUTIONS 
I.3.1 The Stehfest Algorithm 
For a desired observation time t, the s in the Stehfest algorithm (Stehfest 1970a; 1970b) is real and 
given by 
s = 
ln2 
t  ;  = 1; : : : ;NS (Eq. I.14) 
where NS is the number of summation terms in the algorithm and is an even number. 
The unknown vector ~X
at any time t is obtained by by numerically inverting the Laplace space 
solutions ~bX(s ) according to the equation 
~X
(t) = 
ln2 
t 
NS X=1
W 
~bX(s ) ; (Eq. I.15) 
where 
W = (1)NS 
2 + 
minf;NS 
2 g X k=12 
(+1) 
k 
NS 
2 (2k!) 
(NS 
2  k)!k!(k  1)!(  k)!(2k  )! 
: (Eq. I.16) 
Although the accuracy of the method is theoretically expected to improve with increasing NS, 
Stehfest (1970a, b) showed that with increasing NS the number of correct significant figures 
increases linearly at first and then, due to roundoff errors, decreases linearly. He determined 
that the optimum NS is 10 for single-precision variables (8 significant figures) and 18 for doubleprecision 
variables (16 significant figures). Our experience with T2E9nT indicates that Ns = 16 
or Ns = 18 provide the best results. 
A very important issue on the Stehfest algorithm concerns its behavior in the solution of the 
transport of daughters of radioactive decay. Because the Stehfest s includes only real components, 
the algorithm deteriorates in the solution of the daughter equations (Moridis et al. 1999). Thus, 
its use should be limited to simulations of parents only. 
I.3.2 The De Hoog Method 
In the method of De Hoog et al: (1982), hereafter referred to as the De Hoog method, s is a complex 
number given by Crump (1976) as 
s = s0 +  
T 
j; s0 =   
ln(ER) 
2T 
;  = 1; : : : ;NH (Eq. I.17) 
MDL-NBS-HS-000008 REV00 I-9 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
where 2T istheperiod oftheFourierseries approximatingtheinversefunctionintheinterval [0; 2T ], 
j = p1, and NH = 2MH + 1 is an odd number. Moridis (1992, pp: 815-832) showed that very 
accuratesolutionswereobtainedwhen  = 0, 1012  ER  109,and 0:9 tmax  T  1:1 tmax, 
where tmax is the maximum simulation time. 
The inversion of the Laplace space solution obtained with the De Hoog method is far more 
complicated than in the Stehfest algorithm. The solution ~X
(t) is given by 
~X
(t) = 
1
T 
exp(s0t) Re A2MH 
B2MH  ; (Eq. I.18) 
where 
An = An1 + dn z An2; Bn = Bn1 + dn z Bn2; n = 1; : : : ; 2MH; (Eq. I.19) 
z = expj  t 
T  ; (Eq. I.20) 
A1 = 0; A0 = d0; B1 = B0 = 1 ; (Eq. I.21) 
d0 = a0; d2m1 = q(0) 
m ; d2m = e(0) 
m ; m = 1; : : : ;MH; (Eq. I.22) 
for ` = 1; : : : ;MH; e
(k) 
` = q
(k+1) 
`  q
(k) 
` + e
(k+1) 
`1 ; k = 0; : : : ; 2MH  2` ; 
for ` = 2; : : : ;MH; q
(k) 
` = q
(k+1) 
`1 e
(k+1) 
`1 =e
(k) 
`1; k = 0; : : : ; 2MH  2`  1; 
(Eq. I.23) 
e
(k) 
0 = 0 for k = 0; : : : ; 2MH and q
(k) 
1 = ak+1=ak for k = 0; : : : ; 2MH  1; (Eq. I.24) 
and 
a0 = 
1
2X(s0); ak = X(sk): (Eq. I.25) 
A convergence acceleration is obtained if, on the last evaluation of the recurrence relations, d2MH z 
in (I.19) is replaced by R2MH(z), 
R2MH(z) = h2MH h1 p(1 + d2MH z=h2MH)i; (Eq. I.26) 
where 
h2MH = 
1
2 
[1 + z (d2MH1  d2MH )]; (Eq. I.27) 
giving 
bA2MH = A2MH1 + R2MH A2MH2; bB2MH = B2MH1 + R2MH B2MH2; (Eq. I.28) 
MDL-NBS-HS-000008 REV00 I-10 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
in which case the accelerated solution at a time t is given by replacing A2MH and B2MH by bA2MH 
and bB2MH, respectively, in (I.18). 
Moridis (1992, p: 825) determined that the minimum MH for an acceptable accuracy is 5 
(NH = 11), and that MH  6 (NH  13) provides very accurate solutions. All the operations in 
EquationsI.17throughI.27involvecomplexvariables. Becauseboththerealandtheimaginaryparts 
of the Laplace space solutions are needed to obtain the solution in time, the DeHoog method results 
in a matrix of order 2Ne, i.e., twice as large than the matrix for the Stehfest algorithm. An efficient 
set of Preconditioned Conjugate Gradient (PCG) methods is used to solve the equations. Details 
on the PCG methods and their preconditioning can be found in Moridis and Pruess (1995;1998). 
The increase in the order of the matrix may be outweighed by the unique advantages of the De Hoog 
formulation: is (a) it is capable of accurately inverting very steep solution surfaces (even the step 
function) by increasingMH, (b) produces a very accurate solution, which allows accurate tracking 
of daughter transport (a capability which the Stehfest algorithm does not have), and (c) a whole 
range of solutions at times t in the range [0; T] can be obtained from a single set of solutions X, 
i.e., Equation I.13 need not be solved for each t of interest. This drastically reduces the number of 
times the equations need to solved to cover the desired simulation period. The superior accuracy 
of the De Hoog method allows the very accurate solution of the daughter equations. 
MDL-NBS-HS-000008 REV00 I-11 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
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MDL-NBS-HS-000008 REV00 I-12 March 2000

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-1 March 2000 
ATTACHMENT II 
FIGURES FROM THE STUDY OF TRANSPORT IN THE TSw 
HYDROGEOLOGIC UNIT

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-2 March 2000 
FIGURES 
Page 
II.1. 99Tc Concentration Profile in TSw in Cross Section 1. Results for 1,000 years and 10,000 
years overlap. ...................................................................................................................II-4 
II.2. 237Np Concentration Profile in TSw in Cross Section 1. ................................................II-4 
II.3. 239Pu Concentration Profile in TSw in Cross Section 1.. ............................................... II-5 
II.4. Concentration Profiles in the Matrix at z=10 m and t=1,000 Years................................ II-5 
II.5. 99Tc Concentration Profile in TSw in Cross Section 2. Results for 1,000 years and 10,000 
years overlap. .................................................................................................................. II-6 
II.6. 237Np Concentration Profile in TSw in Cross Section 2. ............................................... II-6 
II.7. 239Pu Concentration Profile in TSw in Cross Section 2. ................................................ II-7 
II.8. 99Tc Concentration Profile in TSw in Cross Section 3. Results for 1,000 years and 10,000 
years overlap. .................................................................................................................. II-7 
II.9. 237Np Concentration Profile in TSw in Cross Section 3. ............................................... II-8 
II.10. 239Pu Concentration Profile in TSw in Cross Section 3. ................................................ II-8 
II.11 Effect of Ki on 99Tc Concentration Profiles Along the z-axis in the 
Fractures at t = 1,000 Years. ........................................................................................... II-9 
II.12. Effect of Ki on 237Np Concentration Profiles Along the z-axis in the 
Fractures at t = 1,000 Years. ........................................................................................... II-9 
II.13. Effect of Ki on 237Np Concentration Profiles Along the x-axis in the Matrix at z=50m and 
t=1,000 Years. ............................................................................................................... II-10 
II.14. Effect of Ki on 239Pu Concentration Profiles along the z-axis in the Fractures at t=1,000 
Years. II-10 
II.15. Effect of Ki on 239Pu Concentration Profiles Along the x-axis in the Matrix at 
z=50 m and t=1,000 Years. ..........................................................................................II-11

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-3 March 2000 
II.16. Effect of Matrix Tortuosity on 99Tc Concentration Profiles Along the z-axis in the 
Fractures at t=1,000 Years. ........................................................................................... II-11 
II.17. Effect of Matrix Tortuosity on 99Tc Concentration Profiles Along the x-axis in the Matrix 
at z=50 m and t=1,000 Years. ....................................................................................... II-12 
II.18. Effect of Matrix Tortuosity on 237Np Concentration Profiles Along the z-axis in the 
Fractures at t=1,000 Years. ........................................................................................... II-12 
II.19. Effect of Matrix Tortuosity on 237Np Concentration Profiles Along the x-axis in the 
Matrix at z=50 m and t=1,000 Years............................................................................. II-13 
II.20. Effect of Matrix Tortuosity on 239Pu Concentration Profiles Along the z-axis in the 
Fractures at t=1,000 Years. ........................................................................................... II-13 
II.21. Effect of Matrix Tortuosity on 239Pu Concentration Profiles Along the x-axis in the Matrix 
at z=50 m and t=1,000 Years. ........................................................................................II-14 
II.22. Effect of aL on 99Tc Concentration Profiles Along the z-axis in the 
Fractures at t=1,000 Years. ........................................................................................... II-14 
II.23. Effect of aL on 237Np Concentration Profiles Along the z-axis in the 
Fractures at t=1,000 Years. ........................................................................................... II-15 
II.24. Effect of aL on 239Pu Concentration Profiles Along the z-axis in the 
Fractures at t=1,000 Years. ........................................................................................... II-15 
11.25 Effect of aL on 239Pu Concentration Profiles Along the x-axis in the 
Matrix at z=50 and t=1,000 Years..................................................................................II-16

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-4 March 2000 
DTN: LB991220140160.005 
Figure II.1. 99Tc Concentration Profile in TSw in Cross Section 1. Results for 1,000 years and 10,000 years overlap. 
DTN: LB991220140160.005 
Figure II.2. 237Np Concentration Profile in TSw in Cross Section 1. 
0.01 
0.10 
1.00 
0 10 20 30 40 
Vertical Distance Within the Topopah Spring Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
1 year 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
tsw36 tsw37 tsw38 tsw39 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 10 20 30 40 
Vertical Distance Within the Topopah Spring Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
1 year 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
tsw36 tsw37 tsw38 tsw39

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-5 March 2000 
DTN: LB991220140160.005 
Figure II.3. 239Pu Concentration Profile in TSw in Cross Section 1.
DTN: LB991220140160.005 
Figure II.4. Concentration Profiles in the Matrix at z=10 m and t=1,000 Years. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 10 20 30 40 
Vertical Distance Within the Topopah Spring Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
1 year 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
tsw36 tsw37 tsw38 tsw39 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0.0 0.1 0.2 0.3 0.4 0.5 0.6 
Horizontal Distance X (m) 
Relative Concentration (C/Co) 
Tc 
Np 
Pu

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-6 March 2000 
DTN: LB991220140160.005 
Figure II.5. 99Tc Concentration Profile in TSw in Cross Section 2. Results for 1,000 years and 10,000 years overlap. 
DTN: LB991220140160.005 
Figure II.6. 237Np Concentration Profile in TSw in Cross Section 2. 
0.01 
0.10 
1.00 
0 20 40 60 80 100 120 140 
Vertical Distance Within the Topopah Spring Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
1 year 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
tsw36 tsw37 tsw38
tsw39 
tsw35 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 20 40 60 80 100 120 140 
Vertical Distance Within the Topopah Spring Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
1 year 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
tsw36 tsw37 tsw38
tsw39 
tsw35

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-7 March 2000 
DTN: LB991220140160.005 
Figure II.7. 239Pu Concentration Profile in TSw in Cross Section 2. 
DTN: LB991220140160.005 
Figure II.8. 99Tc Concentration Profile in TSw in Cross Section 3. Results for 1,000 years and 10,000 years overlap. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 20 40 60 80 100 120 140 
Vertical Distance Within the Topopah Spring Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
1 year 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
tsw36 tsw37 tsw38
tsw39 
tsw35 
0.01 
0.10 
1.00 
0 20 40 60 80 100 
Vertical Distance Within the Topopah Spring Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
1 year 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
tsw36 tsw37 tsw38 tsw39 tsw35

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-8 March 2000 
DTN: LB991220140160.005 
Figure II.9. 237Np Concentration Profile in TSw in Cross Section 3. 
DTN: LB991220140160.005 
Figure II.10. 239Pu Concentration Profile in TSw in Cross Section 3. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 20 40 60 80 100 
Vertical Distance Within the Topopah Spring Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
1 year 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
tsw36 tsw37 tsw38 tsw39 tsw35 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 20 40 60 80 100 
Vertical Distance Within the Topopah Spring Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
1 year 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
tsw36 tsw37 tsw38 tsw39 tsw35

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-9 March 2000 
DTN: LB991220140160.006 
Figure II.11 Effect of Ki on 99Tc Concentration Profiles Along the z-axis in the Fractures at t = 1,000 Years. 
DTN: LB991220140160.006 
Figure II.12. Effect of Ki on 237Np Concentration Profiles Along the z-axis in the Fractures at t = 1,000 Years. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 500 1000 1500 2000 2500 3000 3500 
Vertical Distance Z (m) 
Relative Concentration (C/Co) 
Ki=1 
Ki=0.5 
Ki=0.1 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 200 400 600 800 1000 1200 1400 1600 
Vertical Distance Z (m) 
Relative Concentration (C/Co) 
Ki=1 
Ki=0.5 
Ki=0.1

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-10 March 2000 
DTN: LB991220140160.006 
Figure II.13. Effect of Ki on 237Np Concentration Profiles Along the x-axis in the Matrix z=50m and t=1,000 Years. 
DTN: LB991220140160.006 
Figure II.14. Effect of Ki on 239Pu Concentration Profiles Along the z-axis in the Fractures at t=1,000 Years. 
0.0 
0.2 
0.4 
0.6 
0.8 
1.0 
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 
Horizontal Distance X (m) 
Relative Concentration (C/Co) 
Ki=1 
Ki=0.5 
Ki=0.1 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 
Vertical Distance Z (m) 
Relative Concentration (C/Co) 
Ki=1 
Ki=0.5 
Ki=0.1

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-11 March 2000 
DTN: LB991220140160.006 
Figure II.15. Effect of Ki on 239Pu Concentration Profiles Along the x-axis in the Matrix at z=50 m and t=1,000 Years. 
DTN: 991220140160.006 
Figure II.16. Effect of Matrix Tortuosity on 99Tc Concentration Profiles Along the z-axis in the Fractures at t=1,000 
Years. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 
Horizontal Distance X (m) 
Relative Concentration (C/Co) 
Ki=1 
Ki=0.5 
Ki=0.1 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 1000 2000 3000 4000 5000 6000 7000 
Vertical Distance Z (m) 
Relative Concentration (C/Co) 
tort=0.2*phi 
tort=1*phi 
tort=5*phi

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-12 March 2000 
DTN: LB991220140160.006 
Figure II.17. Effect of Matrix Tortuosity on 99Tc Concentration Profiles Along the x-axis in the Matrix at Z=50 m and 
t=1,000 Years. 
DTN: LB991220140160.006 
Figure II.18. Effect of Matrix Tortuosity on 237Np Concentration Profiles Along the z-axis in the Fractures at t=1,000 
Years. 
0.6 
0.7 
0.8 
0.9 
1.0 
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 
Horizontal Distance X (m) 
Relative Concentration (C/Co) 
tort=0.2phi 
tort=1*phi 
tort=5*phi 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 200 400 600 800 1000 1200 
Vertical Distance Z (m) 
Relative Concentration (C/Co) 
tort=0.2*phi 
tort=1*phi 
tort=5*phi

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-13 March 2000 
DTN: LB991220140160.006 
Figure II.19. Effect of Matrix Tortuosity on 237Np Concentration Profiles Along the x-axis in the Matrix at Z=50 m and 
t=1,000 Years 
DTN: LB991220140160.006 
Figure II.20. Effect of Matrix Tortuosity on 239Pu Concentration Profiles Along the z-axis in the Fractures at t=1,000 
Years 
0.0 
0.2 
0.4 
0.6 
0.8 
1.0 
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 
Horizontal Distance X (m) 
Relative Concentration (C/Co) 
tort=0.2*phi 
tort=1*phi 
tort=5*phi 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 
Vertical Distance Z (m) Relative Concentration (C/Co) 
tort=0.2*phi 
tort=1*phi 
tort=5*phi

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-14 March 2000 
DTN: LB991220140160.006 
Figure II.21. Efffect of Matrix Tortuosity on 239Pu Concentration Profiles Along the z-axis in the Matrix at Z=50 m and 
t=1,000 Years. 
DTN: LB991220140160.006 
Figure II.22. Effect of aL on 99Tc Concentration Profiles Along the z-axis in the Fractures at t=1,000 Years. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00
0.00 0.05 0.10 0.15 0.20 
Horizontal Distance X (m) 
Relative Concentration (C/Co) 
tort=0.2*phi 
tort=1*phi 
tort=5*phi 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 500 1000 1500 2000 2500 3000 3500 
Vertical Distance Z (m) 
Relative Concentration (C/Co) 
aLf=0.1 m 
aLf=1 m 
aLf=10 m

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-15 March 2000 
DTN: LB991220140160.006 
Figure II.23. Effect of aL on 237Np Concentration Profiles Along the z-axis in the Fractures at t=1,000 Years. 
DTN: LB991220140160.006 
Figure II.24. Effect of aL on 239Pu Concentration Profiles Along the z-axis in the Fractures at t=1,000 Years. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 200 400 600 800 
Vertical Distance Z (m) 
Relative Concentration (C/Co) 
aLf=0.1 m 
aLf=1 m 
aLf=10 m 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 
Vertical Distance Z (m) 
Relative Concentration (C/Co) 
aLf=0.1 m 
aLf=1 m 
aLf=10 m

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 II-16 March 2000 
Figure II.24. Effect of aL on 239Pu Concentration Profiles Along the X-axis in the Matrix at z=50 m and t=1,000 Years. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00
0.00 0.05 0.10 0.15 0.20 0.25 0.30 
Horizontal Distance X (m) 
Relative Concentration (C/Co) 
aLf=0.1 m 
aLf=1 m 
aLf=10 m

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 III-1 March 2000 
ATTACHMENT III 
FIGURES FROM THE STUDY OF TRANSPORT IN THE CHn 
HYDROGEOLOGIC UNIT

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 III-2 March 2000 
FIGURES 
Page 
III.1 99Tc Concentration Profile in CHn in Cross Section 1. Results for 10,000 Years and 
100,000 Years Overlap.................................................................................................. III-3 
III.2 237Np Concentration Profile CHn in Cross Section 1 ................................................... III-3 
III.3 239Pu Concencentration Profile in CHn in Cross Section 1........................................... III-4 
III.4 99Tc Concentration Profile in CHn in Cross Section 2. Results for 10,000 Years and 
100,000 Years Overlap .................................................................................................. III-4 
III.5 237Np Concentration Profile in CHn in Cross Section 2 .............................................. III-5 
III.6 239Pu Concentration Profile in CHn in Cross Section 2. Results for 10 Years and 100 Years 
Overlap .......................................................................................................................... III-5 
III.7 99Tc Concentration Profile in CHn in Cross Section 3. Results for 10,000 Years and 
100,000 Years Overlap.................................................................................................. III-6 
III.8 237Np Concentration Profile in CHn in Cross Section 3. Results for 10,000 Years and 
100,000 Years Overlap .................................................................................................. III-6 
III.9 239Pu Concentration Profile in CHn in Cross Section 3 ............................................... III-7

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 III-3 March 2000 
DTN: LB991220140160.007 
Figure III.1. 99Tc Concentration Profile in CHn in Cross Section 1. Results for 10,000 years and 100,000 years overlap. 
DTN: LB991220140160.007 
Figure III.2. 237Np Concentration Profile in CHn in Cross Section 1. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 10 20 30 40 50 
Vertical Distance Within the Calico Hills Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
ch1v ch5v ch6z ch2v ch3v ch4v 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 10 20 30 40 50 
Vertical Distance Within the Calico Hills Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
ch1v ch5v ch6z ch2v ch3v ch4v

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 III-4 March 2000 
DTN: LB991220140160.007 
Figure III.3 239Pu Concentration Profile CHn in Cross Section 1. 
DTN: LB991220140160.007 
Figure III.4. 99Tc Concentration Profile in CHn in Cross Section 2. Results for 10,000 years and 100,000 years overlap. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 10 20 30 40 50 
Vertical Distance Within the Calico Hills Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
ch1v ch5v ch6z ch2v ch3v ch4v 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00
0 10 20 30 40 50 60 70 80 90 
Vertical Distance Within the Calico Hills Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
ch1v ch5z ch6z ch2v ch3v ch4v

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 III-5 March 2000 
DTN: LB991220140160.007 
Figure III.5. 237Np Concentraion Profile CHn in Cross Section 2. 
DTN: LB991220140160.007 
Figure III.6. 239Pu Concentration Profile in CHn in Cross Section 2. Results for 10 years and 100 years overlap. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00
0 10 20 30 40 50 60 70 80 90 
Vertical Distance Within the Calico Hills Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
ch1v ch5z ch6z ch2v ch3v ch4v 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00
0 10 20 30 40 50 60 70 80 90 
Vertical Distance Within the Calico Hills Hydrogeologic 
Units (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
ch1v ch5z ch6z ch2v ch3v ch4v

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 III-6 March 2000 
DTN: LB991220140160.007 
Figure III.7. 99Tc Concentration Profile in CHn in Cross Section 3. Results for 10,000 years and 100,000 years overlap. 
DTN: LB991220140160.007 
Figure III.8. 237Np Concentration Profile in CHn in Cross Section 3. Results for 10,000 years and 100,000 years overlap. 
0.6 
0.7 
0.8 
0.9 
1.0 
0 20 40 60 80 100 
Vertical Distance Within the Calico Hills Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
ch1z ch5z ch6z ch2z ch3z ch4z 
1.E-06 
1.E-04 
1.E-02 
1.E+00 
0 20 40 60 80 100 
Vertical Distance Within the Calico Hills Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
ch1z ch5z ch6z ch2z ch3z ch4z

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 III-7 March 2000 
DTN: LB991220140160.007 
Figure III.9. 239Pu Concentration Profile in CHn in Cross Section 3. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 20 40 60 80 100 
Vertical Distance Within the Calico Hills Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
ch1z ch5z ch6z ch2z ch3z ch4z

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 IV-1 March 2000 
ATTACHMENT IV 
FIGURES FROM THE STUDY OF TRANSPORT IN THE PP 
HYDROGEOLOGIC UNIT

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 IV-2 March 2000 
FIGURES 
Page 
IV.1 99Tc Concentration Profile in PP in Cross Section 1. Results for 10,000 years and 100,000 
years overlap. ................................................................................................................. IV-3 
IV.2 237Np Concentration Profile in PP in Cross Section 1. ................................................. IV-3 
IV.3 239Pu Concentration Profile in PP in Cross Section 1. ................................................ IV-4 
IV.4 99Tc Concentration Profile in PP in Cross Section 2. Results for 10,000 years and 100,000 
years overlap. ................................................................................................................ IV-4 
IV.5 237Np Concentration Profile in PP in Cross Section 2.................................................. IV-5 
IV.6 239Pu Concentration Profile in PP in Cross Section 2. ................................................. IV-5 
IV.7 99Tc Concentration Profile in PP in Cross Section 3. Results for 10,000 years and 100,000 
years overlap. ................................................................................................................ IV-6 
IV.8 237Np Concentration Profile in PP in Cross Section 3.................................................. IV-6 
IV.9 239Pu Concentration Profile in PP in Cross Section 3. ................................................. IV-7

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 IV-3 March 2000 
DTN: LB991220140160.008 
Figure IV.1. 99Tc Concentration Profile in PP in Cross Section 1. Results for 10,000 years and 100,000 years overlap. 
DTN: LB991220140160.008 
Figure IV.2. 237Np Concentration Profile in PP in Cross Section 1. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 20 40 60 80 100 120 
Vertical Distance Within the Prow Pass Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 year 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
pp4 pp3 pp2 pp1 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 20 40 60 80 100 120 
Vertical Distance Within the Prow Pass Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 year 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
pp4 pp1 pp3 pp2

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 IV-4 March 2000 
DTN: LB991220140160.008 
Figure IV.3. 239Pu Concentration Profile in PP in Cross Section 1. 
DTN: LB991220140160.008 
Figure IV.4. 99Tc Concentration Profile in PP in Cross Section 2. Results for 10,000 years and 100,000 years overlap. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 20 40 60 80 100 120 
Relative Concentration (C/Co) 
10 year 
100 yrs 
1.000 yrs 
10,000 yrs 
100,000 yrs 
pp4 pp1 pp3 pp2 
Vertical Distance Within the Prow Pass Hydrogeologic Units (m) 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 20 40 60 80 100 
Relative Concentration (C/Co) 
10 year 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
pp4 pp3 pp2 pp1 
Vertical Distance Within the Prow Pass Hydrogeologic Units (m)

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 IV-5 March 2000 
DTN: LB991220140160.008 
Figure IV.5. 237Np Concentration Profile in PP in Cross Section 2. 
DTN: LB991220140160.008 
Figure IV.6. 239Pu Concentration Profile in PP in Cross Section 2. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 20 40 60 80 100 
Vertical Distance Within the Prow Pass Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 year 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
pp4 pp1 pp3 pp2 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 20 40 60 80 100 
Vertical Distance Within the Prow Pass Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 year 
100 yrs 
1.000 yrs 
10,000 yrs 
100,000 yrs 
pp4 pp1 pp3 pp2

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 IV-6 March 2000 
DTN: LB991220140160.008 
Figure IV.7. 99Tc Concentration Profile in PP in Cross Section 3. Results for 10,000 years and 100,000 years overlap. 
DTN: LB991220140160.008 
Figure IV.8. 237Np Concentration Profile in PP in Cross Section 3. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00
0 10 20 30 40 50 60 70 80 
Vertical Distance Within the Prow Pass Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 year 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
pp4 pp3 pp2 pp1 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00
0 10 20 30 40 50 60 70 80 
Vertical Distance Within the Prow Pass Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 year 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
pp4 pp1 pp3 pp2

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 IV-7 March 2000 
DTN: LB991220140160.008 
Figure IV.9. 239Pu Concentration Profile in PP in Cross Section 3. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00
0 10 20 30 40 50 60 70 80 
Vertical Distance Within the Prow Pass Hydrogeologic Units (m) 
Relative Concentration (C/Co) 
10 year 
100 yrs 
1.000 yrs 
10,000 yrs 
100,000 yrs 
pp4 pp1 pp3 pp2

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 V-1 March 2000 
ATTACHMENT V 
FIGURES FROM THE STUDY OF TRANSPORT UNDERNEATH THE REPOSITORY

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 V-2 March 2000 
FIGURES 
Page 
V.1. 99Tc Concentration Profile Under the Potential Repository in Cross Section 1 (Mean 
Present-Day Infiltration, No Perched Water). Results for 10,000 years and 100,000 
years overlap. ............................................................................................................V-4 
V.2. 237Np Concentration Profile Under the Potential Repository in Cross Section 1 (Mean 
Present-Day Infiltration, No Perched Water). ...........................................................V- 4 
V.3. 239Pu Concentration Profile Under the Potential Repository in Cross Section 1 (Mean 
Present-Day Infiltration, No Perched Water). ............................................................V-5 
V.4. 99Tc Concentration Profile Under the Potential Repository in Cross Section 1 (High 
Glacial Infiltration, No Perched Water). Results for 10,000 years and 100,000 years 
overlap........................................................................................................................V-5 
V.5. 237Np Concentration Profile Under the Potential Repository in Cross Section 1 (High 
Glacial Infiltration, No Perched Water). ................................................................... V-6 
V.6. 239Pu Concentration Profile Under the Potential Repository in Cross Section 1 (High 
Glacial Infiltration, No Perched Water). ................................................................... V-6 
V.7. 99Tc Concentration Profile Under the Potential Repository in Cross Section 2 (Mean 
Present-Day Infiltration, No Perched Water). Results for 10,000 years and 100,000 
years overlap. ............................................................................................................ V-7 
V.8. 237Np Concentration Profile Under the Potential Repository in Cross Section 2 (Mean 
Present-Day Infiltration, No Perched Water). ........................................................... V-7 
V.9. 239Pu Concentration Profile Under the Potential Repository in Cross Section 2 (Mean 
Present-Day Infiltration, No Perched Water). ........................................................... V-8 
V.10. 99Tc Concentration Profile Under the Potential Respository in Cross Section 2 (High 
Glacial Infiltration, No Perched Water). Results for 1,000 years, 10,000 years and 
100,000 years overlap. .............................................................................................. V-8 
V.11. 237Np Concentration Profile Under the Potential Repository in Cross Section 2 (High 
Glacial Infiltration, No Perched Water). Results for 10,000 years and 100,000 years 
almost overlap. ..........................................................................................................V-9

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 V-3 March 2000 
V.12. 239Pu Concentration Profile Under the Potential Repository in Cross Section 2 (High 
Glacial Infiltration, No Perched Water). ................................................................... V-9 
V.13. 99Tc Concentration Profile Under the Potential Repository in Cross Section 3 (Mean 
Present-Day Infiltration, No Perched Water). Results for 10,000 years and 100,000 
years overlap. .......................................................................................................... V-10 
V.14. 237Np Concentration Profile Under the Potential Repository in Cross Section 3 (Mean 
Present-Day Infiltration, No Perched Water). ......................................................... V-10 
V.15. 239Pu Concentration Profile Under the Potential Repository in Cross Section 3 (Mean 
Present-Day Infiltration, No Perched Water). .........................................................V-11 
V.16. 99Tc Concentration Profile Under the Potential Repository in Cross Section 3 (High 
Glacial Infiltration, No Perched Water). Results for 1,000 years, 10,000 and 100,000 
years overlap. .......................................................................................................... V-11 
V.17. 237Np Concentration Profile Under the Potential Repository in Cross Section 3 (High 
Glacial Infiltration, No Perched Water). Results for 10,000 and 100,000 years overlap. 
................................................................................................................................V-12 
V.18. 239Pu Concentration Profile Under the Potential Repository in Cross Section 3 (High 
Glacial Infiltration, No Perched Water). ................................................................. V-12 
V.19. 99Tc Concentration Profile Under the Potential Repository in Cross Section 3 for a 
Perched Water Regime (Mean Present-Day Infiltration). Results for 10,000 years and 
100,000 years overlap. ............................................................................................ V-13 
V.20. 237Np Concentration Profile Under the Potential Repository in Cross Section 3 for a 
Perched Water Regime (Mean Present-Day Infiltration). ....................................... V-13 
V.21. 239Pu Concentration Profile Under the Potential Repository in Cross Section 3 for a 
Perched Water Regime (Mean Present-Day Infiltration). ....................................... V-14

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 V-4 March 2000 
DTN: LB991220140160.009 
Figure V.1. 99Tc Concentration Profile Under the Potential Repository in Cross Section 1 (Mean Present-Day 
Infiltration, No Perched Water). Results for 10,000 years and 100,000 years overlap. 
DTN: LB991220140160.009 
Figure V.2. 237Np Concentration Profile Under the Potential Repository in Cross Section 1 (Mean Present-Day 
Infiltration, No Perched Water). 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36-39 bf3 ch(1-5)v pp4 pp3 pp2 ch6z pp1 bf2 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36-39 bf3 ch(1-5)v pp4 pp3 pp2 ch6z pp1 bf2

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 V-5 March 2000 
DTN: LB991220140160.009 
Figure V.3. 239Pu Concentration Profile Under the Potential Repository in Cross Section 1 (Mean Present-Day 
Infiltration, No Perched Water). 
DTN: LB991220140160.009 
Figure V.4. 99Tc Concentration Profile Under the Potential Repository in Cross Section 1 (High Glacial Infiltration, No 
Perched Water). Results for 10,000 years and 100,000 years overlap. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36-39 bf2 bf3 ch(1-5)v pp4 pp3 pp2 ch6z pp1 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0.0 0.1 0.2 0.3 0.4 0.5 0.6 
Horizontal Distance X (m) 
Relative Concentration (C/Co) 
Tc 
Np 
Pu

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 V-6 March 2000 
DTN: LB991220140160.009 
Figure V.5. 237Np Concentration Profile Under the Potential Repository in Cross Section 1 (High Glacial Infiltration, No 
Perched Water). 
DTN: LB991220140160.009 
Figure V.6. 239Pu Concentration Profile Under the Potential Repository in Cross Section 1 (High Glacial Infiltration, No 
Perched Water). 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36-39 bf3 bf2 ch(1-5)v pp4 pp3 pp2 ch6z pp1 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36-39 bf3 bf2 ch(1-5)v pp4 pp3 pp2 ch6z pp1

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 V-7 March 2000 
DTN: LB991220140160.009 
Figure V.7. 99Tc Concentration Profile Under the Potential Repository in Cross Section 2 (Mean Present-Day Infiltration, 
No Perched Water). Results for 10,000 years and 100,000 years overlap. 
DTN: LB991220140160.009 
Figure V.8. 237Np Concentration Profile Under the Potential Repository in Cross Section 2 (Mean Present-Day 
Infiltration, No Perched Water). 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 tsw38 
tsw39
ch1v
ch2v 
pp4 pp3 pp2 
ch6z 
pp1 ch5z 
ch4v 
ch3v tsw35 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 tsw38 
tsw39
ch1v
ch2v 
pp4 pp3 pp2 
ch6z 
pp1 ch5z 
ch4v 
ch3v tsw35

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 V-8 March 2000 
DTN: LB991220140160.009 
Figure V.9. 239Pu Concentration Profile Under the Potential Repository in Cross Section 2 (Mean Present-Day 
Infiltration, No Perched Water). 
DTN: LB991220140160.009 
Figure V.10. 99 Tc Concentration Profile Under the Potential Respository in Cross Section 2 (High Glacial Infiltration, No 
Perched Water). Results for 1,000 years, 10,000 years and 100,000 years overlap. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 tsw38 
tsw39
ch1v
ch2v 
pp4 pp3 pp2 
ch6z 
pp1 ch5z 
ch4v 
ch3v tsw35 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 tsw38 
tsw39
ch1v
ch2v 
pp4 pp3 pp2 
ch6z 
pp1 ch5z 
ch4v 
ch3v tsw35

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 V-9 March 2000 
DTN: LB991220140160.009 
Figure V.11. 237Np Concentration Profile Under the Potential Repository in Cross Section 2 (High Glacial Infiltration, No 
Perched Water). Results for 10,000 years and 100,000 years almost overlap. 
DTN: LB991220140160.009 
Figure V.12. 239Pu Concentration Profile Under the Potential Repository in Cross Section 2 (High Glacial Infiltration, No 
Perched Water). 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 tsw38 
tsw39
ch1v
ch2v 
pp4 pp3 pp2 
ch6z 
pp1 ch5z 
ch4v 
ch3v tsw35 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 tsw38 
tsw39
ch1v
ch2v 
pp4 pp3 pp2 
ch6z 
pp1 ch5z 
ch4v 
ch3v tsw35

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 V-10 March 2000 
DTN: LB991220140160.009 
Figure V.13. 99Tc Concentration Profile Under the Potential Repository in Cross Section 3 (Mean Present-Day 
Infiltration, No Perched Water). Results for 10,000 years and 100,000 years overlap. 
. 
DTN: LB991220140160.009 
Figure V.14. 237Np Concentration Profile Under the Potential Repository in Cross Section 3 (Mean Present-Day 
Infiltration, No Perched Water). 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 
tsw38
tsw39
ch1z ch2z pp4 pp3 pp2 ch6z pp1 ch5z ch4z ch3z 
tsw35 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 
tsw38
tsw39
ch1z ch2z pp4 pp3 pp2 ch6z pp1 ch5z ch4z ch3z 
tsw35

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 V-11 March 2000 
DTN: LB991220140160.009 
Figure V.15. 239Pu Concentration Profile Under the Potential Repository in Cross Section 3 (Mean Present-Day 
Infiltration, No Perched Water). 
DTN: LB991220140160.009 
Figure V.16. 99Tc Concentration Profile Under the Potential Repository in Cross Section 3 (High Glacial Infiltration, No 
Perched Water). Results for 1,000 years, 10,000 and 100,000 years overlap. 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 
tsw38
tsw39
ch1z ch2z pp4 pp3 pp2 ch6z pp1 ch5z ch4z ch3z 
tsw35 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 
tsw38
tsw39
ch1z ch2z pp4 pp3 pp2 ch6z pp1 ch5z ch4z ch3z 
tsw35

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 V-12 March 2000 
DTN: LB991220140160.009 
Figure V.17. 237Np Concentration Profile Under the Potential Repository in Cross Section 3 (High Glacial Infiltration, No 
Perched Water). Results for 10,000 and 100,000 years overlap. 
DTN: LB991220140160.009 
Figure V.18. 239Pu Concentration Profile Under the Potential Repository in Cross Section 3 (High Glacial Infiltration, No 
Perched Water). 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 
tsw38
tsw39
ch1z ch2z pp4 pp3 pp2 ch6z pp1 ch5z ch4z ch3z 
tsw35 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 
tsw38
tsw39
ch1z ch2z pp4 pp3 pp2 ch6z pp1 ch5z ch4z ch3z 
tsw35

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 V-13 March 2000 
DTN: LB991220140160.009 
Figure V.19. 99Tc Concentration Profile Under the Potential Repository in Cross Section 3 for a Perched Water Regime 
(Mean Present-Day Infiltration). Results for 10,000 years and 100,000 years overlap. 
DTN: LB991220140160.009 
Figure V.20. 237Np Concentration Profile Under the Potential Repository in Cross Section 3 for a Perched Water 
Regime (Mean Present-Day Infiltration). 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 
tsw38
tsw39
ch1z ch2z pp4 pp3 pp2 ch6z pp1 ch5z ch4z ch3z 
tsw35 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 
tsw38
tsw39
ch1z ch2z pp4 pp3 pp2 ch6z pp1 ch5z ch4z ch3z 
tsw35

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 V-14 March 2000 
DTN: LB991220140160.009 
Figure V.21. 239Pu Concentration Profile Under the Potential Repository in Cross Section 3 for a Perched Water 
Regime (Mean Present-Day Infiltration). 
1.E-12 
1.E-09 
1.E-06 
1.E-03 
1.E+00 
0 50 100 150 200 250 300 
Vertical Distance Below the Potential Repository (m) 
Relative Concentration (C/Co) 
10 yrs 
100 yrs 
1,000 yrs 
10,000 yrs 
100,000 yrs 
tsw36 tsw37 
tsw38
tsw39
ch1z ch2z pp4 pp3 pp2 ch6z pp1 ch5z ch4z ch3z 
tsw35

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 VI-1 March 2000 
ATTACHMENT VI 
FIGURES FROM THE BUSTED BUTTE STUDIES

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 VI-2 March 2000 
FIGURES 
Page 
VI.1 Schematic Illustration of Borehole Layout in the Phase 1A Test, Busted Butte 
(Not to Scale) .........................................................................................................VI-3 
VI.2 Predicted Nonsorbing Bromide Tracer Distribution after 285 Days for Borehole 3 
(S1A Flow Parameters) ..........................................................................................VI-3 
VI.3 Predicted Nonsorbing Bromide Tracer Distribution after 285 Days for Borehole 3 
(S2A Flow Parameters) ...........................................................................................VI-4 
VI.4 Predicted Nonsorbing Bromide Tracer Distribution after 285 Days for Borehole 1 
(S1A Flow Parameters) ...........................................................................................VI-4 
VI.5 Pedicted Nonsorbing Bromide Tracer Distribution after 285 days for Borehole 4 
(S1A Flow Parameters) ...........................................................................................VI-5 
VI.6 Schematic Illustration of Injection/Collection Boreholes 5 and 6 and Collection 
Locations in Borehole 6 in the Phase 1B Test, Busted Butte (Not to Scale) ..........VI-5 
VI.7 Predicted Bromide Breakthrough Curves at Different Collection Locations in 
Borehole 6 (S1A Flow Parameters) ........................................................................VI-6 
VI.8 Predicted Bromide Breakthrough Curves at Different Collection Locations in 
Borehole 6 (S2B Flow Parameters) ........................................................................VI-6 
VI.9 Predicted Liquid Saturation at Different Collection Locations in Borehole 6 
(S1A Flow Parameters) ..........................................................................................VI-7 
VI.10 Predicted Liquid Saturation at Different Collection Locations in Borehole 6 
(S2B Flow Parameters) ...........................................................................................VI-7 
VI.11 Predicted 2,6-DFBA Breakthrough Curve at Different Collection Locations in 
Borehole 6 (S1A Flow Parameters) .......................................................................VI-8 
VI.12 Predicted Lithium Breakthrough Curve at Different Collection Locations in Borehole 
6 (K_d=2 mL/mg; S1A Flow Parameters) .............................................................VI-8 
VI.13 Predicted Lithium Breakthrough Curve at Different Collection Locations in Borehole 
6 (K_d=2 mL/mg; S2B Flow Parameters)..............................................................VI-9

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 VI-3 March 2000 
Figure V1.1. Schematic Illustration of Borehole Layout in the Phase 1A Test, Busted Butte (Not to Scale). 
DTN: LB991220140160.010 
Figure VI.2. Predicted Nonsorbing Bromide Tracer Distribution after 285 Days for Borehole 3 (S1A Flow Parameters). 
Interface 
ch1v 
ch2v 
Borehole 1 
Borehole 3 
Borehole 4 
Borehol 2 
up 
X (m) 
Z (m) 
0 1 2 3 
-3 
-2 
-1
0 
1.00 
0.90 
0.75 
0.50 
0.25 
0.10 
0.02 
Busted Butte 
Phase 1A test 
Borehole 3 
interface 20 cm below the injection 
injection rate 10 mL/hr 
initial saturation 0.30 
ch1v 
ch2v 
C/Co

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 VI-4 March 2000 
DTN: LB991220140160.010 
Figure VI. 3 Predicted Nonsorbing Bromide Tracer Distribution after 285 Days for Borehole 3 (S2A Flow Parameters). 
DTN: LB991220140160.010 
Figure VI.4. Predicted Nonsorbing Bromide Tracer Distribution after 285 Days for Borehole 1 
(S1A Flow Parameters). 
X (m) 
Z (m) 
0 1 2 3 
-3 
-2 
-1
0 
1.00 
0.90 
0.75 
0.50 
0.25 
0.10 
0.02 
Busted Butte 
Phase 1A test 
Borehole 3 
interface 20 cm below the injection 
injection rate 10 mL/hr 
initial saturation 0.30 
ch1v 
ch2v 
C/Co 
Z (m) 0 1 2 3 
-3 
-2 
-1
0 
1.00 
0.90 
0.75 
0.50 
0.25 
0.10 
0.02 
Busted Butte 
Phase 1A test 
Borehole 1 
injection rate 10 mL/hr 
initial saturation 0.30 
ch1v 
ch1v 
C/Co

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 VI-5 March 2000 
DTN: LB991220140160.010 
Figure VI. 5. Pedicted Nonsorbing Bromide Tracer Distribution after 285 days for Borehole 4 (S1A Flow Parameters). 
DTN: LB991220140160.010 
Figure. VI.6. Schematic Illustration of Injection/Collection Boreholes 5 and 6 and Collection Locations in Borehole 6 in 
the Phase 1B Test, Busted Butte (Not to Scale). 
X (m) 
Z (m) 
0 1 2 3 
-3 
-2 
-1
0 
1.00 
0.90 
0.75 
0.50 
0.25 
0.10 
0.02 
Busted Butte 
Phase 1A test 
Borehole 4 
injection rate 1 mL/hr 
initial saturation 0.30 
ch2v 
ch2v 
C/Co 
tsw39 
28 cm 
Borehole 5 
Borehole 6 
(collection) 
(injection) 
130 cm 
130 cm (injection rate 10 mL/hr) 
150 cm 170 cm 190 cm 110 cm 90 cm 70 cm 
up 
Rock 
k 
face 
X=0

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 VI-6 March 2000 
DTN: LB991220140160.010 
Figure VI.7. Predicted Bromide Breakthrough Curves at Different Collection Locations in Borehole 6 (S1A Flow 
Parameters). 
DTN: LB991220140160.010 
Figure VI.8. Predicted Bromide Breakthrough Curves at Different Collection Locations in Borehole 6 (S2B Flow 
Parameters). 
0.0 
0.1 
0.2 
0.3 
0.4 
0.5 
0.6 
0.7 
0.8 
0.9 
1.0 
05/12/98 
05/26/98 
06/09/98 
06/23/98 
07/07/98 
07/21/98 
08/04/98 
08/18/98 
09/01/98 
09/15/98 
09/29/98 
10/13/98 
10/27/98 
11/10/98 
Date since liquid injection 
Relative concentration (C/Co) 
130 cm 
150 cm 
170 cm 
190 cm 
0.0 
0.1 
0.2 
0.3 
0.4 
0.5 
0.6 
0.7 
0.8 
0.9 
1.0 
05/12/98 
05/26/98 
06/09/98 
06/23/98 
07/07/98 
07/21/98 
08/04/98 
08/18/98 
09/01/98 
09/15/98 
09/29/98 
10/13/98 
10/27/98 
11/10/98 
Date since liquid injection Relative concentration (C/Co) 
130 cm 
150 cm 
170 cm 
190 cm

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 VI-7 March 2000 
DTN: LB991220140160.010 
Figure VI.9. Predicted Liquid Saturation at Different Collection Locations in Borehole 6 (S1A Flow Parameters). 
DTN: LB991220140160.010 
Figure VI.10. Predicted Liquid Saturation at Different Collection Locations in Borehole 6 (S2B Flow Parameters). 
0.30 
0.40 
0.50 
0.60 
0.70 
0.80 
0.90 
1.00 
05/12/98 
05/26/98 
06/09/98 
06/23/98 
07/07/98 
07/21/98 
08/04/98 
08/18/98 
09/01/98 
09/15/98 
09/29/98 
10/13/98 
10/27/98 
11/10/98 
Liquid saturation 
130 cm 
150 cm 
170 cm 
190 cm 
0.30 
0.35 
0.40 
0.45 
0.50 
05/12/98 
05/26/98 
06/09/98 
06/23/98 
07/07/98 
07/21/98 
08/04/98 
08/18/98 
09/01/98 
09/15/98 
09/29/98 
10/13/98 
10/27/98 
11/10/98 
Date since liquid injection 
Liquid saturation 
130 cm 
150 cm 
170 cm 
190 cm

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 VI-8 March 2000 
DTN: LB991220140160.010 
Figure VI.11. Predicted 2,6-DFBA Breakthrough Curve at Different Collection Locations in Borehole 6 (S1A Flow 
Parameters). 
DTN: LB991220140160.010 
Figure. VI.12. Predicted Lithium Breakthrough Curve at Different Collection Locations in Borehole 6 (K_d=2 mL/mg; 
S1A Flow Parameters). 
0.0 
0.1 
0.2 
0.3 
0.4 
0.5 
0.6 
0.7 
0.8 
0.9 
1.0 
05/12/98 
05/26/98 
06/09/98 
06/23/98 
07/07/98 
07/21/98 
08/04/98 
08/18/98 
09/01/98 
09/15/98 
09/29/98 
10/13/98 
10/27/98 
11/10/98 
Date since liquid injection 
Relative concentration (C/Co) 
130 cm 
150 cm 
170 cm 
190 cm 
0.00 
0.02 
0.04 
0.06 
0.08 
0.10 
0.12 
05/12/98 
05/26/98 
06/09/98 
06/23/98 
07/07/98 
07/21/98 
08/04/98 
08/18/98 
09/01/98 
09/15/98 
09/29/98 
10/13/98 
10/27/98 
11/10/98 
Date since liquid injection 
Relative concentration (C/Co) 
130 cm 
150 cm 
170 cm 
190 cm

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 VI-9 March 2000 
DTN: LB991220140160.010 
Figure VI.13. Predicted Lithium Breakthrough Curve at Different Collection Locations in Borehole 6 (K_d=2 mL/mg; S2B 
Flow Parameters). 
0.000 
0.005 
0.010 
0.015 
0.020 
0.025 
0.030 
0.035 
05/12/98 
05/26/98 
06/09/98 
06/23/98 
07/07/98 
07/21/98 
08/04/98 
08/18/98 
09/01/98 
09/15/98 
09/29/98 
10/13/98 
10/27/98 
11/10/98 
Date since liquid injection 
Relative concentration (C/Co) 
130 cm 
150 cm 
170 cm 
190 cm

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 VII-1 
ATTACHMENT VII. 
FIGURES FROM THE 237Np 3-D TRANSPORT STUDIES

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 VII-2 
INTENTIONALLY LEFT BLANK

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 VII-3 
FIGURES 
Page 
VII.1. Distribution of the Relative Mass Fraction XR of 237Np in the Fractures of the 
Tsw39 Layer at t = 100 Years for Mean Present-Day Infiltration.................................VII-5 
VII.2. Distribution of the Relative Mass Fraction XR of 237Np in the Matrix of the 
Tsw39 Layer at t = 100 Years for Mean Present-Day Infiltration.................................VII-6 
VII.3. Distribution of the Relative Sorbed Concentration FR of 237Np in the Matrix of the 
Tsw39 Layer at t = 100 Years for Mean Present-Day Infiltration.................................VII-7 
VII.4. Distribution of the Relative Mass Fraction XR of 237Np in the Fractures of the 
Tsw39 Layer at t = 1,000 Years for Mean Present-Day Infiltration..............................VII-8 
VII.5. Distribution of the Relative Mass Fraction XR of 237Np in the Matrix of the 
Tsw39 Layer at t = 1,000 Years for Mean Present-Day Infiltration..............................VII-9 
VII.6. Distribution of the Relative Sorbed Concentration FR of 237Np in the Matrix of the 
Tsw39 Layer at t = 1,000 Years for Mean Present-Day Infiltration............................VII-10 
VII.7. Distribution of the Relative Mass Fraction XR of 237Np in the Fractures of the 
Tsw39 Layer at t = 10,000 Years for Mean Present-Day Infiltration..........................VII-11 
VII.8. Distribution of the Relative Mass Fraction XR of 237Np in the Matrix of the 
Tsw39 Layer at t = 10,000 Years for Mean Present-Day Infiltration..........................VII-12 
VII.9. Distribution of the Relative Sorbed Concentration FR of 237Np in the Matrix of the 
Tsw39 Layer at t = 10,000 Years for Mean Present-Day Infiltration..........................VII-13 
VII.10. Distribution of the Relative Mass Fraction XR of 237Np in the Fractures of the 
Tsw39 Layer at t = 100,000 Years for Mean Present-Day Infiltration........................VII-14 
VII.11. Distribution of the Relative Mass Fraction XR of 237Np in the Matrix of the 
Tsw39 Layer at t = 100,000 Years for Mean Present-Day Infiltration........................VII-15 
VII.12. Distribution of the Relative Sorbed Concentration FR of 237Np in the Matrix of the 
Tsw39 Layer at t = 100,000 Years for Mean Present-Day Infiltration........................VII-16 
VII.13. Distribution of the Relative Mass Fraction XR of 237Np in the Fractures 
Immediately Above the Groundwater at t = 100 Years for Mean 
Present-Day Infiltration..............................................................................................VII-17

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 VII-4 
FIGURES (Continued) 
Page 
VII.14. Distribution of the Relative Mass Fraction XR of 237Np in the Matrix 
Immediately Above the Groundwater Table at t = 100 Years for a Mean 
Present-Day Infiltration..............................................................................................VII-18 
VII.15. Distribution of the Relative Sorbed Concentration FR of 237Np in the Matrix 
Immediately Above the Groundwater Table at t = 100 Years for a Mean 
Present-Day Infiltration..............................................................................................VII-19 
VII.16. Distribution of the Relative Mass Fraction XR of 237Np in the Fractures 
Immediately Above the Groundwater at t = 1,000 Years for Mean 
Present-Day Infiltration..............................................................................................VII-20 
VII.17. Distribution of the Relative Mass Fraction XR of 237Np in the Matrix 
Immediately Above the Groundwater Table at t = 1,000 Years for a Mean 
Present-Day Infiltration..............................................................................................VII-21 
VII.18. Distribution of the Relative Sorbed Concentration FR of 237Np in the Matrix 
Immediately Above the Groundwater Table at t = 1,000 Years for a Mean 
Present-Day Infiltration..............................................................................................VII-22 
VII.19. Distribution of the Relative Mass Fraction XR of 237Np in the Fractures 
Immediately Above the Groundwater at t = 10,000 Years for Mean 
Present-Day Infiltration..............................................................................................VII-23 
VII.20. Distribution of the Relative Mass Fraction XR of 237Np in the Matrix 
Immediately Above the Groundwater Table at t = 10,000 Years for a Mean 
Present-Day Infiltration..............................................................................................VII-24 
VII.21. Distribution of the Relative Sorbed Concentration FR of 237Np in the Matrix 
Immediately Above the Groundwater Table at t = 10,000 Years for a Mean 
Present-Day Infiltration..............................................................................................VII-25 
VII.22. Distribution of the Relative Mass Fraction XR of 237Np in the Fractures 
Immediately Above the Groundwater at t = 100,000 Years for Mean 
Present-Day Infiltration..............................................................................................VII-26 
VII.23. Distribution of the Relative Mass Fraction XR of 237Np in the Matrix 
Immediately Above the Groundwater Table at t = 100,000 Years for a Mean 
Present-Day Infiltration..............................................................................................VII-27 
VII.24. Distribution of the Relative Sorbed Concentration FR of 237Np in the Matrix 
Immediately Above the Groundwater Table at t = 100,000 Years for a Mean 
Present-Day Infiltration..............................................................................................VII-28

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.1. Distribution of the relative mass fraction XR of 237Np in the fractures of the tsw39 layer at t = 100 
years formeanpresent-day infiltration(DTN: LB991220140160.012, datasubmittedwiththisAMR) . 
MDL-NBS-HS-000008 REV00 VII-5 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.2. Distribution of the relative mass fraction XR of 237Np in the matrix of the tsw39 layer at t = 100 years 
for mean present-day infiltration (DTN: LB991220140160.012, data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VII-6 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.3. Distribution of the relative sorbed concentration FR of 237Np in the matrix of the tsw39 layer at t = 
100 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with this 
AMR). 
MDL-NBS-HS-000008 REV00 VII-7 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.4. Distribution of the relative mass fraction XR of 237Np in the fractures of the tsw39 layer at t = 1,000 
years formeanpresent-day infiltration(DTN: LB991220140160.012, datasubmittedwiththisAMR) . 
MDL-NBS-HS-000008 REV00 VII-8 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.5. Distribution of the relative mass fraction XR of 237Np in the matrix of the tsw39 layer at t = 1,000 
years formeanpresent-day infiltration(DTN: LB991220140160.012, datasubmittedwiththisAMR) . 
MDL-NBS-HS-000008 REV00 VII-9 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.6. Distribution of the relative sorbed concentration FR of 237Np in the matrix of the tsw39 layer at t 
= 1,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 VII-10 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.7. Distribution of the relative mass fraction XR of 237Np in the fractures of the tsw39 layer at t = 10,000 
years formeanpresent-day infiltration(DTN: LB991220140160.012, datasubmittedwiththisAMR) . 
MDL-NBS-HS-000008 REV00 VII-11 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.8. Distribution of the relative mass fraction XR of 237Np in the matrix of the tsw39 layer at t = 10,000 
years formeanpresent-day infiltration(DTN: LB991220140160.012, datasubmittedwiththisAMR) . 
MDL-NBS-HS-000008 REV00 VII-12 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.9. Distribution of the relative sorbed concentration FR of 237Np in the matrix of the tsw39 layer at t 
= 10,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 VII-13 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.10. Distribution of the relative mass fraction XR of 237Np in the fractures of the tsw39 layer at t = 
100,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 VII-14 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.11. Distribution of the relative mass fraction XR of 237Np in the matrix of the tsw39 layer at t = 
100,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 VII-15 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.12. Distribution of the relative sorbed concentration FR of 237Np in the matrix of the tsw39 layer at t = 
100,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 VII-16 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.13. Distribution of the relative mass fraction XR of 237Np in the fractures immediately above the 
groundwater table at t = 100 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VII-17 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.14. Distribution of the relative mass fraction XR of 237Np in the matrix immediately above the 
groundwater at t = 100 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VII-18 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.15. Distribution of the relative sorbed concentration FR of 237Np in the matrix immediately above the 
groundwater at t = 100 years for mean present-day infiltration (DTN: LB991220140160.012, data 
submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VII-19 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.16. Distribution of the relative mass fraction XR of 237Np in the fractures immediately above the 
groundwater at t = 1,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VII-20 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.17. Distribution of the relative mass fraction XR of 237Np in the matrix immediately above the 
groundwater at t = 1,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VII-21 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.18. Distribution of the relative sorbed concentration FR of 237Np in the matrix immediately above the 
groundwaterat t=1,000 yearsformean present-day infiltration(DTN: LB991220140160.012, data 
submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VII-22 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.19. Distribution of the relative mass fraction XR of 237Np in the fractures immediately above the 
groundwater at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VII-23 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.20. Distribution of the relative mass fraction XR of 237Np in the matrix immediately above the 
groundwater at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VII-24 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.21. Distribution of the relative sorbed concentration FR of 237Np in the matrix immediately above the 
groundwater at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VII-25 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.22. Distribution of the relative mass fraction XR of 237Np in the fractures immediately above the 
groundwater at t = 100,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VII-26 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.23. Distribution of the relative mass fraction XR of 237Np in the matrix immediately above the 
groundwater at t = 100,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VII-27 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VII.24. Distribution of the relative sorbed concentration FR of 237Np in the matrix immediately above the 
groundwater at t = 100,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VII-28 March 2000

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 VIII-1 
ATTACHMENT VIII. 
FIGURES FROM THE 239Pu 3-D TRANSPORT STUDIES

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 VIII-2 
INTENTIONALLY LEFT BLANK

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 VIII-3 
FIGURES 
Page 
VIII.1. Distribution of the Relative Mass Fraction XR of 239Pu in the Fractures of the 
Tsw39 Layer at t = 100 Years for Mean Present-Day Infiltration................................VIII-5 
VIII.2. Distribution of the Relative Mass Fraction XR of 239Pu in the Matrix of the 
Tsw39 Layer at t = 100 Years for Mean Present-Day Infiltration................................VIII-6 
VIII.3. Distribution of the Relative Sorbed Concentration FR of 239Pu in the Matrix of the 
Tsw39 Layer at t = 100 Years for Mean Present-Day Infiltration................................VIII-7 
VIII.4. Distribution of the Relative Mass Fraction XR of 239Pu in the Fractures of the 
Tsw39 Layer at t = 1,000 Years for Mean Present-Day Infiltration.............................VIII-8 
VIII.5. Distribution of the Relative Mass Fraction XR of 239Pu in the Matrix of the 
Tsw39 Layer at t = 1,000 Years for Mean Present-Day Infiltration.............................VIII-9 
VIII.6. Distribution of the Relative Sorbed Concentration FR of 239Pu in the Matrix of the 
Tsw39 Layer at t = 1,000 Years for Mean Present-Day Infiltration...........................VIII-10 
VIII.7. Distribution of the Relative Mass Fraction XR of 239Pu in the Fractures of the 
Tsw39 Layer at t = 10,000 Years for Mean Present-Day Infiltration.........................VIII-11 
VIII.8. Distribution of the Relative Mass Fraction XR of 239Pu in the Matrix of the 
Tsw39 Layer at t = 10,000 Years for Mean Present-Day Infiltration.........................VIII-12 
VIII.9. Distribution of the Relative Sorbed Concentration FR of 239Pu in the Matrix of the 
Tsw39 Layer at t = 10,000 Years for Mean Present-Day Infiltration.........................VIII-13 
VIII.10. Distribution of the Relative Mass Fraction XR of 239Pu in the Fractures of the 
Tsw39 Layer at t = 100,000 Years for Mean Present-Day Infiltration.......................VIII-14 
VIII.11. Distribution of the Relative Mass Fraction XR of 239Pu in the Matrix of the 
Tsw39 Layer at t = 100,000 Years for Mean Present-Day Infiltration.......................VIII-15 
VIII.12. Distribution of the Relative Sorbed Concentration FR of 239Pu in the Matrix of the 
Tsw39 Layer at t = 100,000 Years for Mean Present-Day Infiltration.......................VIII-16 
VIII.13. Distribution of the Relative Mass Fraction XR of 239Pu in the Fractures 
Immediately Above the Groundwater at t = 100 Years for Mean 
Present-Day Infiltration.............................................................................................VIII-17

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 VIII-4 
FIGURES (Continued) 
Page 
VIII.14. Distribution of the Relative Mass Fraction XR of 239Pu in the Matrix 
Immediately Above the Groundwater Table at t = 100 Years for a Mean 
Present-Day Infiltration.............................................................................................VIII-18 
VIII.15. Distribution of the Relative Sorbed Concentration FR of 239Pu in the Matrix 
Immediately Above the Groundwater Table at t = 100 Years for a Mean 
Present-Day Infiltration.............................................................................................VIII-19 
VIII.16. Distribution of the Relative Mass Fraction XR of 239Pu in the Fractures 
Immediately Above the Groundwater at t = 1,000 Years for Mean 
Present-Day Infiltration.............................................................................................VIII-20 
VIII.17. Distribution of the Relative Mass Fraction XR of 239Pu in the Matrix 
Immediately Above the Groundwater Table at t = 1,000 Years for a Mean 
Present-Day Infiltration.............................................................................................VIII-21 
VIII.18. Distribution of the Relative Sorbed Concentration FR of 239Pu in the Matrix 
Immediately Above the Groundwater Table at t = 1,000 Years for a Mean 
Present-Day Infiltration.............................................................................................VIII-22 
VIII.19. Distribution of the Relative Mass Fraction XR of 239Pu in the Fractures 
Immediately Above the Groundwater at t = 10,000 Years for Mean 
Present-Day Infiltration.............................................................................................VIII-23 
VIII.20. Distribution of the Relative Mass Fraction XR of 239Pu in the Matrix 
Immediately Above the Groundwater Table at t = 10,000 Years for a Mean 
Present-Day Infiltration.............................................................................................VIII-24 
VIII.21. Distribution of the Relative Sorbed Concentration FR of 239Pu in the Matrix 
Immediately Above the Groundwater Table at t = 10,000 Years for a Mean 
Present-Day Infiltration.............................................................................................VIII-25 
VIII.22. Distribution of the Relative Mass Fraction XR of 239Pu in the Fractures 
Immediately Above the Groundwater at t = 100,000 Years for Mean 
Present-Day Infiltration.............................................................................................VIII-26 
VIII.23. Distribution of the Relative Mass Fraction XR of 239Pu in the Matrix 
Immediately Above the Groundwater Table at t = 100,000 Years for a Mean 
Present-Day Infiltration.............................................................................................VIII-27 
VIII.24. Distribution of the Relative Sorbed Concentration FR of 239Pu in the Matrix 
Immediately Above the Groundwater Table at t = 100,000 Years for a Mean 
Present-Day Infiltration.............................................................................................VIII-28

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.1. Distribution of the relative mass fraction XR of 239Pu in the fractures of the tsw39 layer at t = 
100 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with this 
AMR). 
MDL-NBS-HS-000008 REV00 VIII-5 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.2. Distributionof therelative mass fraction XR of 239Pu in the matrixof thetsw39 layer at t = 100 years 
for mean present-day infiltration (DTN: LB991220140160.012, data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-6 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.3. Distribution of the relative sorbed concentration FR of 239Pu in the matrix of the tsw39 layer at t = 
100 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with this 
AMR). 
MDL-NBS-HS-000008 REV00 VIII-7 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.4. Distribution of the relative mass fraction XR of 239Pu in the fractures of the tsw39 layer at t = 
1,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 VIII-8 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.5. Distribution of the relative mass fraction XR of 239Pu in the matrix of the tsw39 layer at t = 
1,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 VIII-9 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.6. Distribution of the relative sorbed concentration FR of 239Pu in the matrix of the tsw39 layer at t 
= 1,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 VIII-10 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.7. Distribution of the relative mass fraction XR of 239Pu in the fractures of the tsw39 layer at t = 
10,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 VIII-11 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.8. Distribution of the relative mass fraction XR of 239Pu in the matrix of the tsw39 layer at t = 
10,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 VIII-12 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.9. Distribution of the relative sorbed concentration FR of 239Pu in the matrix of the tsw39 layer at t = 
10,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 VIII-13 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.10. Distribution of the relative mass fraction XR of 239Pu in the fractures of the tsw39 layer at t 
= 100,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted 
with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-14 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.11. Distribution of the relative mass fraction XR of 239Pu in the matrix of the tsw39 layer at t = 
100,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 VIII-15 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.12. Distribution of the relative sorbed concentration FR of 239Pu in the matrix of the tsw39 layer at 
t = 100,000 years for mean present-day infiltration (DTN: LB991220140160.012, data submitted 
with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-16 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.13. Distribution of the relative mass fraction XR of 239Pu in the fractures immediately above the 
groundwater at t = 100 years for mean present-day infiltration (DTN: LB991220140160.012, data 
submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-17 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.14. Distribution of the relative mass fraction XR of 239Pu in the matrix immediately above the 
groundwater at t = 100 years for mean present-day infiltration (DTN: LB991220140160.012, data 
submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-18 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.15. Distribution of the relative sorbed concentration FR of 239Pu in the matrix immediately above the 
groundwater at t = 100 years for mean present-day infiltration (DTN: LB991220140160.012, data 
submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-19 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.16. Distribution of the relative mass fraction XR of 239Pu in the fractures immediately above the 
groundwater at t = 1,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-20 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.17. Distribution of the relative mass fraction XR of 239Pu in the matrix immediately above the 
groundwater at t = 1,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-21 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.18. Distribution of the relative sorbed concentration FR of 239Pu in the matrix immediately above the 
groundwater at t = 1,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-22 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.19. Distribution of the relative mass fraction XR of 239Pu in the fractures immediately above the 
groundwater at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-23 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.20. Distribution of the relative mass fraction XR of 239Pu in the matrix immediately above the 
groundwater at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-24 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.21. Distribution of the relative sorbed concentration FR of 239Pu in the matrix immediately above the 
groundwater at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-25 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.22. Distribution of the relative mass fraction XR of 239Pu in the fractures immediately above the 
groundwater at t = 100,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-26 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.23. Distribution of the relative mass fraction XR of 239Pu in the matrix immediately above the 
groundwater at t = 100,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-27 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure VIII.24. Distribution of the relative sorbed concentration FR of 239Pu in the matrix immediately above the 
groundwater at t = 100,000 years for mean present-day infiltration (DTN: LB991220140160.012, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 VIII-28 March 2000

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 IX-1 
ATTACHMENT IX. 
FIGURES FROM THE 3-D TRANSPORT STUDIES OF THE 6 nm COLLOID

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 IX-2 
INTENTIONALLY LEFT BLANK

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 IX-3 
FIGURES 
Page 
IX.1. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Fractures 
of the Tsw39 Layer at t = 10 Years for Mean Present-Day Infiltration..........................IX-5 
IX.2. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Matrix 
of the Tsw39 Layer at t = 10 Years for Mean Present-Day Infiltration..........................IX-6 
IX.3. Distribution of the Relative Filtered Concentration FR of the 6 nm colloid in the Matrix 
of the Tsw39 Layer at t = 10 Years for Mean Present-Day Infiltration..........................IX-7 
IX.4. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Fractures 
of the Tsw39 Layer at t = 100 Years for Mean Present-Day Infiltration........................IX-8 
IX.5. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Matrix 
of the Tsw39 Layer at t = 100 Years for Mean Present-Day Infiltration........................IX-9 
IX.6. Distribution of the Relative Filtered Concentration FR of the 6 nm colloid in the Matrix 
of the Tsw39 Layer at t = 100 Years for Mean Present-Day Infiltration......................IX-10 
IX.7. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Fractures 
of the Tsw39 Layer at t = 1,000 Years for Mean Present-Day Infiltration...................IX-11 
IX.8. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Matrix 
of the Tsw39 Layer at t = 1,000 Years for Mean Present-Day Infiltration...................IX-12 
IX.9. Distribution of the Relative Filtered Concentration FR of the 6 nm colloid in the Matrix 
of the Tsw39 Layer at t = 1,000 Years for Mean Present-Day Infiltration...................IX-13 
IX.10. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Fractures 
of the Tsw39 Layer at t = 10,000 Years for Mean Present-Day Infiltration.................IX-14 
IX.11. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Matrix of the 
Tsw39 Layer at t = 10,000 Years for Mean Present-Day Infiltration...........................IX-15 
IX.12. Distribution of the Relative Filtered Concentration FR of the 6 nm colloid in the Matrix of the 
Tsw39 Layer at t = 10,000 Years for Mean Present-Day Infiltration...........................IX-16 
IX.13. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Fractures 
Immediately Above the Groundwater at t = 10 Years for Mean 
Present-Day Infiltration...............................................................................................IX-17

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 IX-4 
FIGURES (Continued) 
Page 
IX.14. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Matrix 
Immediately Above the Groundwater Table at t = 10 Years for a Mean 
Present-Day Infiltration...............................................................................................IX-18 
IX.15. Distribution of the Relative Filtered Concentration FR of the 6 nm colloid in the Matrix 
Immediately Above the Groundwater Table at t = 10 Years for a Mean 
Present-Day Infiltration...............................................................................................IX-19 
IX.16. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Fractures 
Immediately Above the Groundwater at t = 100 Years for Mean 
Present-Day Infiltration...............................................................................................IX-20 
IX.17. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Matrix 
Immediately Above the Groundwater Table at t = 100 Years for a Mean 
Present-Day Infiltration...............................................................................................IX-21 
IX.18. Distribution of the Relative Filtered Concentration FR of the 6 nm colloid in the Matrix 
Immediately Above the Groundwater Table at t = 100 Years for a Mean 
Present-Day Infiltration...............................................................................................IX-22 
IX.19. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Fractures 
Immediately Above the Groundwater at t = 1,000 Years for Mean 
Present-Day Infiltration...............................................................................................IX-23 
IX.20. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Matrix 
Immediately Above the Groundwater Table at t = 1,000 Years for a Mean 
Present-Day Infiltration...............................................................................................IX-24 
IX.21. Distribution of the Relative Filtered Concentration FR of the 6 nm colloid in the Matrix 
Immediately Above the Groundwater Table at t = 1,000 Years for a Mean 
Present-Day Infiltration...............................................................................................IX-25 
IX.22. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Fractures 
Immediately Above the Groundwater at t = 10,000 Years for Mean 
Present-Day Infiltration...............................................................................................IX-26 
IX.23. Distribution of the Relative Mass Fraction XR of the 6 nm colloid in the Matrix 
Immediately Above the Groundwater Table at t = 10,000 Years for a Mean 
Present-Day Infiltration...............................................................................................IX-27 
IX.24. Distribution of the Relative Filtered Concentration FR of the 6 nm colloid in the Matrix 
Immediately Above the Groundwater Table at t = 10,000 Years for a Mean 
Present-Day Infiltration...............................................................................................IX-28

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.1. Distribution of the relative mass fraction XR of the 6 nm colloid in the fractures of the tsw39 layer at 
t = 10 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted with this 
AMR). 
MDL-NBS-HS-000008 REV00 IX-5 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.2. Distribution of the relative mass fraction XR of the 6 nm colloid in the matrix of the tsw39 layer at t 
= 10 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted with this 
AMR). 
MDL-NBS-HS-000008 REV00 IX-6 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.3. Distribution of the relative filtered concentration FR of the 6 nm colloid in the matrix of the tsw39 
layer at t = 10 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted 
with this AMR). 
MDL-NBS-HS-000008 REV00 IX-7 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.4. Distribution of the relative mass fraction XR of the 6 nm colloid in the fractures of the tsw39 layer at t 
= 100 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted with this 
AMR). 
MDL-NBS-HS-000008 REV00 IX-8 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.5. Distribution of the relative mass fraction XR of the 6 nm colloid in the matrix of the tsw39 layer at t 
= 100 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted with this 
AMR). 
MDL-NBS-HS-000008 REV00 IX-9 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.6. Distribution of therelative filtered concentration FR of the 6 nm colloid in the matrix of thetsw39 layer 
at t = 100 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 IX-10 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.7. Distribution of the relative mass fraction XR of the 6 nm colloid in the fractures of the tsw39 layer at 
t = 1,000 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 IX-11 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.8. Distribution of the relative mass fraction XR of the 6 nm colloid in the matrix of the tsw39 layer at t = 
1,000 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted with this 
AMR). 
MDL-NBS-HS-000008 REV00 IX-12 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.9. Distribution of therelative filtered concentration FR of the 6 nm colloid in the matrix of thetsw39 layer 
at t= 1,000years formean present-day infiltration (DTN: LB991220140160.017, datasubmitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 IX-13 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.10. Distribution of the relative mass fraction XR of the 6 nm colloid in the fractures of the tsw39 layer 
at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted 
with this AMR). 
MDL-NBS-HS-000008 REV00 IX-14 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.11. Distribution of the relative mass fraction XR of the 6 nm colloid in the matrix of the tsw39 layer at t 
= 10,000 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 IX-15 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
FigureIX.12. Distributionoftherelativefiltered concentrationF R ofthe6nmcolloidinthematrixof thetsw39 layer 
at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted 
with this AMR). 
MDL-NBS-HS-000008 REV00 IX-16 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.13. Distribution of the relative mass fraction XR of the 6 nm colloid in the fractures immediately above 
thegroundwater at t= 10years formean present-day infiltration (DTN: LB991220140160.017, data 
submitted with this AMR). 
MDL-NBS-HS-000008 REV00 IX-17 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.14. Distribution of the relative mass fraction XR of the 6 nm colloid in the matrix immediately above the 
groundwater at t = 10 years for mean present-day infiltration (DTN: LB991220140160.017, data 
submitted with this AMR). 
MDL-NBS-HS-000008 REV00 IX-18 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.15. Distribution of the relative filtered concentration FR of the 6 nm colloid in the matrix immediately 
abovethegroundwateratt=10yearsformeanpresent-dayinfiltration(DTN:LB991220140160.017, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 IX-19 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.16. Distribution of the relative mass fraction XR of the 6 nm colloid in the fractures immediately above 
the groundwater at t = 100 years for mean present-day infiltration (DTN: LB991220140160.017, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 IX-20 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.17. Distribution of the relative mass fraction XR of the 6 nm colloid in the matrix immediately above the 
groundwater at t = 100 years for mean present-day infiltration (DTN: LB991220140160.017, data 
submitted with this AMR). 
MDL-NBS-HS-000008 REV00 IX-21 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.18. Distribution of the relative filtered concentration FR of the 6 nm colloid in the matrix immediately 
above the groundwater at t = 100 years for mean present-day infiltration (DTN: 
LB991220140160.017, data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 IX-22 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.19. Distribution of the relative mass fraction XR of the 6 nm colloid in the fractures immediately above 
the groundwater at t = 1,000 years for mean present-day infiltration (DTN: LB991220140160.017, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 IX-23 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.20. Distribution of the relative mass fraction XR of the 6 nm colloid in the matrix immediately above 
the groundwater at t = 1,000 years for mean present-day infiltration (DTN: LB991220140160.017, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 IX-24 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.21. Distribution of the relative filtered concentration FR of the 6 nm colloid in the matrix immediately 
above the groundwater at t = 1,000 years for mean present-day infiltration (DTN: 
LB991220140160.017, data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 IX-25 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.22. Distribution of the relative mass fraction XR of the 6 nm colloid in the fractures immediately above 
the groundwater at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.017, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 IX-26 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.23. Distribution of the relative mass fraction XR of the 6 nm colloid in the matrix immediately above 
the groundwater at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.017, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 IX-27 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure IX.24. Distribution of the relative filtered concentration FR of the 6 nm colloid in the matrix immediately 
above the groundwater at t = 10,000 years for mean present-day infiltration (DTN: 
LB991220140160.017, data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 IX-28 March 2000

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 X-1 
ATTACHMENT X. 
FIGURES FROM THE 3-D TRANSPORT STUDIES OF THE 450 nm COLLOID

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 X-2 
INTENTIONALLY LEFT BLANK

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 X-3 
FIGURES 
Page 
X.1. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Fractures 
of the Tsw39 Layer at t = 10 Years for Mean Present-Day Infiltration..........................X-5 
X.2. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Matrix 
of the Tsw39 Layer at t = 10 Years for Mean Present-Day Infiltration..........................X-6 
X.3. Distribution of the Relative Filtered Concentration FR of the 450 nm colloid in the Matrix 
of the Tsw39 Layer at t = 10 Years for Mean Present-Day Infiltration..........................X-7 
X.4. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Fractures 
of the Tsw39 Layer at t = 100 Years for Mean Present-Day Infiltration........................X-8 
X.5. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Matrix 
of the Tsw39 Layer at t = 100 Years for Mean Present-Day Infiltration........................X-9 
X.6. Distribution of the Relative Filtered Concentration FR of the 450 nm colloid in the 
Matrix of the Tsw39 Layer at t = 100 Years for Mean Present-Day Infiltration. .........X-10 
X.7. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Fractures 
of the Tsw39 Layer at t = 1,000 Years for Mean Present-Day Infiltration...................X-11 
X.8. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Matrix 
of the Tsw39 Layer at t = 1,000 Years for Mean Present-Day Infiltration...................X-12 
X.9. Distribution of the Relative Filtered Concentration FR of the 450 nm colloid in the 
Matrix of the Tsw39 Layer at t = 1,000 Years for Mean Present-Day Infiltration. ......X-13 
X.10. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Fractures 
of the Tsw39 Layer at t = 10,000 Years for Mean Present-Day Infiltration.................X-14 
X.11. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the 
Matrix of the Tsw39 Layer at t = 10,000 Years for Mean Present-Day Infiltration. ....X-15 
X.12. Distribution of the Relative Filtered Concentration FR of the 450 nm colloid in the 
the Matrix of the Tsw39 Layer at t = 10,000 Years for 
Mean Present-Day Infiltration.....................................................................................X-16 
X.13. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Fractures 
Immediately Above the Groundwater at t = 10 Years for Mean 
Present-Day Infiltration...............................................................................................X-17

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 X-4 
FIGURES (Continued) 
Page 
X.14. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Matrix 
Immediately Above the Groundwater Table at t = 10 Years for a Mean 
Present-Day Infiltration................................................................................................X-18 
X.15. Distribution of the Relative Filtered Concentration FR of the 450 nm colloid in the 
Matrix Immediately Above the Groundwater Table at t = 10 Years for a Mean 
Present-Day Infiltration................................................................................................X-19 
X.16. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Fractures 
Immediately Above the Groundwater at t = 100 Years for Mean 
Present-Day Infiltration................................................................................................X-20 
X.17. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Matrix 
Immediately Above the Groundwater Table at t = 100 Years for a Mean 
Present-Day Infiltration................................................................................................X-21 
X.18. Distribution of the Relative Filtered Concentration FR of the 450 nm colloid in the 
Matrix Immediately Above the Groundwater Table at t = 100 Years for a Mean 
Present-Day Infiltration................................................................................................X-22 
X.19. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Fractures 
Immediately Above the Groundwater at t = 1,000 Years for Mean 
Present-Day Infiltration................................................................................................X-23 
X.20. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Matrix 
Immediately Above the Groundwater Table at t = 1,000 Years for a Mean 
Present-Day Infiltration................................................................................................X-24 
X.21. Distribution of the Relative Filtered Concentration FR of the 450 nm colloid in the 
Matrix Immediately Above the Groundwater Table at t = 1,000 Years for a Mean 
Present-Day Infiltration................................................................................................X-25 
X.22. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Fractures 
Immediately Above the Groundwater at t = 10,000 Years for Mean 
Present-Day Infiltration................................................................................................X-26 
X.23. Distribution of the Relative Mass Fraction XR of the 450 nm colloid in the Matrix 
Immediately Above the Groundwater Table at t = 10,000 Years for a Mean 
Present-Day Infiltration................................................................................................X-27 
X.24. Distribution of the Relative Filtered Concentration FR of the 450 nm colloid in the 
Matrix Immediately Above the Groundwater Table at t = 10,000 Years for a Mean 
Present-Day Infiltration................................................................................................X-28

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.1. Distribution of the relative mass fraction XR of the 450 nm colloid in the fractures of the tsw39 layer at 
t = 10 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted with this 
AMR). 
MDL-NBS-HS-000008 REV00 X-5 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.2. Distribution of the relative mass fraction XR of the 450 nm colloid in the matrix of the tsw39 layer at 
t = 10 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted with this 
AMR). 
MDL-NBS-HS-000008 REV00 X-6 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.3. Distribution of the relative filtered concentration FR of the 450 nm colloid in the matrix of the tsw39 
layer at t = 10 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted 
with this AMR). 
MDL-NBS-HS-000008 REV00 X-7 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.4. Distribution of the relative mass fraction XR of the 450 nm colloid in the fractures of the tsw39 layer 
at t = 100 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 X-8 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.5. Distribution of the relative mass fraction XR of the 450 nm colloid in the matrix of the tsw39 layer at t 
= 100 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted with this 
AMR). 
MDL-NBS-HS-000008 REV00 X-9 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.6. Distribution of the relative filtered concentration FR of the 450 nm colloid in the matrix of the tsw39 
layer at t = 100 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted 
with this AMR). 
MDL-NBS-HS-000008 REV00 X-10 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.7. Distribution of the relative mass fraction XR of the 450 nm colloid in the fractures of the tsw39 layer at 
t = 1,000 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 X-11 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.8. Distribution of the relative mass fraction XR of the 450 nm colloid in the matrix of the tsw39 layer at 
t = 1,000 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted with 
this AMR). 
MDL-NBS-HS-000008 REV00 X-12 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.9. Distribution of the relative filtered concentration FR of the 450 nm colloid in the matrix of the tsw39 
layer att =1,000yearsformean present-day infiltration (DTN: LB991220140160.017,datasubmitted 
with this AMR). 
MDL-NBS-HS-000008 REV00 X-13 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.10. Distribution of the relative mass fraction XR of the 450 nm colloid in the fractures of the tsw39 layer 
at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted 
with this AMR). 
MDL-NBS-HS-000008 REV00 X-14 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.11. Distribution of the relative mass fraction XR of the 450 nm colloid in the matrix of the tsw39 layer 
at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.017, data submitted 
with this AMR). 
MDL-NBS-HS-000008 REV00 X-15 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.12. Distribution of the relative filtered concentration FR of the 450 nm colloid in the matrix of the 
tsw39 layer at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.017, data 
submitted with this AMR). 
MDL-NBS-HS-000008 REV00 X-16 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.13. Distribution of the relative mass fraction XR of the 450 nm colloid in the fractures immediately above 
the groundwater at t = 10 years for mean present-day infiltration (DTN: LB991220140160.017, data 
submitted with this AMR). 
MDL-NBS-HS-000008 REV00 X-17 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.14. Distribution of the relative mass fraction XR of the 450 nm colloid in the matrix immediately above 
the groundwater at t = 10 years for mean present-day infiltration (DTN: LB991220140160.017, data 
submitted with this AMR). 
MDL-NBS-HS-000008 REV00 X-18 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.15. Distributionof therelative filtered concentration FR of the 450 nmcolloid in the matrix immediatelyabove 
thegroundwater at t =10 years for meanpresent-day infiltration (DTN: LB991220140160.017, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 X-19 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.16. Distribution of the relative mass fraction XR of the 450 nm colloid in the fractures immediately above 
the groundwater at t = 100 years for mean present-day infiltration (DTN: LB991220140160.017, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 X-20 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.17. Distribution of the relative mass fraction XR of the 450 nm colloid in the matrix immediately above 
the groundwater at t = 100 years for mean present-day infiltration (DTN: LB991220140160.017, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 X-21 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.18. Distributionof therelative filtered concentration FR of the 450 nmcolloid in the matrix immediatelyabove 
thegroundwaterat t=100 yearsformean present-day infiltration (DTN: LB991220140160.017, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 X-22 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.19. Distribution of the relative mass fraction XR of the 450 nm colloid in the fractures immediately above 
the groundwater at t = 1,000 years for mean present-day infiltration (DTN: LB991220140160.017, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 X-23 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.20. Distribution of the relative mass fraction XR of the 450 nm colloid in the matrix immediately above 
the groundwater at t = 1,000 years for mean present-day infiltration (DTN: LB991220140160.017, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 X-24 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.21. Distribution of the relative filtered concentration FR of the 450 nm colloid in the matrix immediately 
above the groundwater at t = 1,000 years for mean present-day infiltration (DTN: 
LB991220140160.017, data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 X-25 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.22. Distribution of the relative mass fraction XR of the 450 nm colloid in the fractures immediately above 
the groundwater at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.017, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 X-26 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.23. Distribution of the relative mass fraction XR of the 450 nm colloid in the matrix immediately above 
the groundwater at t = 10,000 years for mean present-day infiltration (DTN: LB991220140160.017, 
data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 X-27 March 2000

Title:Radionuclide Transport Models Under Ambient Conditions U0060 
Figure X.24. Distribution of the relative filtered concentration FR of the 450 nm colloid in the matrix immediately 
above the groundwater at t = 10,000 years for mean present-day infiltration (DTN: 
LB991220140160.017, data submitted with this AMR). 
MDL-NBS-HS-000008 REV00 X-28 March 2000

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XI-1 
ATTACHMENT XI. 
FORTRAN ROUTINES

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XI-2 
INTENTIONALLY LEFT BLANK

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XI-3 
XI. FORTRAN ROUTINES USED IN THIS AMR 
The software routines in this attachment have been documented according to AP-SI.1Q, Rev. 2, 
ICN 2, Section 5.1.1, and all documentation has been submitted to the Records Processing 
Center. The accession numbers for the software routine documentation are listed on Table 3.1, 
and also included in the short descriptions of each routine. 
All the routines were written in FORTRAN77, and were all used for the rearrangement of data in 
the very large input or output files of the EOS9nT runs. The routines do not use any external 
input parameters and do not perform any computations. They simply open the data files 
indicated in the routines and rearrange the data to (a) meet the formatting requirements of 
EOS9nT input files or (b) extract a small portion of data at locations of interest. 
XI.1. The xtract1.f Routine 
The xtract1.f V1.0 routine (STN: 10213-1.0-00) is used to modify the grid system from the 
EOS9 runs for use in the EOS9nT runs. The modifications involve (a) determining the grid 
elements corresponding to the potential repository, (b) moving them to the end of the element 
file, where (c) the upper and lower boundary elements are also moved. 
A listing of the xtract1.f routine follows. 
PROGRAM xtract1 
IMPLICIT DOUBLE PRECISION (A-H,O-Z) 
CHARACTER*5 name(2000) 
CHARACTER*5 onoma 
CHARACTER*5 MA12 
C
C 
OPEN(UNIT=11,FILE='REPOS',STATUS='OLD') 
OPEN(UNIT=12,FILE='ELEME',STATUS='OLD') 
OPEN(UNIT=21,FILE='ELEMA') 
OPEN(UNIT=22,FILE='ELEMI') 
C
C 
C 
DO 100 n=1,2000 
READ(11,6003) name(n) 
IF(name(n).EQ.'+++ ') THEN 
GO TO 101 
ELSE 
READ(11,6004) xx 
END IF 
100 CONTINUE 
101 nsour = N-1 
C
C 

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XI-4 
C 
nnaa = 0 
nnss = 0 
nnbb = 0 
jini = 1 
DO 1000 N=1,97976 
READ(12,6005) onoma,NSEQ,NADD,MA12, 
& VOLX,AHTX,zref,X,Y,Z 
DO 200 j8=jini,nsour 
IF(onoma.EQ.name(j8)) THEN 
nnss = nnss+1 
VOLX =1.0d55 
WRITE(22,6005) onoma,NSEQ,NADD,MA12, 
& VOLX,AHTX,zref,X,Y,Z 
jini = j8 
GO TO 1000 
END IF 
200 CONTINUE 
c 
IF(MA12.EQ.'topbd'.OR.MA12.EQ.'botbd') THEN 
nnbb = nnbb+1 
IF(nnbb.EQ.1) VOLX =-VOLX 
WRITE(22,6005) onoma,NSEQ,NADD,MA12, 
& VOLX,AHTX,zref,X,Y,Z 
GO TO 1000 
END IF 
c 
nnaa = nnaa+1 
WRITE(21,6005) onoma,NSEQ,NADD,MA12, 
& VOLX,AHTX,zref,X,Y,Z 
1000 CONTINUE 
C
C
C 
5000 FORMAT(3(A20)) 
6001 FORMAT(T5,'ENTER THE NAME OF THE DATA FILE') 
6002 FORMAT(6(1pe15.8,2x)) 
6003 FORMAT(A5) 
6004 FORMAT(4E20.13) 
6005 FORMAT(A5,2I5,A5,3E10.4,2F10.3,F10.4) 
999 STOP 
END

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XI-5 
XI.2. The xtract2.f Routine 
The xtract2.f V1.0 routine (STN: 10214-1.0-00) is used to obtain initial condition files (INCON) 
using the SAVE files from the EOS9 runs. The INCON files are then used for the EOS9nT 
simultaneous simulations of 99Tc, 237Np and 239Pu transport. 
A listing of the xtract2.f routine follows. 
PROGRAM xtract2 
IMPLICIT DOUBLE PRECISION (A-H,O-Z) 
CHARACTER*5 name(2000) 
CHARACTER*5 onoma 
C
C
C 
OPEN(UNIT=11,FILE='REPOS',STATUS='OLD') 
OPEN(UNIT=12,FILE='BSAVE',STATUS='OLD') 
OPEN(UNIT=22,FILE='INCON') 
C
C 
C 
DO 100 n=1,2000 
READ(11,6003) name(n) 
IF(name(n).EQ.'+++ ') THEN 
GO TO 101 
ELSE 
READ(11,6004) xx 
END IF 
100 CONTINUE 
101 nsour = N-1 
C
C 
C 
jini = 1 
READ(12,6003) onoma 
WRITE(22,6003) onoma 
DO 1000 N=1,97976 
READ(12,6004) onoma,NSEQ,NADD,PORX,ktracr 
READ(12,6005) xxx,yyy 
ktracr = 3 
DO 200 j8=jini,nsour 
IF(onoma.EQ.name(j8)) THEN 
nnss = nnss+1 
WRITE(22,6004) onoma,NSEQ,NADD,PORX,ktracr 
WRITE(22,6005) xxx,yyy,0.0d0,0.0d0 
WRITE(22,6005) 1.0d0,1.0d0,1.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0 
jini = j8 
GO TO 1000 
END IF 
200 CONTINUE 
c

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XI-6 
WRITE(22,6004) onoma,NSEQ,NADD,PORX,ktracr 
WRITE(22,6005) xxx,yyy,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0 
c 
1000 CONTINUE 
WRITE(22,6006) 
WRITE(22,6006) 
C
C
C 
6003 FORMAT(A5) 
6004 FORMAT(A5,2I5,E15.8,3I2) 
6005 FORMAT(4E20.13) 
6006 FORMAT(80(' ')) 
999 STOP 
END

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XI-7 
XI.3. The xtract2a.f Routine 
The xtract2a.f V1.0 routine (STN: 10215-1.0-00) is used to obtain initial condition files (INCON) 
using the SAVE files from the EOS9 runs. The INCON files are then used for the EOS9nT 
simulations of transport of the 237Np and 239Pu decay chains. 
A listing of the xtract2a.f routine follows. 
PROGRAM xtract2a 
IMPLICIT DOUBLE PRECISION (A-H,O-Z) 
CHARACTER*5 name(2000) 
CHARACTER*5 onoma 
C
C
C 
OPEN(UNIT=11,FILE='REPOS',STATUS='OLD') 
OPEN(UNIT=12,FILE='BSAVE',STATUS='OLD') 
OPEN(UNIT=22,FILE='INCON') 
C
C 
C 
DO 100 n=1,2000 
READ(11,6003) name(n) 
IF(name(n).EQ.'+++ ') THEN 
GO TO 101 
ELSE 
READ(11,6004) xx 
END IF 
100 CONTINUE 
101 nsour = N-1 
C
C 
C 
jini = 1 
READ(12,6003) onoma 
WRITE(22,6003) onoma 
DO 1000 N=1,97976 
READ(12,6004) onoma,NSEQ,NADD,PORX,ktracr 
READ(12,6005) xxx,yyy 
ktracr = 3 
DO 200 j8=jini,nsour 
IF(onoma.EQ.name(j8)) THEN 
nnss = nnss+1 
WRITE(22,6004) onoma,NSEQ,NADD,PORX,ktracr 
WRITE(22,6005) xxx,yyy,0.0d0,0.0d0 
WRITE(22,6005) 1.0d0,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0 
jini = j8 
GO TO 1000 
END IF 
200 CONTINUE

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XI-8 
c 
WRITE(22,6004) onoma,NSEQ,NADD,PORX,ktracr 
WRITE(22,6005) xxx,yyy,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0 
c 
1000 CONTINUE 
WRITE(22,6006) 
WRITE(22,6006) 
C
C
C 
6003 FORMAT(A5) 
6004 FORMAT(A5,2I5,E15.8,3I2) 
6005 FORMAT(4E20.13) 
6006 FORMAT(80(' ')) 
999 STOP 
END

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XI-9 
XI.4. The xtract2b.f Routine 
The xtract2b.f V1.0 routine (STN: 10216-1.0-00) is used to obtain initial condition files 
(INCON) using the SAVE files from the EOS9 runs. The INCON files are then used for the 
EOS9nT simulations of transport of 99Tc, 237Np and the 239Pu decay chain. 
A listing of the xtract2b.f routine follows. 
PROGRAM xtract2b 
IMPLICIT DOUBLE PRECISION (A-H,O-Z) 
CHARACTER*5 name(2000) 
CHARACTER*5 onoma 
C
C
C 
OPEN(UNIT=11,FILE='REPOS',STATUS='OLD') 
OPEN(UNIT=12,FILE='BSAVE',STATUS='OLD') 
OPEN(UNIT=22,FILE='INCON') 
C
C 
C 
DO 100 n=1,2000 
READ(11,6003) name(n) 
IF(name(n).EQ.'+++ ') THEN 
GO TO 101 
ELSE 
READ(11,6004) xx 
END IF 
100 CONTINUE 
101 nsour = N-1 
C
C 
C 
jini = 1 
READ(12,6003) onoma 
WRITE(22,6003) onoma 
DO 1000 N=1,97976 
READ(12,6004) onoma,NSEQ,NADD,PORX,ktracr 
READ(12,6005) xxx,yyy 
ktracr = 5 
DO 200 j8=jini,nsour 
IF(onoma.EQ.name(j8)) THEN 
nnss = nnss+1 
WRITE(22,6004) onoma,NSEQ,NADD,PORX,ktracr 
WRITE(22,6005) xxx,yyy,0.0d0,0.0d0 
WRITE(22,6005) 1.0d0,1.0d0,1.0d0,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0,0.0d0,0.0d0 
jini = j8 
GO TO 1000 
END IF 
200 CONTINUE

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XI-10 
c 
WRITE(22,6004) onoma,NSEQ,NADD,PORX,ktracr 
WRITE(22,6005) xxx,yyy,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0,0.0d0,0.0d0,0.0d0,0.0d0 
c 
1000 CONTINUE 
WRITE(22,6006) 
WRITE(22,6006) 
C
C
C 
6003 FORMAT(A5) 
6004 FORMAT(A5,2I5,E15.8,3I2) 
6005 FORMAT(4E20.13) 
6006 FORMAT(80(' ')) 
999 STOP 
END

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XI-11 
XI.5. The xtract5.f Routine 
The xtract5.f V1.0 routine (STN: 10217-1.0-00) is used to obtain initial condition files (INCON) 
using the SAVE files from the EOS9 runs. The INCON files are then used for the EOS9nT 
simulations of Cl transport in the ESF. 
A listing of the xtract5.f routine follows. 
PROGRAM xtract5 
IMPLICIT DOUBLE PRECISION (A-H,O-Z) 
CHARACTER*5 onoma 
C
C
C 
OPEN(UNIT=12,FILE='INCON_i',STATUS='OLD') 
OPEN(UNIT=22,FILE='INCON_m') 
C
C 
C 
READ(12,6003) onoma 
WRITE(22,6003) onoma 
DO 1000 N=1,120000 
READ(12,6004) onoma,NSEQ,NADD,PORX,ktracr 
IF(onoma(1:3).EQ.'+++') GO TO 1001 
READ(12,6005) xxx,yyy 
c 
ktracr = 1 
c 
WRITE(22,6004) onoma,NSEQ,NADD,PORX,ktracr 
WRITE(22,6005) xxx,yyy,0.0d0,0.0d0 
WRITE(22,6005) 0.0d0 
WRITE(22,6005) 0.0d0 
WRITE(22,6005) 0.0d0 
c 
1000 CONTINUE 
1001 WRITE(22,6006) 
WRITE(22,6006) 
C
C
C 
6003 FORMAT(A5) 
6004 FORMAT(A5,2I5,E15.8,3I2) 
6005 FORMAT(4E20.13) 
6006 FORMAT(80(' ')) 
999 STOP 
END

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XI-12 
XI.6. The xtract6.f Routine 
The xtract6.f V1.0 routine (STN: 10218-1.0-00) is used to extract the Cl concentrations 
corresponding to the ESF elements from the output of the EOS9nT simulation of Cl transport. 
A listing of the xtract6.f routine follows. 
PROGRAM xtract6 
IMPLICIT DOUBLE PRECISION (A-H,O-Z) 
DIMENSION tmf(2000),xx(2000) 
CHARACTER*5 name(2000) 
CHARACTER*5 onoma 
C
C 
OPEN(UNIT=11,FILE='esf',STATUS='OLD') 
OPEN(UNIT=12,FILE='cl.out',STATUS='OLD') 
OPEN(UNIT=22,FILE='ESF_Cl') 
C
C 
C 
xmin = 1.0d6 
DO 100 n=1,2000 
READ(11,6003) name(n),xx(n) 
IF(name(n).EQ.'+++ ') GO TO 101 
100 CONTINUE 
101 nsour = N-1 
C
C 
C 
DO 1000 N=1,104156 
READ(12,6012) onoma,id,value 
DO 200 j8=1,nsour 
IF(onoma.EQ.name(j8)) THEN 
tmf(j8) = value 
GO TO 1000 
END IF 
200 CONTINUE 
1000 CONTINUE 
C
C 
C 
DO 2000 N=1,nsour 
WRITE(22,6022) xx(n),tmf(n) 
2000 CONTINUE 
C
C
C 
6003 FORMAT(A5,7x,F9.4) 
6004 FORMAT(4E20.13) 
6005 FORMAT(A5,2I5,A5,3E10.4,2F10.3,F10.4) 
6012 FORMAT(T3,A5,2x,I6,4x,1pe15.8,3x,2('(',i1,')',1pe15.8,2x), 
& 1x,1pe15.8,2x,'(',i1,')',1pe15.8)

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XI-13 
6020 FORMAT(T3,A5,2x,F9.4,2x,1pe15.8) 
6022 FORMAT(T3,F9.4,2x,1pe15.8) 
999 STOP 
END

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XI-14 
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Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-1 March 2000 
ATTACHMENT XII. 
INPUT AND OUTPUT FILES

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-2 March 2000 
INTENTIONALLY LEFT BLANK

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-3 March 2000 
XII. INPUT AND OUTPUT FILES 
XII.1 FILES IN DTN: LB991220140160.001 
This DTN includes the files involved in the 2-D numerical simulations for the EOS9nT 
validation (see Section 6.4). These files, located in the directory Val_num, are the following: 
TestFMs The input file for the simulation of the matrix-fracture transport 
problem using the coarse (2x320) grid. 
TestFMs_T_out Output corresponding to the TestFMs input file for conventional 
timestepping. 
TestFMs_S_out Output corresponding to the TestFMs input file for a Laplace 
transfrom formulation using the Stehfest algorithm (Stehfest 
1970a;b). 
TestFMs_H_out Output corresponding to the TestFMs input file for a Laplace 
transfrom formulation using the DeHoog method (DeHoog et al. 
1982). 
TestFMb The input file for the simulation of the matrix-fracture transport 
problem using the medium (5x320) grid. 
TestFMb_T_out Output corresponding to the TestFMb input file for conventional 
timestepping. 
TestFMb_S_out Output corresponding to the TestFMb input file for a Laplace 
transfrom formulation using the Stehfest algorithm (Stehfest 
1970a;b). 
TestFMb_H_out Output corresponding to the TestFMb input file for a Laplace 
transfrom formulation using the DeHoog method (DeHoog et al. 
1982). 
TestFMx The input file for the simulation of the matrix-fracture transport 
problem using the fine (12x320) grid. 
TestFMx_T_out Output corresponding to the TestFMx input file for conventional 
timestepping. 
TestFMx_S_out Output corresponding to the TestFMx input file for a Laplace 
transfrom formulation using the Stehfest algorithm (Stehfest 
1970a;b).

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-4 March 2000 
TestFMx_H_out Output corresponding to the TestFMx input file for a Laplace 
transfrom formulation using the DeHoog method (DeHoog et al. 
1982). 
The three outputs for each input file can be obtained by minor modifications of the input file. 
These modifications are the same for all three input files, and are introduced to the first line of 
the TRACR data block. Thus, the setting 
TRACR----1----*----2----*----3----*----4----*----5----*----6----*----7----*----8 
100010 05 steady0HOOG08 1.0e-14 
leads to simulations using conventional timestepping. When it is changed to 
TRACR----1----*----2----*----3----*----4----*----5----*----6----*----7----*----8 
100010 05 steady1HOOG08 1.0e-14 
the simulation uses a Laplace transform formulation based on the DeHoog method (DeHoog et 
al. 1982). Finally, modification to 
TRACR----1----*----2----*----3----*----4----*----5----*----6----*----7----*----8 
100010 05 steady1STFS18 1.0e-14 
yields the solution based on a Laplace transform formulation following the Stehfest algorithm 
(Stehfest 1970a;b).

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-5 March 2000 
XII.2 FILES IN DTN: LB991220140160.002 
This DTN includes the files involved in the 2-D semianalytical simulations for the FRACL 
validation (see Section 6.4). These files, located in the directory Val_san, are the following: 
Data_2h The input file for the simulation of a matrix-fracture transport 
problem involving three subdomains (two finite and one semiinfinite 
in z). 
Data_2h.C(z)_H Output corresponding to the Data_2h input file. 
Data_3h The input file for the simulation of a matrix-fracture transport 
problem involving a single domain (semi-infinite in z). 
Data_3h.C(z)_H Output corresponding to the Data_3h input file.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-6 March 2000 
XII.3 FILES IN DTN: LB991220140160.003 
This DTN includes the files involved in the 2-D semianalytical simulations of the Cl distribution 
in the UE-25 UZ#16 borehole. The FRACL simulations were conducted in support of the model 
validation (see Section 6.4). These files, located in the directory uz16_cl, are the following: 
cl_10kyr Input file to simulate chloride distribution at 10,000 years. 
cl_10kyr.C(z) Output corresponding to the cl_10kyr input file (vertical 
profile). 
cl_10kyr.C(x) Output corresponding to the cl_10kyr input file (horizontal 
profile). 
cl_2500yr Input file to simulate chloride distribution at 2,500 years. 
cl_2500yr.C(z) Output corresponding to the cl_2500yr input file (vertical 
profile). 
cl_2500yr.C(x) Output corresponding to the cl_2500yr input file (horizontal 
profile). 
cl_1kyr Input file to simulate chloride distribution at 1,000 years. 
cl_1kyr.C(z) Output corresponding to the cl_1kyr input file (vertical profile). 
cl_1kyr.C(x) Output corresponding to the cl_1kyr input file (horizontal 
profile). 
cl_100yr Input file to simulate chloride distribution at 100 years. 
cl_100yr.C(z) Output corresponding to the cl_100yr input file (vertical 
profile). 
cl_100yr.C(x) Output corresponding to the cl_100yr input file (horizontal 
profile).

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-7 March 2000 
XII.4 FILES IN DTN: LB991220140160.004 
This DTN includes the files involved in the 3-D site-scale numerical simulations of Cl transport 
using a calibrated present-day infiltration regime. This simulation was conducted in support of 
verification (see Section 6.4), and was used to determine the Cl concentration distribution in the 
ESF. All the corresponding files are located in the directory ESF_Cl, and are listed below. 
MESH The file containing the mesh (grid geometry). 
INDEX Output and/or input file containing the global indices of the 
neighbors (active and/or inactive) of each grid cell. 
VELOC The input file containing the steady-state velocities across the cell 
boundaries. 
INCON Input file containing the initial conditions. 
chloride Input file for the EOS9nT simulation to determine the Cl 
distribution. 
chloride.out Output corresponding to the chloride input file.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-8 March 2000 
XII.5 FILES IN DTN: LB991220140160.005 
This DTN includes the files involved in the 2-D semianalytical FRACL simulations of the 
transport of three radionuclides (99Tc, 237Np, and 239Pu) in the layers of the TSw hydrogeologic 
unit at three representative 2-D cross sections (i.e., Cross Sections 1, 2 and 3, see Section 6.5). 
The files in this DTN were used to obtain the results discussed in Section 6.6. 
XII.5.1 Main Directory 
All the files associated with this DTN are located in the directory 3crosssections_tsw. 
XII.5.2 Level 1 Directories 
The 3crosssections_tsw directory includes the three Level 1 directories 
crosssection1, crosssection2, and crosssection3. These correspond to Cross 
Sections 1, 2 and 3, respectively. 
XII.5.3 Level 2 Directories 
Each of the crosssection1, crosssection2, crosssection3 directories includes 
the following Level 2 subdirectories: 
10kyear Input and output data for the 10,000-year simulation 
1kyear Input and output data for the 1,000-year simulation 
100year Input and output data for the 100-year simulation 
10year Input and output data for the 10-year simulation 
1year Input and output data for the 1-year simulation 
XII.5.4 Files in Each Level 2 Directory 
Each Level 2 directory includes the following files: 
tc Input file for the 99Tc simulation. 
tc.C(z) Output corresponding to the tc input file (vertical profile). 
tc.C(x) Output corresponding to the tc input file (horizontal profile). 
np Input file for the 237Np simulation. 
np.C(z) Output corresponding to the np input file (vertical profile).

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-9 March 2000 
np.C(x) Output corresponding to the np input file (horizontal profile). 
pu Input file for the 239Pu simulation. 
pu.C(z) Output corresponding to the pu input file (vertical profile). 
pu.C(x) Output corresponding to the pu input file (horizontal profile). 
Note that the file names are the same in all level 2 directories, and only the name of the Level 1 
and/or 2 directory changes.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-10 March 2000 
XII.6 FILES IN DTN: LB991220140160.006 
This DTN includes the files involved in the sensitivity analysis studies of transport of 99Tc, 237Np, 
and 239Pu. These studies were conducted using the 2-D semianalytical FRACL model, and were 
conducted in the tsw35 layer of the TSw hydrogeologic unit. The files in this DTN were used to 
obtain the results discussed in Section 6.6. 
XII.6.1 Main Directory 
All the files associated with this DTN are located in the directory analysis_tsw35. 
XII.6.2 Level 1 Directories 
The analysis_tsw35 main directory includes the following three Level 1 directories: 
aleffect Directory of the files corresponding to the study of the effect of 
longitudinal dispersivity L on transport. 
kieffect Directory of the files corresponding to the study of the effect of 
transfer coefficient Ki on transport. 
torteffect Directory of the files corresponding to the study of the effect of 
tortuosity on transport. 
XII.6.3 Level 2 Directories of the aleffect Level 1 Directory 
The aleffect level 1 directory includes the following three Level 2 directories: 
alf0.1 Directory of the files corresponding to L= 0.1 m. 
alf1 Directory of the files corresponding to L= 1 m. 
alf10 Directory of the files corresponding to L= 10 m. 
XII.6.4 Level 2 Directories of the kieffect Level 1 Directory 
The aleffect level 1 directory includes the following three Level 2 directories: 
ki0.1 Directory of the files corresponding to Ki = 0.1. 
ki0.5 Directory of the files corresponding to Ki = 0.5.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-11 March 2000 
ki1 Directory of the files corresponding to Ki = 1. 
XII.6.5 Level 2 Directories of the torteffect Level 1 Directory 
The aleffect level 1 directory includes the following three Level 2 directories: 
tort0.2phi Directory of the files corresponding to = 0.2f (f : matrix 
porosity). 
tort1phi Directory of the files corresponding to = f. 
tort5phi Directory of the files corresponding to = 5f. 
XII.6.6 Files in Each Level 2 Directory 
Each Level 2 directory includes the following files: 
tc Input file for the 99Tc simulation. 
tc.C(z) Output corresponding to the tc input file (vertical profile). 
tc.C(x) Output corresponding to the tc input file (horizontal profile). 
np Input file for the 237Np simulation. 
np.C(z) Output corresponding to the np input file (vertical profile). 
np.C(x) Output corresponding to the np input file (horizontal profile). 
pu Input file for the 239Pu simulation. 
pu.C(z) Output corresponding to the pu input file (vertical profile). 
pu.C(x) Output corresponding to the pu input file (horizontal profile).

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XII.7 FILES IN DTN: LB991220140160.007 
This DTN includes the files involved in the 2-D semianalytical FRACL simulations of the 
transport of three radionuclides (99Tc, 237Np, and 239Pu) in the layers of the CHn hydrogeologic 
unit at three representative 2-D cross sections (i.e., Cross Sections 1, 2 and 3, see Section 6.5). 
The files in this DTN were used to obtain the results discussed in Section 6.7. 
XII.7.1 Main Directory 
All the files associated with this DTN are located in the directory 3crosssections_chn. 
XII.7.2 Level 2 Directories 
The 3crosssections_chn directory includes the three Level 1 directories 
crosssection1, crosssection2, and crosssection3. These correspond to Cross 
Sections 1, 2 and 3, respectively. 
XII.7.3 Level 3 Directories 
Each of the crosssection1, crosssection2, and crosssection3 directories 
includes the following Level 2 subdirectories: 
100kyear Input and output data for the 100,000-year simulation 
10kyear Input and output data for the 10,000-year simulation 
1kyear Input and output data for the 1,000-year simulation 
100year Input and output data for the 100-year simulation 
10year Input and output data for the 10-year simulation 
XII.7.4 Files in Each Level 3 Directory 
Each Level 2 directory includes the following files: 
tc Input file for the 99Tc simulation. 
tc.C(z) Output corresponding to the tc input file (vertical profile). 
tc.C(x) Output corresponding to the tc input file (horizontal profile). 
np Input file for the 237Np simulation. 
np.C(z) Output corresponding to the np input file (vertical profile).

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np.C(x) Output corresponding to the np input file (horizontal profile). 
pu Input file for the 239Pu simulation. 
pu.C(z) Output corresponding to the pu input file (vertical profile). 
pu.C(x) Output corresponding to the pu input file (horizontal profile). 
Note that the file names are the same in all level 2 directories, and only the name of the Level 1 
and/or 2 directory changes.

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XII.8 FILES IN DTN: LB991220140160.008 
This DTN includes the files involved in the 2-D semianalytical FRACL simulations of the 
transport of three radionuclides (99Tc, 237Np, and 239Pu) in the layers of the PP hydrogeologic unit 
at three representative 2-D cross sections (i.e., Cross Sections 1, 2 and 3, see Section 6.5). The 
files in this DTN were used to obtain the results discussed in Section 6.8. 
XII.8.1 Main Directory 
All the files associated with this DTN are located in the directory 3crosssections_pp. 
XII.8.2 Level 2 Directories 
The 3crosssections_pp directory includes the three Level 1 directories 
crosssection1, crosssection2, and crosssection3. . These correspond to Cross 
Sections 1, 2 and 3, respectively. 
XII.8.3 Level 3 Directories 
Each of the crosssection1, crosssection2, crosssection3 directories includes 
the following Level 2 subdirectories: 
100kyear Input and output data for the 100,000-year simulation 
10kyear Input and output data for the 10,000-year simulation 
1kyear Input and output data for the 1,000-year simulation 
100year Input and output data for the 100-year simulation 
10year Input and output data for the 10-year simulation 
XII.8.4 Files in Each Level 3 Directory 
Each Level 2 directory includes the following files: 
tc Input file for the 99Tc simulation. 
tc.C(z) Output corresponding to the tc input file (vertical profile). 
tc.C(x) Output corresponding to the tc input file (horizontal profile). 
np Input file for the 237Np simulation. 
np.C(z) Output corresponding to the np input file (vertical profile).

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np.C(x) Output corresponding to the np input file (horizontal profile). 
pu Input file for the 239Pu simulation. 
pu.C(z) Output corresponding to the pu input file (vertical profile). 
pu.C(x) Output corresponding to the pu input file (horizontal profile). 
Note that the file names are the same in all level 2 directories, and only the name of the Level 1 
and/or 2 directory changes.

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XII.9 FILES IN DTN: LB991220140160.009 
This DTN includes the files involved in the 2-D semianalytical FRACL simulations of the 
transport of three radionuclides (99Tc, 237Np, and 239Pu) in vertical cross sections that include all 
the hydrogeologic units from the potential repository horizon to the water table. Transport is 
studied in the three 2-D geological profiles of Cross Sections 1, 2 and 3 (see Section 6.5). The 
files in this DTN were used to obtain the results discussed in Section 6.9. 
XII.9.1 Main Directory 
All the files associated with this DTN are located in the directory 3rosssections. 
XII.9.2 Level 2 Directories 
The 3rosssections directory includes the two Level 1 directories 6mmyr and 34mmyr. 
The first corresponds to a mean present-day infiltration, and the second to a high glacial 
infiltration. 
XII.9.3 Level 3 Directories 
The 6mmyr directory includes the four Level 2 directories crosssection1, 
crosssection2, crosssection3, and crosssection3_perch. The first three 
correspond to Cross Sections 1, 2, 3, respectively (with no perched water), while the fourth 
corresponds to Cross Section 3 with a perched water body. 
The 34mmyr directory includes the three Level 2 directories crosssection1, 
crosssection2 and crosssection3. These correspond to Cross Sections 1, 2, 3, 
respectively (with no perched water). 
XII.9.4 Level 4 Directories 
Each of the Level 3 directories includes the following Level 4 subdirectories: 
100kyear Input and output data for the 100,000-year simulation 
10kyear Input and output data for the 10,000-year simulation 
1kyear Input and output data for the 1,000-year simulation 
100year Input and output data for the 100-year simulation 
10year Input and output data for the 10-year simulation 
XII.9.5 Files in Each Level 4 Directory 
Each Level 2 directory includes the following files:

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tc Input file for the 99Tc simulation. 
tc.C(z) Output corresponding to the tc input file (vertical profile). 
tc.C(x) Output corresponding to the tc input file (horizontal profile). 
np Input file for the 237Np simulation. 
np.C(z) Output corresponding to the np input file (vertical profile). 
np.C(x) Output corresponding to the np input file (horizontal profile). 
pu Input file for the 239Pu simulation. 
pu.C(z) Output corresponding to the pu input file (vertical profile). 
pu.C(x) Output corresponding to the pu input file (horizontal profile). 
Note that the file names are the same in all level 2 directories, and only the name of the level 1, 2 
and/or 3 directory changes.

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XII.10 FILES IN DTN: LB991220140160.010 
This DTN includes the files involved in the T2R3D V1.4 (STN: 10006-1.4-00) 3-D simulations 
of the tracer injections in the Busted Butte field test. The files in this DTN were used to obtain 
the results discussed in Section 6.10. The files are located in two separate file directories that 
correspond to Phase 1A and Phase 1B tests. 
XII.10.1 Directory bbphase1a 
This directory corresponds to the simulations of the Phase 1A of the Busted Butte test, and 
includes the following files: 
MESH The mesh (grid geometry) file that is common to all the 
simulations listed under this file directory. 
uz99bh1 Input file to simulate the borehole 1 test using the S1A flow 
parameters. 
uz99bh1.out Output corresponding to the uz99bh1 input file. 
uz99bh3 Input file to simulate the borehole 3 test using the S1A flow 
parameters. 
uz99bh3.out Output corresponding to the uz99bh3 input file. 
uz99bh4 Input file to simulate the borehole 4 test using the S1A flow 
parameters. 
uz99bh4.out Output corresponding to the uz99bh4 input file. 
usgsbh3 Input file to simulate borehole 3 test using the S2A flow 
parameters. 
usgsbh3.out Output corresponding to the usgsbh3 input file. 
XII.10.2 Directory bbphase1b 
This directory corresponds to the simulations of the Phase 1B of the Busted Butte test, and 
includes the following files: 
MESH The mesh (grid geometry) file that is common to all the 
simulations listed under this file directory.

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uz99_br Input file to simulate bromide breakthrough curves using the S1A 
flow parameters. 
uz99_br.out Output corresponding to the uz99_br input file. 
uz99_br.gasobs Output containing simulation results in specific elements at 
specific times, corresponding to the uz99_br input file. 
uz99_26dfba Input file to simulate 2,6-DFBA breakthrough curves using the 
S1A flow parameters. 
uz99_26dfba.out Output corresponding to the uz99_26dfba input file. 
uz99_26dfba.gasobs Output containing simulation results in specific elements at 
specific times, corresponding to the uz99_26dfba input file. 
uz99_li_kd1 Input file to simulate, using the S1A flow parameters, lithium 
breakthrough curves (use sorption coefficient Kd=1 mL/g). 
uz99_li_kd1.out Output corresponding to the uz99_ li_kd1 input file. 
uz99_li_kd1.gasobs Output containing simulation results in specific elements at 
specific times, corresponding to the uz99_li_kd1 input file. 
uz99_li_kd2 Input file to simulate, using the S1A flow parameters, lithium 
breakthrough curves (use sorption coefficient Kd=2 mL/g). 
uz99_li_kd2.out Output corresponding to the uz99_li_kd2 input file. 
uz99_li_kd2.gasobs Output containing simulation results in specific elements at 
specific times, corresponding to the uz99_ li_kd2 input file. 
usgs99_br Input file to simulate bromide breakthrough curves using the S2B 
flow parameters. 
usgs99_br.out Output corresponding to the usgs99_br input file. 
usgs99_br.gasobs Output containing simulation results in specific elements at the 
specific times, corresponding to the usgs99_br input file.

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XII.11 FILES IN DTN: LB991220140160.011 
This DTN includes the files involved in the 3-D site-scale simulations of flow in the UZ of 
Yucca Mountain using the TOUGH2 V1.4 Module EOS9 V1.4 (STN: 10007-1.4-01) code. 
These simulations were conducted to generate the steady-state conditions, flow fields and 
velocities that are used as inputs for the 3-D site-scale simulations of solute and colloid transport 
through the UZ of Yucca Mountain (see Section 6.11). 
XII.11.1 Main Directories 
All the files associated with this DTN are located in the following directories: 
present Directory of the files corresponding to the present-day infiltration 
regime under the #1 perched water model. 
monsoon Directory of the files corresponding to the monsoon infiltration 
regime under the #1 perched water model. 
glacial Directory of the files corresponding to the glacial infiltration 
regime under the #1 perched water model. 
present_perch Directory of the files corresponding to the mean present-day 
infiltration regime for the #2 perched water model and the noperched 
water model. 
esf_cl_flow Directory of the files corresponding to the flow regime for the 
study of chloride distribution in the ESF. 
XII.11.2 Level 1 Directories 
Each of the present, monsoon and glacial main directories includes the three Level 1 
directories lower, mean and upper. These correspond to the lower, mean and upper 
infiltration of each climatic regime (see Table 6.11). 
The main directory present_perch includes the two Level 1 directories nonperch_mean 
and perch2_mean. These correspond to the non-perched and the #2 perched water models, 
respectively. The main directory esf_cl_flow does not include any subdirectories. 
XII.11.3 Files With Common Names in All Level 1 Directories and in the esf_cl_flow 
Main Directory 
All Level 1 directories and the esf_cl_flow main directory include the following files:

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MESH The mesh (grid geometry) file. 
INCON The input file that records the initial thermodynamic conditions of 
a TOUGH2 simulation run. 
VELOC The output file containing the steady-state velocities across the cell 
boundaries. 
SAVE The output file that records thermodynamic conditions at the end 
of a TOUGH2 simulation run. 
Note that although these files may share the same names, they include different data in the Level 
1 directories and in the esf_cl_flow Main directory. 
XII.11.4 Files With Common Names in the lower Level 1 Directories 
All Level 1 directories with the name lower include the following files: 
lower Input file containing the initial conditions for the EOS9 simulation 
of flow under conditions of low infiltration of the corresponding 
regime (denoted by the main directory name). 
lower.out The output file corresponding to the lower input file. 
Note that although these files may share the same names, they include different data in each 
Level 1 directory. 
XII.11.5 Files With Common Names in the mean Level 1 Directories 
All Level 1 directories with the name lower include the following files: 
mean Input file containing the initial conditions for the EOS9 simulation 
of flow under conditions of mean infiltration of the corresponding 
regime (denoted by the main directory name). 
mean.out The output file corresponding to the mean input file. 
Note that although these files may share the same names, they include different data in each 
Level 1 directory. 
XII.11.6 Files With Common Names in the mean Level 1 Directories 
All Level 1 directories with the name lower include the following files:

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upper Input file containing the initial conditions for the EOS9 simulation 
of flow under conditions of high infiltration of the corresponding 
regime (denoted by the main directory name). 
mean.out The output file corresponding to the upper input file. 
Note that although these files may share the same names, they include different data in each 
Level 1 directory. 
XII.11.7 Files With Common Names in the nonperch_mean and perch2_mean Level 1 
Directories, and in the esf_cl_flow Main Directory 
The nonperch_mean and perch2_mean Level 1 directories and the esf_cl_flow main 
directory include the following files: 
flow In the nonperch_mean and perch2_mean Level 1 
directories, this is the input file containing the initial conditions for 
the EOS9 simulation of flow under conditions of mean present-day 
infiltration under the corresponding perched water conceptual 
model (denoted by the Level 1 directory name). 
In the esf_cl_flow main directory, this is the input file 
containing the initial conditions for the EOS9 simulation of flow 
for the study of the chloride distribution in the ESF. 
flow.out The output file corresponding to the flow input file. 
Note that although these files may share the same names, they include different data in each 
Level 1 directory.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
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XII.12 FILES IN DTN: LB991220140160.012 
This DTN includes the files involved in the 3-D site-scale simulations of solute transport for the 
#1 perched water model under the present-day climatic scenario (see Sections 6.12, 6.13 and 
6.14). All these files are located in the directory Present_case. 
XII.12.1 Input Files Common to Simulations 
These files are common to all the simulations listed in this DTN. All these files are located in 
the subdirectory Pr_mean of the Present_day directory. These are the following: 
MESH The file containing the mesh (grid geometry). 
INDEX Output and/or input file containing the global indices of the 
neighbors (active and/or inactive) of each grid cell. 
UNVEC Output and/or input file containing the x,y and z components of the 
unit vectors normal to the cell interfaces. 
XII.12.2 Files for Transport Simulations for a 
Mean Present-Day Infiltration Regime 
All the files listed in this section are located in the subdirectory Pr_mean of the 
Present_case directory. These are the following: 
VELOC The input file containing the steady-state velocities across the cell 
boundaries. 
INCON_3P Input file containing the initial conditions of three parent 
radionuclides (99Tc, 237Np and 239Pu). 
INCON_3d Input file containing the initial conditions of a parent and two 
daughter radionuclides. 
M_pre_3P Input file for the EOS9nT simulation of the three parent 
radionuclides. The output options in this file limit the simulation 
output to (a) species mass balances and (b) species mass fluxes 
across the repository and the groundwater boundaries. 
M_pre_3P.out Output corresponding to the M_pre_3P input file. 
M_pre_3Pdis Input file for the EOS9nT simulation of the three parent 
radionuclides. The output options lead to printouts of the

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concentration distributions of the three species in the liquid and 
solid phases. 
M_pre_3Pdis.out Output corresponding to the M_pre_3Pdis input file. 
M_pre_3dNp Input file for the EOS9nT simulation of 237Np and its daughters 
(233U and 229Th). The output options are as in the M_pre_3P file. 
M_pre_3dNp.out Output corresponding to the M_pre_3dNp input file. 
M_pre_3dPu Input file for the EOS9nT simulation of 239Pu and its daughters 
(235U and 231Pa). The output options are as in the M_pre_3P file. 
M_pre_3dPu.out Output corresponding to the M_pre_3dPu input file. 
M_pre_3P_nD Same as the M_pre_3P file, but with zero molecular diffusion 
for all species. 
M_pre_3P_nD.out Output corresponding to the M_pre_3P_nD input file. 
M_pre_3dPu_nD Same as the M_pre_3dPu file, but with zero molecular diffusion 
for all species. 
M_pre_3dPu_nD.out Output corresponding to the M_pre_3dPu_nD input file. 
XII.12.3 Files for Transport Simulations for a 
Low Present-Day Infiltration Regime 
All the files listed in this section are located in the subdirectory Pr_low of the Present_ 
case directory. These are the following: 
VELOC The input file containing the steady-state velocities across the cell 
boundaries. 
INCON_3P Input file containing the initial conditions of the three parent 
radionuclides. 
INCON_3d Input file containing the initial conditions of a parent and two 
daughter radionuclides. 
L_pre_3P Input file for the EOS9nT simulation of the three parent 
radionuclides. The output options are as in the M_pre_3P file. 
L_pre_3P.out Output corresponding to the L_pre_3P input file.

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L_pre_3dPu Input file for the EOS9nT simulation of 239Pu and its daughters. 
The output options are as in the M_pre_3P file. 
L_pre_3dPu.out Output corresponding to the L_pre_3dPu input file. 
XII.12.4 Files for Transport Simulations for a 
High Present-Day Infiltration Regime 
All the files listed in this section are located in the subdirectory Pr_high of the Present_ 
case directory. These are the following: 
VELOC The input file containing the steady-state velocities across the cell 
boundaries. 
INCON_3P Input file containing the initial conditions of the three parent 
radionuclides. 
INCON_3d Input file containing the initial conditions of a parent and two 
daughter radionuclides. 
H_pre_3P Input file for the EOS9nT simulation of the three parent 
radionuclides. The output options are as in the M_pre_3P file. 
H_pre_3P.out Output corresponding to the H_pre_3P input file. 
H_pre_3dPu Input file for the EOS9nT simulation of 239Pu and its daughters. 
The output options are as in the M_pre_3P file. 
H_pre_3dPu.out Output corresponding to the H_pre_3dPu input file.

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XII.13 FILES IN DTN: LB991220140160.013 
This DTN includes the files involved in the 3-D site-scale simulations of solute transport for the 
#1 perched water model under the monsoon climatic scenario (see Sections 6.12, 6.13 and 6.14). 
All these files are located in the directory Monsoon_case. 
XII.13.1 Input Files Common to All Simulations 
The files common to all the simulations listed in this DTN are MESH, INDEX and UNVEC. 
These files are identical to those discussed in Section XII.12.1, and can be found in the 
subdirectory Pr_mean of the Present_day directory. 
XII.13.2 Files for Transport Simulations for a Mean Monsoon Infiltration Regime 
All the files listed in this section are located in the subdirectory Mns_mean of the 
Monsoon_case directory. These are the following: 
VELOC The input file containing the steady-state velocities across the cell 
boundaries. 
INCON_3P Input file containing the initial conditions of the three parent 
radionuclides. 
INCON_3d Input file containing the initial conditions of a parent and two 
daughter radionuclides. 
M_mns_3P Input file for the EOS9nT simulation of the three parent 
radionuclides. The output options are as in the M_pre_3P file. 
M_mns_3P.out Output corresponding to the M_mns_3P input file. 
M_mns_3dPu Input file for the EOS9nT simulation of 239Pu and its daughters. 
The output options are as in the M_pre_3P file. 
M_mns_3dPu.out Output corresponding to the M_mns_3dPu input file. 
XII.13.3 Files for Transport Simulations for a Low Monsoon Infiltration Regime 
All the files listed in this section are located in the subdirectory Mns_low of the 
Monsoon_case directory. These are the following: 
VELOC The input file containing the steady-state velocities across the cell 
boundaries.

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INCON_3P Input file containing the initial conditions of the three parent 
radionuclides. 
INCON_3d Input file containing the initial conditions of a parent and two 
daughter radionuclides. 
L_mns_3P Input file for the EOS9nT simulation of the three parent 
radionuclides. The output options are as in the M_pre_3P file. 
L_mns_3P.out Output corresponding to the L_mns_3P input file. 
L_mns_3dPu Input file for the EOS9nT simulation of 239Pu and its daughters. 
The output options are as in the M_pre_3P file. 
L_mns_3dPu.out Output corresponding to the L_mns_3dPu input file. 
XII.13.4 Files for Transport Simulations for a High Monsoon Infiltration Regime 
All the files listed in this section are located in the subdirectory Mns_high of the 
Monsoon_case directory. These are the following: 
VELOC The input file containing the steady-state velocities across the cell 
boundaries. 
INCON_3P Input file containing the initial conditions of the three parent 
radionuclides. 
INCON_3d Input file containing the initial conditions of a parent and two 
daughter radionuclides. 
H_mns_3P Input file for the EOS9nT simulation of the three parent 
radionuclides. The output options are as in the M_pre_3P file. 
H_mns_3P.out Output corresponding to the H_mns_3P input file. 
H_mns_3dPu Input file for the EOS9nT simulation of 239Pu and its daughters. 
The output options are as in the M_pre_3P file. 
H_mns_3dPu.out Output corresponding to the H_mns_3dPu input file.

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MDL-NBS-HS-000008 REV 00 XII-28 March 2000 
XII.14 FILES IN DTN: LB991220140160.014 
This DTN includes the files involved in the 3-D site-scale simulations of solute transport for the 
#1 perched water model under the monsoon climatic scenario (see Sections 6.12, 6.13 and 6.14). 
All these files are located in the directory Glacial_case. 
XII.14.1 Input Files Common to All Simulations 
The files common to all the simulations listed in this DTN are MESH, INDEX and UNVEC. 
These files are identical to those discussed in Section XII.12.1, and can be found in the 
subdirectory Pr_mean of the Present_day directory. 
XII.14.2 Files for Transport Simulations for a Mean Glacial Infiltration Regime 
All the files listed in this section are located in the subdirectory Gl_mean of the 
Glacial_case directory. These are the following: 
VELOC The input file containing the steady-state velocities across the cell 
boundaries. 
INCON_3P Input file containing the initial conditions of the three parent 
radionuclides. 
INCON_3d Input file containing the initial conditions of a parent and two 
daughter radionuclides. 
M_gla_3P Input file for the EOS9nT simulation of the three parent 
radionuclides. The output options are as in the M_pre_3P file. 
M_gla_3P.out Output corresponding to the M_gla_3P input file. 
M_gla_3dPu Input file for the EOS9nT simulation of 239Pu and its daughters. 
The output options are as in the M_pre_3P file. 
M_gla_3dPu.out Output corresponding to the M_gla_3dPu input file. 
XII.14.3 Files for Transport Simulations for a Low Glacial Infiltration Regime 
All the files listed in this section are located in the subdirectory Gl_low of the 
Glacial_case directory. These are the following: 
VELOC The input file containing the steady-state velocities across the cell 
boundaries.

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INCON_3P Input file containing the initial conditions of the three parent 
radionuclides. 
INCON_3d Input file containing the initial conditions of a parent and two 
daughter radionuclides. 
L_gla_3P Input file for the EOS9nT simulation of the three parent 
radionuclides. The output options are as in the M_pre_3P file. 
L_gla_3P.out Output corresponding to the L_gla_3P input file. 
L_gla_3dPu Input file for the EOS9nT simulation of 239Pu and its daughters. 
The output options are as in the M_pre_3P file. 
L_gla_3dPu.out Output corresponding to the L_gla_3dPu input file. 
XII.14.4 Files for Transport Simulations for a High Glacial Infiltration Regime 
All the files listed in this section are located in the subdirectory Gl_high of the 
Glacial_case directory. These are the following: 
VELOC The input file containing the steady-state velocities across the cell 
boundaries. 
INCON_3P Input file containing the initial conditions of the three parent 
radionuclides. 
INCON_3d Input file containing the initial conditions of a parent and two 
daughter radionuclides. 
H_gla_3P Input file for the EOS9nT simulation of the three parent 
radionuclides. The output options are as in the M_pre_3P file. 
H_gla_3P.out Output corresponding to the H_gla_3P input file. 
H_gla_3dPu Input file for the EOS9nT simulation of 239Pu and its daughters. 
The output options are as in the M_pre_3P file. 
H_gla_3dPu.out Output corresponding to the H_gla_3dPu input file.

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MDL-NBS-HS-000008 REV 00 XII-30 March 2000 
XII.15 FILES IN DTN: LB991220140160.015 
This DTN includes the files involved in the 3-D site-scale simulations of solute transport for the 
#2-perched-water model under the mean present-day infiltration regime (see Section 6.15). All 
these files are located in the directory PER_2, and are listed below. 
MESH The file containing the mesh (grid geometry). 
INDEX Output and/or input file containing the global indices of the 
neighbors (active and/or inactive) of each grid cell. 
VELOC The input file containing the steady-state velocities across the cell 
boundaries. 
INCON Input file containing the initial conditions of the three parent 
radionuclides. 
M_pre_3P_p2 Input file for the EOS9nT simulation of (a) the three parent 
radionuclides and (b) the daughters of 239Pu. The output options 
are as in the M_pre_3P file. 
M_pre_3P_p2.out Output corresponding to the M_pre_3P_p2 input file.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-31 March 2000 
XII.16 FILES IN DTN: LB991220140160.016 
This DTN includes the files involved in the 3-D site-scale simulations of solute transport for the 
no-perched-water model under the mean present-day infiltration regime (see Section 6.15). All 
these files are located in the directory No_PER, and are listed below. 
MESH The file containing the mesh (grid geometry). 
INDEX Output and/or input file containing the global indices of the 
neighbors (active and/or inactive) of each grid cell. 
VELOC The input file containing the steady-state velocities across the cell 
boundaries. 
INCON Input file containing the initial conditions of the three parent 
radionuclides. 
M_pre_3P_np Input file for the EOS9nT simulation of (a) the three parent 
radionuclides and (b) the daughters of 239Pu. The output options 
are as in the M_pre_3P file. 
M_pre_3P_np.out Output corresponding to the M_pre_3P_np input file.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-32 March 2000 
XII.17 FILES IN DTN: LB991220140160.017 
This DTN includes the files involved in the 3-D site-scale simulations of colloid transport for the 
#1 perched water model under the mean present-day infiltration regime (see Sections 6.16 and 
6.17).. All these files are located in the subdirectory Colloids of the Present_day 
directory. 
XII.17.1 Input Files Common to All Simulations 
The files common to all the simulations listed in this DTN are MESH, INDEX, UNVEC and 
VELOC. These files are identical to those discussed in Sections XII.12.1 and XII.12.2, and can 
be found in the subdirectory Pr_mean of the Present_day directory. 
XII.17.2 Files for Transport Simulations for a Mean Monsoon Infiltration Regime 
All the files listed in this section are located in the subdirectory Colloids of the 
Present_day directory.. These are the following: 
INCON Input file containing the initial conditions of the three parent 
radionuclides. 
M_pre_4C_no Input file for the EOS9nT simulation of four colloids with different 
particle sizes for Case 1 (see Section 6.16). The output options are 
as in the M_pre_3P file. 
M_pre_4C_no.out Output corresponding to the M_pre_4C_no input file. 
M_pre_4Ca Input file for the EOS9nT simulation of four colloids with different 
particle sizes for Case 2 (see Section 6.16). The output options are 
as in the M_pre_3P file. 
M_pre_4Ca.out Output corresponding to the M_pre_4Ca input file. 
M_pre_4Ca_dis Input file for the EOS9nT simulation of four colloids with different 
particle sizes for Case 2 (see Section 6.16). The output options are 
as in the M_pre_3P_dis file. 
M_pre_4Ca_dis.out Output corresponding to the M_pre_4Ca_dis input file. 
M_pre_4Cb Input file for the EOS9nT simulation of four colloids with different 
particle sizes for Case 3 (see Section 6.16). The output options are 
as in the M_pre_3P file. 
M_pre_4Cb.out Output corresponding to the M_pre_4Cb input file.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-33 March 2000 
M_pre_4Cc Input file for the EOS9nT simulation of four colloids with different 
particle sizes for Case 4 (see Section 6.16). The output options are 
as in the M_pre_3P file. 
M_pre_4Cc.out Output corresponding to the M_pre_4Cc input file. 
M_pre_4Ca_nD Same as the M_pre_4Ca file, but with zero colloidal diffusion for 
all four species.. 
M_pre_4Ca_nD.out Output corresponding to the M_pre_4Ca_nD input file.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 XII-34 March 2000 
XII.18 FILES IN DTN: LB991220140160.019 
This DTN includes parameter values taken and/or computed from information in the scientific 
literature. Four data sets of parameter values are listed in the file inputs_019, along with the 
corresponding reference source.

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XIII-1 
ATTACHMENT XIII. 
DOCUMENT INPUTS REFERENCE SYSTEM

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV 00 March 2000 XIII-2 
INTENTIONALLY LEFT BLANK

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-3 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
1. 
DTN: GS950608312272.001. 
Chemical Data for Pore Water 
from Tuff Cores of USW 
NRG-6, NRG7/7A, UZ-14 
AND UZ-N55, and UE-25 
UZ#16. Submittal date: 
05/30/1995. 
S97476 
_013, 
UZ#16 
N/AReference 
only 
Table 6.3 
Figure 
6.4.4 
Calibration-Cl concentration in 
UE-25 UZ#16. 
For model verification. 
Comparison only. 
N/A N/A N/A N/A 
2. 
DTN: GS990308312242.007. 
Laboratory And Centrifuge 
Measurements Of Physical 
And Hydraulic Properties Of 
Core Samples From Busted 
Butte Boreholes UZTT-BBINJ-
1, UZTT-BB-INJ-3, 
UZTT-BB-INJ-4, UZTT-BBINJ-
6, UZTT-BB-COL-5 and 
UZTT-BB-COL-8. Submittal 
date: 03/22/1999. Initial use. 
Entire TBV-4001 6.10 
Matrix porosity, permeability, 
initial saturation, and rock grain 
density of the field samples. 1 N/A N/A 3 
3. 
DTN: GS990708312242.008. 
Physical and Hydraulic 
Properties of Core Samples 
from Busted Butte Boreholes. 
Submittal date: 07/01/1999. 
Entire TBV-3620 6.10 
Matrix porosity, permeability, 
initial saturation, and rock grain 
density of the field samples. 
1 N/A N/A 3

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-4 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
4. 
DTN: 
LAIT831341AQ96.001. 
Radionuclide Retardation. 
Measurements of Batch 
Sorption Distribution 
Coefficients for Barium, 
Cesium, Selenium, Strontium, 
Uranium, Plutonium, and 
Neptunium. Submittal date: 
11/12/1996. 
Entire 
N/ATechnical 
Product 
Output 
6.5-6.9 
6.11- 
6.15 
6.17 
Sorption coefficient Kd for Np, 
Pu, and U. 
N/A N/A N/A N/A 
5. 
DTN: 
LAJF831222AQ98.007. 
Chloride, Bromide, and 
Sulfate Analyses of Salts 
Leached from ECRBCWAT#
1, #2, and #3 Drill 
core. Submittal date: 
09/09/1998. Initial use. 
Entire TBV-4002 6.4 
Field chloride distribution data 
in the ESF 
1 N/A N/A 3 
6. 
DTN: LA9909JF831222.010. 
Chloride, Bromide, Sulfate, 
and Chlorine-36 Analyses of 
ESF Porewaters. Submittal 
date: 09/29/1999. Initial use. 
Entire 
N/AQualified- 
Verification 
Level 2 
6.4 
Field distribution data in the 
ESF 
N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-5 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
7. 
DTN: LA9909JF831222.012. 
Chloride, Bromide, and 
Sulfate Analyses of Porewater 
Extracted from ESF Niche 
3566 (Niche #1) and ESF 
3650 (Niche #2) Drillcore. 
Submittal date: 09/29/1999. 
Initial use. 
Entire 
N/AQualified- 
Verification 
Level 2 
6.4 
Field distribution data in the 
ESF 
N/A N/A N/A N/A 
8. 
DTN: 
LA9909WS831372.001. 
Busted Butte UZ Transport 
Test: Phase I Collection Pad 
Extract Concentrations. 
Submittal date: 09/29/1999. 
Initial use. 
Entire 
N/AReference 
only 
6.10 Measured tracer concentration. N/A N/A N/A N/A 
9. 
DTN: 
LA9909WS831372.002. 
Busted Butte UZ Transport 
Test: Phase I Collection Pad 
Tracer Loading And Tracer 
Concentrations. Submittal 
date: 09/30/1999. Initial use. 
Entire 
N/AReference 
only 
6.10 Measured tracer concentration. N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-6 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
10. 
DTN: LB971212001254.001. 
DKM Basecase Parameter Set 
For UZ Model with Mean 
Fracture Alpha, Present Day 
Infiltration, and Estimated 
Welded, Non-Welded and 
Zeolitic FMX. Submittal 
date: 12/12/1997. 
Entire 
N/AReference 
only 
6.10 
Calibrated flow parameters for 
dual-permeability model basecase 
in the matrix of the ch1v 
and ch2v layers (porosity, 
permeability, van Genuchten 
and m parameters, residual 
saturation, satiated saturation, 
rock grain density, tortuosity) 
N/A N/A N/A N/A 
11. 
DTN: LB990501233129.001. 
Fracture Properties for the UZ 
Model Grids and Uncalibrated 
Fracture and Matrix 
Properties for the UZ Model 
Layers for AMR U0090, 
Analysis of Hydrologic 
Properties Data. Submittal 
date: 08/25/1999. 
Entire 
N/ATechnical 
Product 
Output 
6.5-6.17 Fracture aperture N/A N/A N/A N/A 
12. 
DTN: LB990501233129.004. 
3-D UZ Model Calibration 
Grids for AMR U0000, 
Development of Numerical 
Grids of UZ Flow and 
Transport Modeling. 
Submittal date; 9/24/1999. 
Entire 
N/ATechnical 
Product 
Output 
6.5-6.9 Hydrogeologic unit profiles N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-7 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
13. 
DTN: LB990701233129.002. 
3-D Model Calibration Grid 
for Calculation of Flow Fields 
using #3 Perched Water 
Conceptual Model (Non- 
Perched Water Model). 
Submittal date: Will be 
submitted with AMR. 
Entire 
N/ATechnical 
Product 
Output 
6.4 
Chloride distribution modeling 
in borehole UE-25 UZ-16 3-D 
flow field (e.g. mesh) 
N/A N/A N/A N/A 
14. 
DTN: LB990801233129.001. 
TSPA Grid Flow Simulations 
for AMR U0050, UZ Flow 
Models and Submodels. 
(Flow Field #1). Submittal 
date: 11/29/1999. 
Entire 
N/ATechnical 
Product 
Output 
6.12- 
6.15 
Present day infiltration  Lower 
bound, (perched water model 
#1) 
N/A N/A N/A N/A 
15. 
DTN: LB990801233129.003. 
TSPA Grid Flow Simulations 
for AMR U0050, UZ Flow 
Models and Submodels. 
(Flow Field #3). Submittal 
date: 11/29/1999. 
Entire 
N/ATechnical 
Product 
Output 
6.5-6.17 
Steady-state fracture and matrix 
saturation 
Present day infiltration- mean 
(perched water model #1) 
N/A N/A N/A N/A 
16. 
DTN: LB990801233129.004. 
TSPA Grid Flow Simulations 
for AMR U0050, UZ Flow 
Models and Submodels. 
Submittal date: 11/29/1999. 
Entire 
N/ATechnical 
Product 
Output 
6.15 
Present-day mean infiltration 
(perched-water model #2) 
N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-8 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
17. 
DTN: LB990801233129.005. 
TSPA Grid Flow Simulations 
for AMR U0050, UZ Flow 
Models and Submodels. 
(Flow Field #5). Submittal 
date: 11/29/1999. 
Entire 
N/ATechnical 
Product 
Output 
6.11- 
6.15 
Present day infiltration-upper 
bound (perched water model 
#1) 
N/A N/A N/A N/A 
18. 
DTN: LB990801233129.007. 
TSPA Grid Flow Simulations 
for AMR U0050, UZ Flow 
Models and Submodels. 
(Flow Field #7). Submittal 
date: 11/29/1999. 
Entire 
N/ATechnical 
Product 
Output 
6.11- 
6.15 
Glacial infiltration-lower bound 
(perched water model #1) N/A N/A N/A N/A 
19. 
DTN: LB990801233129.009. 
TSPA Grid Flow Simulations 
for AMR U0050, UZ Flow 
Models and Submodels. 
(Flow Field #9). Submittal 
date: 11/29/1999. 
Entire 
N/ATechnical 
Product 
Output 
6.11- 
6.15 
Glacial infiltration-mean 
(perched water model #1) N/A N/A N/A N/A 
20. 
DTN: LB990801233129.011. 
TSPA Grid Flow Simulations 
for AMR U0050, UZ Flow 
Models and Submodels. 
(Flow Field #11). Submittal 
date: 11/29/1999. 
Entire 
N/ATechnical 
Product 
Output 
6.11- 
6.15 
Glacial infiltration-upper bound 
(perched water model #1) N/A N/A N/A N/A 
21. 
DTN: LB990801233129.013. 
TSPA Grid Flow Simulations 
for AMR U0050, UZ Flow 
Models and Submodels. 
(Flow Field #13). Submittal 
date: 11/29/1999. 
Entire 
N/ATechnical 
Product 
Output 
6.11- 
6.15 
Monsoon infiltration-lower 
bound (perched water model 
#1) 
N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-9 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
22. 
DTN: LB990801233129.015. 
TSPA Grid Flow Simulations 
for AMR U0050, UZ Flow 
Models and Submodels. 
(Flow Field #15). Submittal 
date: 11/29/1999. 
Entire 
N/ATechnical 
Product 
Output 
6.11- 
6.15 
Monsoon infiltration-mean 
(perched water model #1) N/A N/A N/A N/A 
23. 
DTN: LB990801233129.017. 
TSPA Grid Flow Simulations 
for AMR U0050, UZ Flow 
Models and Submodels. 
(Flow Field #17). Submittal 
date: 11/29/1999. 
Entire 
N/ATechnical 
Product 
Output 
6.11- 
6.15 
Monsoon infiltration-upper 
bound (perched water model 
#1) 
N/A N/A N/A N/A 
24. 
DTN: LB990801233129.019. 
TSPA Grid Flow Simulations 
for AMR U0050, UZ Flow 
Models and Submodels. 
Flow Field #19: Present Day 
Mean Infiltration Map for 
Non-Perched Water 
Conceptual Model. Submittal 
date: will be submitted with 
AMR. 
Entire 
N/ATechnical 
Product 
Output 
6.15 
Present day mean infiltration (no 
perched water model) 
N/A N/A N/A N/A 
25. 
DTN: LB991131233129.003. 
Analytical and Simulation 
Results of Chloride and 
Chlorine-36 Analysis. 
Submittal date: Will be 
submitted with AMR U0050. 
Entire 
N/ATechnical 
Product 
Output 
4.1, 6.4 
Chloride concentration 
distribution 
N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-10 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
26. 
DTN: LB991220140160.019. 
Values from Refereed 
Literature Used as Input in 
AMR U0060. Submittal date: 
Will be submitted with AMR. 
Entire 
N/ATechnical 
Product 
Output 
6.4-6.16 
Simulation input parameters 
from literature. 
N/A N/A N/A N/A 
27. 
DTN: LB997141233129.001. 
Calibrated Basecase 
Infiltration 1-D Parameter Set 
for the UZ Flow and 
Transport Model, FY99. 
Submittal date: 07/21/1999. 
Entire 
N/ATechnical 
Product 
Output 
6.11- 
6.15 
.
Calibrated flow parameters for 
base-case infiltration in the 
matrix of the ch1v and ch2v 
layers (porosity, permeability, 
van Genuchten and m 
parameters, residual saturation, 
satiated saturation, rock grain 
density, tortuosity) 
N/A N/A N/A N/A 
28. DTN: 
MO9901MWDISMMM.000. 
ISM3.1 MINERALOGIC 
MODELS. Submittal date: 
01/22/1999. 
Entire N/AQualification 
Level 2 
Table 4 Geologic profiles and rock 
properties at the three crosssections 
N/A N/A N/A N/A 
29. DTN: 
MO9910MWDISMMM.003. 
ISM3.1 MINERALOGIC 
MODELS. Submittal date: 
10/01/1999. 
Entire N/AReference 
only 
6.12.1.3 
Fig. 
12.21 
Mineralogy plots of % zeolites N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-11 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
30. Abdel-Salam, A. and C.V. 
Chrysikopoulos. 1995. 
Modeling of colloid and 
colloid-facilitated 
contaminant transport in a 
two-dimensional fracture with 
spatially variable aperture. 
Transport in Porous Media, 
20, 197-221. Dordrecht, The 
Netherlands: The Journal 
Editorial Office, Kluwer 
Academic Publishers. TIC: 
applied for. 
pp.199- 
200 
N/AReference 
only 
6.2 N/A N/A N/A N/A N/A 
31. Bates, J.K.; Bradley, J.P.; 
Teetsov, A.; Bradley, C.R.; 
and ten Brink, M.B. 1992. 
Colloid Formation during 
Waste Form Reaction: 
Implications for Nuclear 
Waste Disposal. Science, 
256, 649651. Washington, 
D.C.: American Association 
for the Advancement of 
Science. TIC: 239138. 
Entire N/AReference 
only 
6.2 N/A N/A N/A N/A N/A 
32. Bear, J. 1972. Dynamics of 
Fluid in Porous Media. New 
York, New York: Dover 
Publications. TIC: 217568. 
p.127 N/AReference 
only 
5.1 N/A N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-12 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
33. Benson, C.F. and Bowman, 
R.S. 1994. Tri- and 
Tetrafluorobenzoates as 
Nonreactive Tracers in Soil 
and Groundwater. Soil 
Science Society of America 
Journal, 58, 11231129. 
Madison, Wisconsin: Soil 
Science Society of America. 
TIC: applied for. 
p.1125 N/AReference 
only 
6.10 N/A N/A N/A N/A N/A 
34. Bird, R.B.; Stewart, W.E.; and 
Lightfoot, E.N. 1960. 
Transport Phenomena. New 
York: John Wiley & Sons. 
TIC: 208957. 
p.514 N/AReference 
only 
6.1 N/A N/A N/A N/A N/A 
35. Bodvarsson, G.S.; Boyle, W.; 
Patterson, R.; and Williams, 
D. 1999. Overview of 
Scientific Investigations at 
Yucca Mountainthe 
Potential Repository for High- 
Level Nuclear Waste. 
Journal of Contaminant 
Hydrology 38 (13), 324. 
Amsterdam, The Netherlands: 
Elsevier Science Publishers. 
TIC: 244160. 
pp.8-15 N/AReference 
only 
6.1 N/A N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-13 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
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6. Input Description 
7. TBV/TBD 
Priority 
36. Boggs, J.M. and Adams, E.E. 
1992. Field Study in a 
Heterogeneous Aquifer. 4: 
Investigation of Adsorption 
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33253336. Washington, 
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6.1 N/A N/A N/A N/A N/A 
37. Bowen, B.D. and Epstein, N. 
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38. Bradbury, M.H. and Stephen, 
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6.1 N/A N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-14 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
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Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
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4. Input 
Status 
5. 
Section 
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6. Input Description 
7. TBV/TBD 
Priority 
39. Buddemeier, R.W. and Hunt, 
J.R. 1988. Transport of 
Colloidal Contaminants in 
Groundwater: Radionuclide 
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3, 535548. Amsterdam, The 
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6.1 N/A N/A N/A N/A N/A 
40. Cameron, D.R. and Klute, A. 
1977. Convective- 
Dispersive Solute Transport 
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6.2 N/A N/A N/A N/A N/A 
41. Conca, J.L. and Wright, J. 
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in Gravel under Unsaturated 
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Washington, D.C.: American 
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Entire N/AReference 
only 
6.1 N/A N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-15 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
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Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
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6. Input Description 
7. TBV/TBD 
Priority 
42. Corapcioglu, M.Y.; Abboud, 
N.M.; and Haridas, A. 1987. 
Governing Equations for 
Particle Transport in Porous 
Media. Advances in 
Transport Phenomena in 
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342 
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6.2 N/A N/A N/A N/A N/A 
43. Cook, A.J. 1989. A Desk 
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only 
6.2 N/A N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-16 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
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6. Input Description 
7. TBV/TBD 
Priority 
44. Crump, K.S. 1976. 
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Fourier Series 
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N/A N/A N/A N/A N/A 
45. CRWMS M&O (Civilian 
Radioactive Waste 
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Contractor) 1999a. M&O Site 
Investigations. Activity 
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Entire N/A  
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2 Standards, Codes & Regulations N/A N/A N/A N/A 
46. CRWMS M&O 1999b. M&O 
Site Investigations. Activity 
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2 Standards, Codes & Regulations N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-17 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
47. 
CRWMS M&O 1999c. 
Analysis & Modeling 
Development Plan (DP) for 
U0060 , Radionuclide 
Transport Models under 
Ambient Conditions, Rev. 00. 
TDP-NBS-HS-000013. Las 
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MOL.19990830.0381. 
Entire 
N/A - 
Reference 
only 
2 Standards, Codes & Regulations N/A N/A N/A N/A 
48. 
CRWMS M&O 1999d. UZ 
Flow Models and Submodels. 
MDL-NBS-HS-000006. Las 
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M&O. ACC: 
MOL.19990721.0527. URN- 
0030. 
6 
N/A - 
Reference 
only 
6.4, 
6.10- 
6.16 
N/A N/A N/A N/A N/A 
49. 
CRWMS M&O 1999e. 
Unsaturated Zone and 
Saturated Zone Transport 
Properties. ANL-NBS-HS- 
000019. Las Vegas, Nevada: 
CRWMS M&O. URN-0038. 
6 
N/AReference 
only 
5.2, 6.1, 
6.2, 6.10, 
7.1 
N/A N/A N/A N/A N/A 
50. CRWMS M&O 1999f. UZ 
Colloid Transport Model. 
ANL-NBS-HS-000028. Las 
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only 
5.2, 5.4, 
6.1, 6.16 
N/A N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-18 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
51. CRWMS M&O 1999g. 
Enhanced Design Alternative 
(EDA) II Repository Layout 
for 10 cm/s Ventilation Plan. 
Las Vegas, Nevada: CRWMS 
M&O. ACC: 
MOL.19990409.0102. 
Entire N/AReference 
only 
5.4, 6.1 N/A N/A N/A N/A N/A 
52. CRWMS M&O 1999h. 
Development of Numerical 
Grids for UZ Flow and 
Transport Modeling. ANLNBS-
HS-000015. Las Vegas, 
Nevada: CRWMS M&O. 
ACC: MOL.19990721.0517. 
6 N/AReference 
only 
6.1, 6.4, 
6.5, 6.6, 
6.11 
N/A N/A N/A N/A N/A 
53. CRWMS M&O 2000a. 
Calibrated Properties Model. 
MDL-NBS-HS-000003. Las 
Vegas, Nevada: CRWMS 
M&O. ACC: 
MOL.19990721.0520. URN- 
0053. 
6 N/AReference 
only 
5.1, 6.7, 
6.8, 6.9, 
6.12 
N/A N/A N/A N/A N/A 
54. CRWMS M&O 2000b. Drift- 
Scale Coupled Processes 
(DST and THC Seepage) 
Models. MDL-NBS-HS- 
000001. Las Vegas, Nevada: 
CRWMS M&O. ACC: 
MOL.19990721.0523. URN- 
0054. 
6 N/AReference 
only 
5.1, 5.2, 
6.1 
N/A N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-19 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
55. CRWMS M&O 2000c. 
Seepage Calibration Model 
and Seepage Testing Data. 
MDL-NBS-HS-000004. Las 
Vegas, Nevada: CRWMS 
M&O. ACC: 
MOL.19990721.0521. 
6 N/AReference 
only 
5.3 N/A N/A N/A N/A N/A 
56. CRWMS M&O 2000d. 
Analysis of Hydrologic 
Properties Data. ANL-NBSHS-
000002. Las Vegas, 
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6 N/AReference 
only 
6.1, 6.11 N/A N/A N/A N/A N/A 
57. CRWMS M&O 2000e. 
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6 N/AReference 
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6.11 N/A N/A N/A N/A N/A 
58. Cussler, E.L. 1984. Diffusion: 
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Title: Radionuclide Transport Models Under Ambient Conditions U0060 
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OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
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Status 
5. 
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6. Input Description 
7. TBV/TBD 
Priority 
59. DeHoog, F.R.; Knight, J.H.; 
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N/A N/A N/A N/A N/A 
60. 
de Marsily, G. 1986. 
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6.2 N/A N/A N/A N/A N/A 
61. 
DOE (U.S. Department of 
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Entire 
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only 
6.1 N/A N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-21 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
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6. Input Description 
7. TBV/TBD 
Priority 
62. 
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63. 
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Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-22 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
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Section 
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7. TBV/TBD 
Priority 
64. 
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65. 
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66. 
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Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-23 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
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2. Technical Product Input Source 
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From 
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Priority 
67. 
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6.1 N/A N/A N/A N/A N/A 
68. 
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69. 
Grathwohl, P. 1998. 
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only 
6.1, 6.6, 
6.12, 
6.15 
N/A N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-24 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
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7. TBV/TBD 
Priority 
70. 
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6.16 
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71. 
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6.2 N/A N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-25 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
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Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
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7. TBV/TBD 
Priority 
72. 
Holtta, P.; Siitati-Kauppi, M.; 
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73. 
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74. 
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Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-26 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
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Input Document 8. TBV Due To 
2. Technical Product Input Source 
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3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
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6. Input Description 
7. TBV/TBD 
Priority 
75. 
Hu, Q. and Brusseau, M.L. 
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Entire 
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6.1 N/A N/A N/A N/A N/A 
76. 
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Entire 
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6.2 N/A N/A N/A N/A N/A 
77. 
Jacobsen, O.H.; Moldrup, P.; 
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186 
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only 
6.1 N/A N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-27 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
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3. 
Section 
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From 
Uncontrolled 
Source 
Unconfirmed 
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6. Input Description 
7. TBV/TBD 
Priority 
78. 
Jahnke, F.M. and Radke, C.J. 
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only 
6.1 N/A N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-42 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
121. 
Wemheuer, R.F. 1999. First 
Issue of FY00 NEPO QAP-2- 
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Interoffice correspondence 
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October 1, 1999, 
LV.NEPO.RTPS.TAG.10/99- 
155, with attachments, 
Activity Evaluation for Work 
Package #1401213UM1. 
ACC: MOL.19991028.0162. 
Work 
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only 
6.1 N/A N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-43 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
123. 
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Entire 
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only 
6.1 N/A N/A N/A N/A N/A 
124. 
Wu, Y.S.; Ahlers, C.F.; 
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Entire 
N/AReference 
only 
6.2 N/A N/A N/A N/A N/A 
125. 
Software Code: TOUGH2 
V1.4 Module EOS9 V1.4. 
STN: 10007-1.4-01 
Entire 
N/AQualified/ 
Confirmed/ 
Verified 
6.10 General software use N/A N/A N/A N/A 
126. 
Software Code: TOUGH2 
V1.11 Module EOS9nT V1.0. 
STN: 10065- 
1.11MEOS9NTV1.0-00. 
Entire TBV-4008 6.4-6.16 General software use 1 3 N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-44 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
127. 
Software Code: T2R3D V1.4. 
STN: 10006-1.4-00. 
Entire 
N/AQualified/ 
Confirmed/ 
Verified 
6.10 General software use N/A N/A N/A N/A 
128. 
Software Code: FRACL 
V1.0. STN: 10191-1.0-00 
Entire 
N/AReference 
only 
6.10 Comparison purposes only N/A N/A N/A N/A 
129. 
Software routine: xtract1.f 
V1.0. STN: 10213-1.0-00. 
Entire 
N/AQualified/ 
Confirmed/ 
Verified 
6.10 General software use N/A N/A N/A N/A 
130. 
Software routine: xtract2.f 
V1.0. STN: 10214-1.0-00. 
Entire 
N/AQualified/ 
Confirmed/ 
Verified 
6.10 General software use N/A N/A N/A N/A 
131. Software routine: xtract2a.f 
V1.0. STN: 10215-1.0-00. 
Entire 
N/AQualified/ 
Confirmed/ 
Verified 
6.10 General software use N/A N/A N/A N/A 
132. Software routine: xtract2b.f 
V1.0. STN: 10216-1.0-00. 
Entire 
N/AQualified/ 
Confirmed/ 
Verified 
6.10 General software use N/A N/A N/A N/A 
133. 
Software routine: xtract5.f 
V1.0. STN: 10217-1.0-00. 
Entire 
N/AQualified/ 
Confirmed/ 
Verified 
6.10 General software use N/A N/A N/A N/A

Title: Radionuclide Transport Models Under Ambient Conditions U0060 
MDL-NBS-HS-000008 REV00 March 2000 XIII-45 
OFFICE OF CIVILIAN RADIOACTIVE WASTE MANAGEMENT 
DOCUMENT INPUT REFERENCE SHEET 
1. Document Identifier No./Rev.: 
MDL-NBS-HS-000008/Rev. 00D 
Change: Title: 
Radionuclide Transport Models under Ambient Conditions 
Input Document 8. TBV Due To 
2. Technical Product Input Source 
Title and Identifier(s) with Version 
3. 
Section 
Unqual. 
From 
Uncontrolled 
Source 
Unconfirmed 
2a 
4. Input 
Status 
5. 
Section 
Used in 
6. Input Description 
7. TBV/TBD 
Priority 
134. Software routine: xtract6.f 
V1.0. STN: 10218-1.0-00. 
Entire 
N/AQualified/ 
Confirmed/ 
Verified 
6.10 General software use N/A N/A N/A N/A 
AP-3.15Q.1 Rev. 06/30/1999