Water Quality Assessment and TMDLs for the
Flathead River Headwaters
Planning Area, Montana
Prepared by:
U.S. Environmental Protection Agency
Montana Operations Office,
Flathead National Forest,
and Tetra Tech, Inc.
Project Manager: Ron Steg
Contributing Authors:
Jason Gildea
Tina Laidlaw
Donna Pridmore
Ron Steg
Photos by Montana Fish, Wildlife, and Parks,
Flathead National Forest,
and Tetra Tech, Inc.
Prepared for the
Montana Department of Environmental Quality
December 31, 2004
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Flathead River Headwaters TPA
Contents
CONTENTS
1.0 Introduction 1
2.0 Watershed Characterization 5
2.1 Physical Characteristics 5
2.1.1 Climate 5
2.1.2 Hydrology 8
2.1.2.1 Flow Data 8
2.1.2.2 Stream Gradient 11
2.1.2.3 Significant Flood Events: 1964 and 1996 13
2.1.3 Stream Types 15
2.1.4 Topography 18
2.1.5 Geology 20
2.1.6 Landform Groups 24
2.1.7 Land Use and Land Cover 27
2.1.8 Soils 29
2.1.8.1 Soil Map Units 29
2.1.8.2 Sediment Hazard Ranking 31
2.1.9 Forest Harvest History 35
2.1.10 Fire History 39
2.1.11 Forest Roads 43
2.2 Biological Characteristics 47
2.2.1 Threatened and Endangered Species 47
2.2.2 Fisheries 48
2.3 Cultural Characteristics 49
2.3.1 Population 49
2.3.2 Land Ownership 50
3.0 Water Quality Impairment Status 53
3.1 3 03 (d) List Status 53
3.2 Applicable Water Quality Standards 57
3.2.1 Classification and Beneficial Uses 57
3.2.2 Standards 59
3.2.2.1 Sediment 59
3.2.2.2 Nutrients 60
3.3 Water Quality Goals and Indicators 61
3.3.1 Sediment Targets 66
3.3.1.1 McNeil Core - Percent Subsurface Substrate Fines < 6.35 mm 66
3.3.1.2 Substrate Scores 66
3.3.1.3 Macroinvertebrates 67
3.3.1.4 Surface Fines 67
Sediment Supplemental Indicators 69
3.3.1.5 Macroinvertebrates 69
3.3.1.6 Periphyton 70
3.3.1.7 Pfankuch Ratings 70
3.3.1.8 Fish Population 72
3.3.1.9 Suspended Sediment Concentration 73
3.3.1.10 Turbidity 73
3.3.1.11 Sediment Sources 73
3.3.2 Nutrient T argets 75
3.3.2.1 EPA Ecoregion Nutrient Criteria 75
3.3.2.2 Benthic Chlorophyll-a 75
3.3.3 Nutrient Supplemental Indicators 75
3.3.3.1 Hilsenhoff Biotic Index 76
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Contents
Flathead River Headwaters TPA
3.3.3.2 Mountain IBI 76
3.3.3.3 Water Column Chlorophyll-a 76
3.3.3.4 Dissolved Oxygen 76
3.3.3.5 Nutrient Sources 77
3.4 Current Water Quality Impairment Status 78
3.4.1 North Fork Flathead River Watershed 78
3.4.1.1 Big Creek 78
3.4.1.2 Red Meadow Creek 80
3.4.1.3 Whale Creek 85
3.4.1.4 South Fork of Coal Creek 92
3.4.1.5 North Fork Coal Creek: Siltation 98
3.4.1.6 North Fork Coal Creek: Nutrients 104
3.4.1.7 Lower Coal Creek 107
3.4.2 Middle Fork Flathead River Watershed 116
3.4.2.1 Challenge Creek 116
3.4.2.2 Granite Creek 118
3.4.2.3 Skyland Creek 125
3.4.2.4 Morrison Creek 131
3.4.3 South Fork Flathead River Watershed 136
3.4.3.1 Hungry Horse Reservoir 136
3.4.3.2 South Fork Flathead River 136
3.4.3.3 Sullivan Creek 138
3.5 Water Quality Impairment Status Summary 144
4.0 Coal Creek Sediment TMDL 147
4.1 Significant Sources of Sediment in the Coal Creek Watershed 147
4.1.1 Roads 148
4.1.2 Bank Erosion 152
4.1.3 Fire 155
4.1.4 Harvest Activities 156
4.1.5 Other Potential Anthropogenic Sediment Sources 157
4.1.6 Large Woody Debris 158
4.1.7 Summary of Sources 161
4.1.8 Source Assessment Uncertainty 163
4.2 Targets 163
4.3 TMDL and Allocations 164
4.3.1 Existing Road Allocation 166
4.3.2 Historical/Current Harvest Allocation 166
4.3.3 Bank Erosion Allocation 166
4.3.4 Other Allocation 166
4.3.5 Future Roads and Harvest Allocation 166
4.3.6 Phase II Allocation Strategy 166
4.4 Monitoring and Assessment Strategy 167
4.4.1 Trend Monitoring 167
4.4.2 Supplemental Monitoring 167
4.4.3 North Fork Nutrient Assessment 167
4.5 Restoration Strategy 168
4.6 Dealing with Uncertainty and Margin of Safety 168
5.0 Voluntary Water Quality Improvement Strategy for Red Meadow,
Whale, and Sullivan Creeks 169
5.1 Identified Potential Sediment Sources 169
5.2 Monitoring Strategy 169
5.3 Conceptual Implementation Strategy 169
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Flathead River Headwaters TPA
Contents
6.0 Public Involvement 175
7.0 References 177
Appendix A: Landform Groups in the Flathead TMDL Planning Area A-l
Appendix B: Flathead National Forest and Montana Fish, Wildlife, and Parks
Source Assessments B-l
Appendix C: 2002 and 2003 Field Sampling Data C-l
Appendix D: McNeil Core, Substrate Score, and Fisheries Data D-l
Appendix E: Response to Public Comments E-l
Appendix F: Public Notice of Availability G-l
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Contents
Flathead River Headwaters TPA
TABLES
Table 1-1. Impaired Streams Within the Flathead River Headwaters TPA on the 1996 and 2002
Montana 303(d) Lists 3
Table 1-2. Causes of Impairment in the Flathead River Headwaters TPA 4
Table 2-1. Average Total Precipitation at Selected Gages (inches) 7
Table 2-2. Average Total Snowfall at Selected Gages (inches) 7
Table 2-3. Active Flow Gages in the Flathead Headwaters TMDL Planning Area 8
Table 2-4. Summary Flow Characteristics of the 303(d)-Listed Streams 11
Table 2-5. Rosgen Stream Classifications for the Flathead River Headwaters TMDL
Planning Area 16
Table 2-6. Landform Groups in the Flathead River Headwaters TMDL Planning Area 24
Table 2-7. Land Use/Land Cover in the FTPA (Source: USGS National Land Cover Dataset
based on 1992 Landsat Thematic Mapper Imagery) 27
Table 2-8. Summary of Sediment Hazard 32
Table 2-9. Road Density Risk Ratings in Miles per Square Mile 43
Table 2-10. Road Densities in Selected Watersheds Within the FTPA 43
Table 2-11. Federally Threatened, Endangered, and USFS Region 1 Sensitive
Species in the FTPA 47
Table 2-12. Comparison of 303(d)-Listed Streams With Core and Priority Bull Trout Watersheds 49
Table 2-13. Land Ownership and Management by Drainage 50
Table 3-1. Impaired Streams Within the Flathead River Headwaters TPA on the 1996 and 2002
Montana 303(d) Lists 54
Table 3-2. Causes of Impairment in the Flathead River Headwaters TPA 55
Table 3-3. Montana Surface Water Classifications and Designated Beneficial Uses 58
Table 3-4. Applicable Rules for Sediment-Related Pollutants 60
Table 3-5. Numeric Dissolved Oxygen Criteria 61
Table 3-6. Summary of the Proposed Sediment Targets and Supplemental Indicators for
the Flathead TPA 62
Table 3-7. Summary of the Proposed Nutrient Targets and Supplemental Indicators for
the Flathead TPA 63
Table 3-8. Mass Wasting Rating Description 71
Table 3-9. Vegetative Bank Protection Description 72
Table 3-10. Cutting Description 72
Table 3-11. Deposition Description 72
Table 3-12. Nutrient Concentration Targets for the North Fork Coal Creek 75
Table 3-13. Numeric Dissolved Oxygen Criteria 77
Table 3-14. Selected Pfankuch Ratings for Red Meadow Creek 82
Table 3-15. Comparison of Available Data with the Proposed Targets and Supplemental
Indicators for Red Meadow Creek 84
Table 3-16. Pfankuch Ratings for Segments of Whale Creek 88
Table 3-17. Comparison of Available SSC Data for Whale Creek with the Supplemental Indicator
Values 89
Table 3-18. Comparison of Available Data with the Proposed Targets and Supplemental Indicators
for Whale Creek 91
Table 3-19. Pfankuch Ratings for Segments of South Fork Coal Creek 95
Table 3-20. Comparison of Available SSC Data for South Fork Coal Creek with the Supplemental
Indicator Values 95
Table 3-21. Comparison of Available Data to the Proposed Targets and Supplemental Indicators
for South Fork Coal Creek 97
iv
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Flathead River Headwaters TPA
Contents
Table 3-22. Pfankuch Ratings for Segments of North Fork Coal Creek 101
Table 3-23. Comparison of Available SSC Data for North Fork Coal Creek with the Supplemental
Indicators 101
Table 3-24. Comparison of Available Data with the Proposed Targets and Supplemental
Indicators for North Fork Coal Creek (Sediment) 103
Table 3-25. Nutrient Data and Comparison with the Targets 104
Table 3-26. Comparison of Available Data with the Proposed Targets and Supplemental
Indicators for North Fork Coal Creek (Nutrients) 106
Table 3-27. Pfankuch Ratings for Segments of Lower Coal Creek 112
Table 3-28. Comparison of Available Data with the Proposed Targets and Supplemental Indicators
for Lower Coal Creek 115
Table 3-29. Pfankuch Ratings for Segments of Granite Creek 121
Table 3-30. Comparison of Available SSC Data for Challenge Creek with the Supplemental
Indicator Values 122
Table 3-31. Comparison of Available SSC Data for Dodge Creek with the Supplemental Indicator
Values 122
Table 3-32. Comparison of Available Data with the Proposed Targets and Supplemental Indicators
for Granite Creek 124
Table 3-33. Pfankuch Ratings for Segments of Skyland Creek 127
Table 3-34. Comparison of Available SSC Data for Skyland Creek with the Supplemental
Indicator Values 128
Table 3-35. Comparison of Available Data with the Proposed Targets and Supplemental
Indicators for Skyland Creek 130
Table 3-36. Comparison of Available Data with the Proposed Targets and Supplemental
Indicators for Morrison Creek 135
Table 3-37. Pfankuch Ratings for Segments of Sullivan Creek 141
Table 3-38. Comparison of Available SSC Data for Sullivan Creek with the Supplemental
Indicator Values 141
Table 3-39. Comparison of Available Data with the Proposed Targets and Supplemental
Indicators for Sullivan Creek 143
Table 3-40. Current Water Quality Impairment Status for the Flathead River Headwaters TPA 145
Table 4-1. Road Characteristics in the Coal Creek Watershed 148
Table 4-2. Sediment Loads from Roads in the Coal Creek Watershed3 150
Table 4-3. Estimates of Bank Erosion and Sediment Loads 153
Table 4-4. Large Woody Debris Conditions in Selected Tributaries in the Coal Creek Watershed .... 159
Table 4-5. Summary of Sediment Sources in the Coal Creek Watershed 161
Table 4-6. Coal Creek Water Quality Goals 164
Table 4-7. Load Allocations for Sediment in Coal Creek 165
Table 5-1. Potential Sources of Sediment in Selected Watersheds 170
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Flathead River Headwaters TPA
FIGURES
Figure 1 -1. Location of the Flathead River Headwaters TPA 2
Figure 2-1. Distribution of NOAA climate monitoring stations within the FTPA 6
Figure 2-2. Active USGS flow monitoring stations within the FTPA 9
Figure 2-3. Historical average monthly flows at three USGS gaging stations on the
Middle Fork, North Fork, and South Fork Flathead rivers 10
Figure 2-4. Profile of the North Fork Flathead River: International border to confluence with
the Middle Fork Flathead River 12
Figure 2-5. Profile of the Middle Fork Flathead River: Headwaters to confluence with the
North Fork Flathead River 12
Figure 2-6. Profile of the South Fork Flathead River: Danaher to Hungry Horse Reservoir 13
Figure 2-7. Mean monthly discharge in the North Fork, Middle Fork, and South Fork
Flathead rivers compared to flood peaks in 1964 and 1996 14
Figure 2-8. Rosgen stream types for selected watersheds in the North Fork Flathead River basin.... 17
Figure 2-9. Rosgen stream types for selected watersheds in the Middle Fork Flathead River basin.. 17
Figure 2-10. Rosgen stream types for selected watersheds in the South Fork Flathead River basin.... 18
Figure 2-11. Shaded relief of the FTPA 19
Figure 2-12. General geology of the North Fork Flathead River watershed 21
Figure 2-13. General geology of the Middle Fork Flathead River watershed 22
Figure 2-14. General geology of the South Fork Flathead River watershed 23
Figure 2-15. Landform groups for selected watersheds in the North Fork Flathead River basin 25
Figure 2-16. Landform groups for selected watersheds in the Middle Fork Flathead River basin 25
Figure 2-17. Landform groups for selected watersheds in the South Fork Flathead River basin 26
Figure 2-18. Land use/land cover in the FTPA 28
Figure 2-19. Major soil units in the FTPA 30
Figure 2-20. Sediment hazard ratings for selected watersheds in the North Fork Flathead
River basin 33
Figure 2-21. Sediment hazard ratings for selected watersheds in the Middle Fork Flathead
River basin 33
Figure 2-22. Sediment hazard ratings for selected watersheds in the South Fork Flathead
River basin 34
Figure 2-23. Harvest trends in selected watersheds in the North Fork Flathead River basin 36
Figure 2-24. Harvest trends in selected watersheds in the Middle Fork Flathead River basin 37
Figure 2-25. Harvest trends in selected watersheds in the South Fork Flathead River basin 38
Figure 2-26. Fire history in the North Fork Flathead River watershed 40
Figure 2-27. Fire history in the Middle Fork Flathead River watershed 41
Figure 2-28. Fire history in the South Fork Flathead River watershed 42
Figure 2-29. Roads and stream crossings in selected watersheds in the North Fork Flathead
River basin 44
Figure 2-30. Roads and stream crossings in selected watersheds in the Middle Fork Flathead
River basin 45
Figure 2-31. Roads and stream crossings in selected watersheds in the South Fork Flathead
River basin 46
Figure 3-1. Location of the 303(d)-listed streams 56
Figure 3-2. Weight-of-evidence approach for determining beneficial use impairments 64
Figure 3-3. Methodology for determining compliance with water quality standards 65
Figure 3-4. North Fork Flathead River watershed 79
Figure 3-5. Red Meadow Creek watershed 80
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Flathead River Headwaters TPA
Contents
Figure 3-6. Age 1 and older bull trout and Westslope cutthroat trout densities in Red Meadow
Creek 82
Figure 3-7. Whale Creek watershed 85
Figure 3-8. Bull trout redd counts in Whale Creek 87
Figure 3-9. Age 1 and older bull trout densities in Whale Creek 88
Figure 3-10. South Fork Coal Creek watershed 92
Figure 3-11. Age 1 and older bull trout and Westslope cutthroat trout densities in South Fork Coal
Creek 94
Figure 3-12. North Fork Coal Creek watershed 98
Figure 3-13. Age 1 and older bull trout and Westslope cutthroat trout densities in North Fork Coal
Creek 100
Figure 3-14. Coal Creek watershed 107
Figure 3-15. McNeil core values for Lower Coal Creek 108
Figure 3-16. McNeil core and bull trout redd count trends in Lower Coal Creek 109
Figure 3-17. McNeil core values at six sites in the Flathead River Headwaters TPA 109
Figure 3-18. Age 1 and older bull trout densities in Lower Coal Creek Ill
Figure 3-19. Bull trout redd counts in Lower Coal Creek Ill
Figure 3-20. Middle Fork Flathead River watershed 117
Figure 3-21. Granite Creek watershed 119
Figure 3-22. Bull trout redd counts for Granite Creek 121
Figure 3-23. Skyland Creek watershed 125
Figure 3-24. Morrison Creek watershed 131
Figure 3-25. Bull trout densities in Morrison Creek 133
Figure 3-26. Bull trout redd counts in Morrison Creek 133
Figure 3-27. South Fork Flathead River watershed 137
Figure 3-28. Sullivan Creek watershed 138
Figure 3-29. Bull trout redd counts in Sullivan Creek and Quintonkon Creek 140
Figure 4-1. Location of roads in the Coal Creek watershed 148
Figure 4-2. Roads up to full BMP standards in the Coal Creek watershed 149
Figure 4-3. Plugged culvert at Road 1693 151
Figure 4-4. Active stream eroding road prism on Road 5278 151
Figure 4-5. Plugged culvert on Road 1604 151
Figure 4-6. Example of BMP to divert water from the road surface 151
Figure 4-7. Location of bank erosion sites in Coal Creek as identified by MFWP 153
Figure 4-8. Bank erosion at Old Road culvert (Map ID #1) 154
Figure 4-9. Bank erosion on North Fork Coal Creek (Map ID #13) 154
Figure 4-10. Bank erosion on North Fork Coal Creek (Map ID #15) 154
Figure 4-11. Effects of the Moose Fire and vegetative regrowth since 2001 (Note the shrub and
herbaceous vegetation that has already resulted in excellent ground cover) 155
Figure 4-12. Clear-cut land in the Coal Creek watershed (Year 2000) 156
Figure 4-13. Historical (1980s) clear-cut land in the Coal Creek watershed 156
Figure 4-14. Old skid trail with stream formation in the Mathias Creek watershed 157
Figure 4-15. Eroding soils in the Mathias Creek watershed 157
Figure 4-16. Location of LWD sites 159
Figure 4-17. Portion of Coal Creek artificially straightened; lack of LWD 160
Figure 4-18. Accumulation of LWD with accumulating deposits 160
Figure 4-19. Accumulation of LWD with accumulating deposits 160
Figure 4-20. Distribution of sediment sources 162
Figure 4-21. Distribution of sediment sources (Without Moose Fire) 162
vii
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Contents
Flathead River Headwaters TPA
Figure 5-1. Examples of sources of sediment in the Whale Creek watershed 171
Figure 5-2. Examples of sources of sediment in the Red Meadow Creek watershed 172
Figure 5-3. Examples of sources of sediment in the Sullivan Creek watershed 173
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Flathead River Headwaters TPA
Executive Summary
Executive Summary
The Flathead River Headwaters Total Maximum Daily Load (TMDL) Planning Area (TPA) drains
approximately 4,369 square miles in northwestern Montana and Canada. Twelve stream segments and
one reservoir in the Flathead River Headwaters TPA appeared on Montana's 1996 Clean Water Act
section 303(d) list. The listed causes of impairment included flow alteration, other habitat alterations,
nutrients, suspended solids, and siltation. Cold-water fish and aquatic life were the beneficial uses listed
as impaired or threatened. Montana Department of Environmental Quality (MDEQ) revised the 303(d)
list in 2002 using a new procedure, and two waters were removed from the list based on the revised listing
procedure. A watershed-scale approach was used to evaluate beneficial uses in the following waters:
Big Creek Challenge Creek Granite Creek
Hungry Horse Reservoir Lower Coal Creek Morrison Creek
North Fork Coal Creek Red Meadow Creek South Fork Coal Creek
South Fork Flathead River Sullivan Creek Whale Creek
A summary of the way in which each of these waters has been addressed is provided in Table 1.
It has been determined that the cold-water fishery and aquatic life beneficial uses in Red Meadow Creek,
Whale Creek, South Fork Coal Creek, North Fork Coal Creek, Granite Creek, and Morrison Creek are
fully supported. These waters are not considered impaired due to sediment-related causes (siltation or
suspended solids), and therefore no TMDLs are required. However, minor anthropogenic sediment
sources were identified in Red Meadow, Whale, and Sullivan creeks. A Voluntary Water Quality
Improvement Strategy is proposed to improve the overall watershed health in those three streams.
Although the available data do not support the conclusion presented in the 1996 303(d) list that North
Fork Coal Creek is impaired due to nutrients, there is still some uncertainty because of limited data.
Additional water quality data have been collected to address these uncertainties and will be evaluated to
make a final determination. If it is found that anthropogenic sources of nutrients are not causing an
impairment, documentation will be provided to the MDEQ so that the 303(d) list status of this water body
can be changed in 2006 (when MDEQ is to propose the next 303(d) list). If, on the other hand, it is
determined that anthropogenic sources of nutrients are causing impairment, a TMDL will be prepared.
The following waters were also considered in the analyses, but they are not addressed herein because they
were found to be fully supporting on the 2002 303(d) list, all necessary TMDLs have already been
completed, or the waters were not listed for a pollutant:
South Fork Flathead River (flow and habitat alteration, no pollutants)
Hungry Horse Reservoir (fully supporting on 2002 303(d) list)
Big Creek (TMDL approved May 9, 2003)
Challenge Creek (fully supporting on 2002 303(d) list)
Finally, unlike the populations in many of the other North Fork Flathead River tributaries, bull trout
populations have failed to rebound in Lower Coal Creek. The cause of this impairment is unknown. The
fact that the substrate conditions are slightly less than optimal, based on comparison with proposed target
values, might or might not be contributing to this impairment. Other factors, such as physical habitat
condition (e.g., large woody debris, number of pools, barriers, stream temperature) or high loads of
sediment delivered to the stream from natural sources like eroding banks or the recent Moose Fire, could
be the cause. Or, perhaps, a combination of factors are responsible. Given the uncertainty, a TMDL
focusing on addressing all known anthropogenic sediment sources and further study to identify the
cause(s) of the bull trout population decline is proposed herein.
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Executive Summary
Flathead River Headwaters TPA
Table 1. Summary of Required TMDL Elements for the Flathead River Headwaters TMDL
Planning Area
Water Bodies,
Pollutants of Concern,
and Current
Impairment Status
The following seven individual water body/pollutant combinations were addressed by
demonstrating that they currently meet water quality standards (WQS):
Red Meadow Creek (listed for siltation, meeting WQS)
Whale Creek (listed for siltation, meeting WQS)
South Fork Coal Creek (listed for siltation, meeting WQS)
North Fork Coal Creek (listed for siltation and nutrients, meeting WQS for
siltation, proposed plan to collect additional data regarding nutrients)
Granite Creek (listed for siltation, meeting WQS)
Skyland Creek (listed for siltation, meeting WQS)
Morrison Creek (listed for siltation, meeting WQS)
A TMDL has been prepared for Lower Coal Creek (listed for siltation), which addresses
the entire Coal Creek Watershed (including South Fork and North Fork Coal).
Because a watershed-scale approach was taken, the following waters were also
considered in the analyses. They were not addressed because they were found to be
fully supporting on the 2002 303(d) list, all necessary TMDLs have already been
completed, or the waters were not listed for a pollutant:
South Fork Flathead River (flow and habitat alteration, no pollutants)
Hungry Horse Reservoir (fully supporting on 2002 303(d) list)
Big Creek (TMDL approved May 9, 2003)
Challenge Creek (fully supporting on 2002 303(d) list)
Section 303(d)(1) or
303(d)(3) TMDL
303(d)(1) TMDL to address siltation in the Coal Creek watershed
Impaired Beneficial
Uses
All waters appeared on the 1996 and/or 2002 303(d) lists for partial support, or threatened
status, for the cold-water fishery and/or aquatic life beneficial uses.
Pollutant Sources
Sediment: Natural (e.g., fire, flood, bank erosion), and anthropogenic, associated with
current or historical forest harvest and roads.
Nutrients (North Fork only): Unknown at this time.
Target Development
Strategies
The current water quality impairment status of each of the waters originally listed
on the 1996 303(d) list was evaluated using a weight-of-evidence approach with
a suite of targets and supplemental indicators.
Targets for Coal Creek watershed include threshold values for McNeil Cores;
substrate scores; percent surface fines smaller than 2 millimeters; and dinger
richness.
TMDLs
Reduction in sediment loads from all known anthropogenic sediment sources (Coal Creek
watershed only)
Allocation
Phased allocation, in which Phase I addresses the known anthropogenic sediment
sources and Phase II provides for further study to address uncertainties (Coal Creek
watershed only).
Restoration Strategies
Water Quality Improvement Plan to address identified sediment sources in Red
Meadow, Whale, and Sullivan creeks.
A phased restoration strategy is proposed for the Coal Creek watershed, in
which Phase I addresses known anthropogenic sediment sources and additional
studies are conducted to address uncertainties. Phase II is to be determined
based on Phase I.
Margin of Safety
For the Coal Creek watershed, a margin of safety is provided by conservative
assumptions and proposed additional studies to address uncertainties.
Seasonal
Considerations
The focus of the Coal Creek watershed sediment TMDL is on annual sediment loading.
There does not appear to be a seasonal critical condition that needs to be addressed.
x
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Flathead River Headwaters TPA
Introduction
1.0 INTRODUCTION
The Flathead River Headwaters Total Maximum Daily Load (TMDL) Planning Area (TPA) drains
approximately 4,369 square miles in northwestern Montana and Canada (Figure 1-1). Twelve stream
segments and one reservoir in the Flathead River Headwaters TPA appeared on Montana's 1996 Clean
Water Act section 303(d) list, and the listing information is shown in Tables 1-1 and 1-2 (MDEQ, 1996).
The causes of impairment include flow alteration, other habitat alterations, nutrients, suspended solids,
and siltation. The Montana Department of Environmental Quality (MDEQ) revised the 303(d) list in
2002 using a new procedure. The updated 2002 303(d) listings are shown in Tables 1-1 and 1-2.
Challenge Creek and Hungry Horse Reservoir were removed from the 2002 303(d) list on the basis of the
revised listing procedure.
The purposes of this document are to provide an updated assessment of all waters within this TPA
appearing on either the 1996 or 2002 303(d) list, to provide recommendations for future modifications to
Montana's 303(d) list with respect to these water bodies, and to provide water quality
improvement/restoration plans to address the significant anthropogenic sources of impairment identified
through this process. The relevant physical, chemical, biological, and socioeconomic characteristics of
the environment in which the subject water bodies exist are described in Section 2.0, Watershed
Characterization. A summary and evaluation of all available water quality data and updated water quality
impairment determinations are presented in Section 3.0, Water Quality Impairment Status. Section 4.0
includes a sediment TMDL for Coal Creek, including all the necessary TMDL components. Finally, a
water quality improvement plan for Red Meadow, Whale, and Sullivan creeks is presented in Section 5.0.
1
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Introduction
Flathead River Headwaters TPA
10
Flathead
County
O Cities
, A s ' Counties
^ Lakes
/ Major Streams
Watersheds
North Fork Flathead River
Middle Fork Flathead River
South Fork Flathead River
20 Miles
Figure 1-1. Location of the Flathead River Headwaters TPA.
2
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Flathead River Headwaters TPA
Introduction
Table 1-1. Impaired Streams Within the Flathead River Headwaters TPA on the 1996 and 2002
Montana 303(d) Lists
Watershed
Sub-Drainage and
Water body No.
Use
Class
Year
Listed
Cold Water
Fishery
Aquatic Life
Recreation
(Swimmable)
Industry
Agriculture
Drinking
Water
Big Creek
B1
1996
P
P
X
X
X
X
MT76Q002-050
2002
TMDL Completed
Red Meadow Creek
B1
1996
P
P
X
X
X
X
MT76Q002-020
2002
P
P
F
F
F
X
North Fork
Flathead
River
Whale Creek
B1
1996
T
X
X
X
X
X
MT76Q002-030
2002
P
P
F
F
F
X
South Fork Coal Creek
B1
1996
P
P
X
X
X
X
MT76Q002-040
2002
P
P
F
F
F
X
Coal Creek
B1
1996
P
P
X
X
X
X
MT76Q002-080
2002
P
P
F
F
F
X
North Fork Coal Creek
B1
1996
P
P
X
X
X
X
MT76Q002-070
2002
P
P
F
F
F
X
Granite Creek
B1
1996
X
P
X
X
X
X
MT76I002-010
2002
P
P
F
F
F
X
Middle Fork
Flathead
River
Skyland Creek
B1
1996
P
P
X
X
X
X
MT76I002-020
2002
X
X
X
F
F
X
Challenge Creek
B1
1996
p
p
X
X
X
X
MT76I002-040
2002
Not Listed
Morrison Creek
B1
1996
P
p
X
X
X
X
MT76I002-050
2002
P
p
F
F
F
X
South Fork
1996
P
p
X
X
X
X
South Fork
Flathead
Flathead River
MT76J001-010
B1
2002
X
X
p
F
F
X
Sullivan Creek
B1
1996
P
p
X
X
X
X
River
MT76J003-010
2002
X
X
F
F
F
X
Hungry Horse Reservoir
B1
1996
P
p
F
F
F
F
MT76J002-1
2002
Not Listed
Impairment Status Definitions for Table 1-1:
P = partial support of beneficial use.
F = full support of beneficial use.
T = threatened support of beneficial use.
X = sufficient credible data not available.
3
-------
Introduction
Flathead River Headwaters TPA
Table 1-2. Causes of Impairment in the Flathead River Headwaters TPA
Watershed
Sub-Drainage and
Water body No.
Use
Class
Year
Listed
Probable
Causes
North Fork
Flathead River
Big Creek
MT76LJ003-050
B1
1996
Habitat alter/siltation
2002
TMDL completed
Red Meadow Creek
MT76Q002-020
B1
1996
Habitat alter/siltation
2002
Habitat alter/siltation
Whale Creek
MT76Q002-030
B1
1996
Habitat alter/siltation
2002
Habitat alter/siltation
South Fork Coal Creek
MT76Q002-040
B1
1996
Habitat alter/siltation
2002
Habitat alter/siltation
Coal Creek
MT76Q002-080
B1
1996
Siltation
2002
Siltation
North Fork Coal Creek
MT76Q002-070
B1
1996
Nutrients/siltation
2002
Siltation
Middle Fork
Flathead River
Granite Creek
MT76I002-010
B1
1996
Habitat alter/ siltation/suspended
solids
2002
Siltation/bank erosion
Skyland Creek
MT76I002-020
B1
1996
Habitat alter/ siltation/suspended
solids
2002
No SCD
Morrison Creek
MT76I002-050
B1
1996
Habitat alter/siltation
2002
Habitat alter/siltation
Challenge Creek
MT76I002-040
B1
1996
Habitat alter/siltation
2002
Not Listed
South Fork
Flathead River
Below HHD
South Fork
Flathead River
MT76J001-010
B1
1996
Habitat alterations
Flow alterations
2002
Flow alterations
Sullivan Creek
MT76J003-010
B1
1996
Habitat alterations
2002
No SCD
Hungry Horse Reservoir
MT76J002-1
B1
1996
Flow alterations
siltation
suspended solids
2002
Not listed
Note: Alter= alternation (s): SCD= sufficient credible data.
4
-------
Flathead River Headwaters TPA
Watershed Characterization
2.0 WATERSHED CHARACTERIZATION
The intent of this section is to put the subject water bodies into the context of the watersheds in which
they occur. This section should provide the reader with a general understanding of the environmental
characteristics of the watershed that might have relevance to the 303(d)-listed causes of impairments. This
section also provides some detail regarding watershed characteristics that might play a significant role in
driving pollutant loading (e.g., geographic distribution of soil types, vegetative cover, land use).
2.1 Physical Characteristics
2.1.1 Climate
Weather stations at Polebridge (Station ID 246615), West Glacier (Station ID 248809), and Hungry
Horse Dam (Station ID 244328) were used to characterize climatic conditions in the North Fork, Middle
Fork, and South Fork Flathead rivers, respectively (Figure 2-1).
The weather variations for the entire Flathead Headwaters region are the result of the influence of
maritime patterns from the Pacific Ocean. The general easterly flow by lower layers of the atmosphere
common at this latitude of the Pacific Northwest is modified by the mountain complexes of western
Montana and central Idaho. The high mountains in the Continental Divide, directly east of the Flathead
region, form an effective barrier to severe, cold Artie patterns flowing south through Canada. The valleys
experience many days with dense fog or low stratus cloud layers during the winter months due to
radiational cooling of the dense, valley bottom air with relatively warmer Pacific-source air moving over
the top.
Precipitation varies widely with season, elevation, and location. Sections of the higher portions of the
North Fork of the Flathead have as much as 120 inches of mean annual precipitation. The greatest
percentage of precipitation falls as snow during the winter months. The density of the mountain snowpack
increases from about 20 percent water equivalency in early winter to about 35 percent in April. Average
total precipitation and average annual snowfall for each of the three watersheds in the Flathead River
Headwaters TMDL Planning Area (FTPA) are summarized in Table 2-1 and Table 2-2.
5
-------
Watershed Characterization
Flathead River Headwaters TPA
Grave Creek J\~
Lincoln
County
\r- . _ canada_ _
\> UNITED STATES-
-
^Badger Pass
Teton
County
Poison Kerr
h Snotel Stations
ฎ Climate Stations
N 'Counties
f V
Major Streams
Lakes
Watersheds
North Fork
Middle Fork
South Fork
County
Kraft Creek 0
North Fork Jocko
a
Lewis and Clark
County
Figure 2-1. Distribution of NOAA climate monitoring stations within the FTPA.
6
-------
Flathead River Headwaters TPA
Watershed Characterization
Table 2-1. Average Total Precipitation at Selected Gages (inches)
Station
Polebridge
West
Glacier
Hungry
Horse Dam
Jan
Feb
Mar
Apr
May
Mc
Jun
nth
Jul
Aug
Sep
Oct
Nov
Dev
Annual
Mean
2.62
1.86
1.47
1.31
1.75
2.30
1.41
1.32
1.31
1.62
2.40
2.60
21.98
3.38
2.36
1.87
1.85
2.55
3.29
1.72
1.60
2.04
2.32
3.08
3.29
29.35
3.53
2.61
2.31
2.29
2.80
3.43
1.78
1.79
2.28
2.89
3.72
3.67
33.10
Period of Record at Polebridge = 7/1/1948 to 7/31/2000.
Period of Record at West Glacier = 10/1/1949 to 12/31/2002.
Period of Record at Hungry Horse = 7/2/1948 to 12/31/2002.
Table 2-2. Average Total Snowfall at Selected Gages (inches)
Polebridge
Jan
Feb
Mar
Apr
May
Jun
Jul
Aug
Sep
Oct
Nov
Dec
Ave.
Total
31.4
17.7
10.9
3.4
0.5
0.3
0.0
0.0
0.2
2.8
15.8
24.9
Ave.
Depth
19
22
19
5
0
0
0
0
0
0
3
11
Annual Mean Total =107.8
West Glacier
Jan
Feb
Mar.
Apr
May
Jun
Jul
Aug
Sep
Oct
Nov
Dec
Ave.
Total
38.8
22.6
15.0
3.6
0.5
0.2
0.0
0.0
0.1
1.9
16.7
37.3
Ave.
Depth
18
21
18
6
0
0
0
0
0
0
2
9
Annual Mean Total =136.8
Hungry Horse Dam
Jan
Feb
Mar
Apr
May
Jun
Jul
Aug
Sep
Oct
Nov
Dec
Ave.
Total
23.5
14.4
9.2
1.1
0.2
0.1
0.0
0.0
0.0
1.7
8.1
21.1
Ave.
Depth
12
14
10
1
0
0
0
0
0
0
2
4
Annual Mean Total =79.4
Period of Record at Polebridge = 7/1/1948 to 7/31/2000.
Period of Record at West Glacier = 10/1/1949 to 12/31/2002.
Period of Record at Hungry Horse = 7/2/1948 to 12/31/2002.
7
-------
Watershed Characterization
Flathead River Headwaters TPA
2.1.2 Hydrology
2.1.2.1 Flow Data
The U.S. Geological Survey (USGS) National Water Information System (NWIS) online database lists 34
flow gages in the FTPA. There are 7 active flow gages with current and historical flow data (Table 2-3)
and 27 inactive flow gages with historical data. The USGS active flow monitoring sites and the regional
drainage pattern are displayed in Figure 2-2.
Flow between the monitoring stations at the Middle Fork Flathead River at West Glacier (1235700), the
North Fork Flathead near Columbia Falls (12355500), and the South Fork Flathead above Twin Creek,
above Hungry Horse Reservoir (12359800), are compared in Figure 2-3. On average, peak flows in the
South Fork above Hungry Horse Reservoir arrive considerably earlier in the year than in the other two
drainages in the FTPA. This difference is due to elevation and temperature differences in the South Fork
Flathead River watershed (lower elevations, warmer temperatures), which cause snowmelt to occur
earlier.
Water quality and quantity monitoring stations were maintained on the 303(d)-listed streams in the FTPA
from the late 1970s through the mid-1990s. Flow characteristics extracted from the EPA Legacy
STORET database for the 303(d) drainages are summarized in Table 2-4.
The regional drainage patterns are dendritic and controlled by the geologic structure of the surrounding
mountain ranges. The Rocky Mountain Trench extends from southeast to northwest through the Mission
and Flathead valleys, with extensional half-graben faults through the Swan, North Fork, South Fork, and
Middle Fork valleys (Constenius, 1996). The region is deeply mantled by reworked glacial till and
outwash, which mask the interactions between ground water and surface water.
Table 2-3. Active Flow Gages in the Flathead Headwaters TMDL Planning Area
Station ID
Station Name
Drainage
Area (mi2)
12355000
Flathead River at Flathead British Columbia
427
12355500
North Fork Flathead River near Columbia Falls, MT
1,548
12358500
Middle Fork Flathead River at West Glacier, MT
943
12359800
South Fork Flathead R above Twin Cr near Hungry Horse, MT
1,160
12362000
Hungry Horse Reservoir near Hungry Horse, MT
1,654
12362500
South Fork Flathead River near Columbia Falls, MT
1,663
12363000
Flathead River at Columbia Falls, MT
4,464
8
-------
Flathead River Headwaters TPA
Watershed Characterization
>235500#
_ CANADA
UNITED STATES
Glacier
County
&
Flathead
County
Teton
County
Lewis and Clark
County
ฉ Active USGS Flow Gages
^^'Counties
Major Streams
Lakes
Watersheds
North Fork
Middle Fork
South Fork
Figure 2-2. Active USGS flow monitoring stations within the FTPA.
9
-------
Watershed Characterization
Flathead River Headwaters TPA
12000
10000 -
ฃ
? 8000 -
a
g, 6000 -
ra
o 4000 -
-------
Flathead River Headwaters TPA
Watershed Characterization
Table 2-4. Summary Flow Characteristics of the 303(d)-Listed Streams
Drainage
Name
FNF
Station
I.D.
Period
of
Record
Drainage
Area
(mi2)
Main Stem
Length
(mi)
Average
Gradient
(%)
Average
Sinuosity
Mean
Annual
"reported"15
Q(cfs)
Peak
"reported"
Q
(cfs)
Whale
FL7002
(lower)
1977 to
1994
64.1
21 3
26.1
1.02
261.2
1,189.0
Red
Meadow
FL7003
(lower)
1978 to
1981
29.5
13.9
28.4
1.02
57.2
200.4
Upper Coal
(N. Fork)
FL7009
1983 to
1995
23.4
9.0
36.3
1.01
110.4
494.0
South Fork
Coal
FL7010
1983 to
1995
18.5
8.1
29.4
1.01
96.6
450.6
Lower Coal
w/o Cyclone
FL7011
1983 to
1995
40.2
10.0
28.6
1.02
236.2
1,141.0
Granite
(Challenge)3
FL6005
1987 to
1995
28.7
Confluence
Challenge,
Dodge to
MF 8.2
25.5
1.02
16.4
129.6
Granite
(Dodge)3
FL6012
1983 to
1995
CO
CO
60.0
Morrison
FL6006
1980
50.5
14.8
19.3
1.03
9.5
19.2
Skyland
FL6009
1980
to1993
8.3
5.5
19.5
1.02
16.5
80.2
Sullivan
FL4004
1978 to
1989
72.9
13.9
33.1
1.02
202.1
1,000.0
a The monitoring stations used for Granite are on the primary tributaries, Challenge and Dodge, which form
Granite Creek at confluence. Granite Creek continues from the confluence south by southwest into the
wilderness and on to the Middle Fork River.
b Discharge measurements were collected as "snapshots" during spring high flows and then sporadically
throughout the water year; therefore, the average annual "reported" flows do not reflect actual channel
capacity.
2.1.2.2 Stream Gradient
The valleys of the North and Middle forks in the FTPA flow through wide floodplains. Hungry Horse
dam impounded the South Fork in 1949, flooding the lower valley reaches. Figure 2-4, Figure 2-5, and
Figure 2-6 compare the gradients of the three major tributaries in the FTPA.
The average gradient for the Middle Fork is 16 to 20 feet per mile higher than the average gradients of the
North and South Forks. The "headwaters" of the Middle Fork are the Continental Divide. The down-
gradient direction is east to west, as opposed to the down-gradient directions of the North and South
forks, which are north to south and south to north, respectively. The North and South forks parallel the
Continental Divide, whereas the Middle Fork flows perpendicular to and from the Continental Divide.
11
-------
Watershed Characterization
Flathead River Headwaters TPA
Ave. Gradieat=34 6/mi River mi|es
Figure 2-4. Profile of the North Fork Flathead River: International border to confluence with the
Middle Fork Flathead River.
Ave. Gradient=50 ti/mi River miles
Figure 2-5. Profile of the Middle Fork Flathead River: Headwaters to confluence with the North
Fork Flathead River.
12
-------
Flathead River Headwaters TPA
Watershed Characterization
70
Figure 2-6. Profile of the South Fork Flathead River: Danaher to Hungry Horse Reservoir.
2.1.2.3 Significant Flood Events: 1964 and 1996
Extreme flood events can significantly alter the morphological characteristics of stream channels and can
also affect the condition of the stream's floodplains and riparian corridors. In some cases, the resulting
changes are evident many years after the events. Two such events have occurred in the FTPA, one in
1964 and one in 1996. Figure 2-7 illustrates these high-flow events as recorded by USGS in the three
major rivers in the FTPA.
On June 7 and 8, 1964, the entire Flathead River watershed experienced rainfall varying from 3 to 16
inches over 40 hours. The rain fell on a deeper-than-normal snowpack, and the saturated snow and soil
mantle provided the instrumental factors necessary to produce extreme runoff and flood conditions
(Lundeen et al., 1964). The three forks of the Flathead each carried a record volume of runoff, although
the South Fork River runoff was mitigated by significant storage capacity in Hungry Horse Reservoir.
Lower valley areas were protected by Flathead Lake, which stored runoff from the North Fork, Middle
Fork, and Swan rivers. All the main rivers were running at normal spring flow prior to the storm and
were unable to carry all the surface runoff, producing flood flows in valley areas. Damages were most
severe in the Middle Fork and South Fork areas, with lesser amounts along the North Fork and Swan
rivers. Flathead Valley residents between Columbia Falls and Kalispell sustained extensive flood losses
to crops, livestock, and homes. Resource damages to fisheries and watershed values along the main rivers
and tributary streams occurred in the Flathead National Forest (FNF). Restoration of transportation
facilities was the largest and most costly flood expense.
The Forest Service conducted surveys of flood damages immediately, dealing mainly with National
Forest damages. The damages were classified into three types:
1. Loss of resources
2. Damage to developments
3. Loss or interruption of business
4,800
4,600
(/>
E
c
o
(0
>
0)
LU
3,000
0 10 20
Ave. Gradient=30 ft/mi
30 40
River miles
50
60
13
-------
Watershed Characterization
Flathead River Headwaters TPA
FHPA Big River Flow with Flood Comparison
Monthly Mean Q
~
NF-1911 to 2002: 1548 Sq.Mi.
ฆ
MF-1940 to 2002: 1128 Sq.Mi.
A
SF above HH Reservoir- 1965 to 2002: 1160 Sq.Mi.
ฆ
MF-1964 Flood Peak
~
NF-1996 Flood Peak
ฆ
MF-1996 Flood Peak
A
SF-1996 Flood Peak
NF-1964 Flood Peak
Figure 2-7. Mean monthly discharge in the North Fork, Middle Fork, and South Fork Flathead
rivers compared to flood peaks in 1964 and 1996.
This summary addresses only the loss of resources that directly relate to watershed values, sedimentation,
and fisheries habitat.
The FNF submitted a report to the Bureau of State Fisheries that summarized the flood damage to these
forest resources. The damage to fisheries habitat was extensive on the east side of the FNF, particularly
the Middle Fork. Above the mouth of Bear Creek, 45 miles of Middle Fork River bottom was scarred.
Approximately 109 miles of tributary streams that contained spawning habitat were severely scarred.
Skyland and Dickey creeks had washouts and slides that damaged roads. Marion Creek washed out the
Essex Creek road. U.S. Highway 2 sustained major damage where it directly encroaches on the Middle
Fork floodplain and was closed to all traffic for 2 months.
The South Fork River sustained severe flood damage to 60 miles of river bottom and approximately 104
miles of tributary streams, particularly in the Spotted Bear River, Upper and Lower Twin creeks,
Blackbear Creek, and the White River. All the side drainage roads around Hungry Horse Reservoir
required extensive maintenance after the storm and floodculvert and ditch cleaning, debris removal,
replacement of road surface material, and replacement of eroded fills. Bridges or approaches were
washed out at Emery, Tiger, Margaret, Riverside, Murray, Deep, Logan, Dead Horse, Lower, and Upper
Twin creeks.
The North Fork River scours every spring (Lundeen et al., 1964), but the flood damaged an additional 25
miles of tributary streams. The main North Fork road was washed out south of Big Creek where the river
flows adjacent to the road. Bridge footings and approaches were washed out at Red Meadow, Whale, and
Moose creeks. The Whale Creek road washed out for 500 feet at Ninko Creek, and the Whale Buttes
bridge was damaged. The bridge was washed out on Coal Creek. On Big Creek, the Hallowat bridge
14
-------
Flathead River Headwaters TPA
Watershed Characterization
washed out, the approaches and wingwalls were damaged at the Skookoleel bridge, and the Canyon Creek
cutover was washed out.
The high floodwater velocity and force carried maximum sediment as a result of bank sluffing and
undercutting, scouring old channels down to bedrock, and cutting new channels.
The flood event in 1996 resulted from a weather pattern similar to that which precipitated the 1964 flood
event. A larger-than-normal snowpack was inundated by an early rainstorm that generated more runoff
than channel capacity. Again, Hungry Horse Reservoir and Flathead Lake served as storage and
prevented major damages.
2.1.3 Stream Types
The stream channels and valley bottoms in the FTPA represent the entire range of variability, from
narrow V-shaped valleys with bedrock waterfalls to broad, flat valley bottoms with meandering streams
in unconfined valleys. Valley forms and stream shape result in different sediment transport and
deposition patterns. In uppermost reaches, the capacity to transport sediments exceeds sediment supply,
so erosion is more common than deposition. In stream reaches that flatten and begin to meander, the
capacity to transport sediments typically balances the amount of available sediments. A small change in
water volume determines the occurrence of erosion or deposition. As stream gradients continue to flatten
downstream, deposition is dominant over erosion, except when high peak flows occur to erode upper
channel banks and transport the sediment downstream.
The Rosgen Stream Classification System (Rosgen, 1988) provides a method for categorizing streams
according to their morphological characteristics. Morphological characteristics include factors such as
channel gradient, sinuosity, width/depth ratio, dominant particle size of bed and bank materials, channel
entrenchment, and channel confinement. A Rosgen Stream Type Classification (level 1) was developed
for the FNF in 1999 using digital elevation models (DEMs). The computer models reliably identify only
A, B, C, and E stream types. Rosgen stream types for the subject streams are listed in Table 2-5. Stream
classification maps for each of the subject watersheds are presented in Figure 2-8, Figure 2-9, and, Figure
2-10.
15
-------
Watershed Characterization
Flathead River Headwaters TPA
Table 2-5. Rosgen Stream Classifications for the Flathead River Headwaters TMDL Planning
Area
Stream
Percent
Drainage
Density
Miles per
total
Drainage
Area
Total
(mi /
Stream
Stream
stream
Watershed
Name
(mi2)
Stream (mi)
mi2)
Type
Type
miles
Red
Meadow
Creek
A
57.4
89.3
29.5
64.3
2.18
B
2.30
3.58
C
4.30
6.69
E
0.20
0.31
A
96.2
87.7
Whale Creek
64.1
109.7
1.71
B
5.50
5.01
C
6.80
6.19
E
1.20
1.09
North Fork
Flathead
River
A
25.0
89.3
South Fork
18.5
28.0
1.51
B
1.50
5.37
Coal Creek
C
1.49
5.33
E
0.00
0.00
A
40.6
91.6
Upper Coal
23.4
44.3
1.89
B
1.39
3.14
Creek (NF)
C
2.40
5.42
E
0.00
0.00
Lower
Coal Creek
w/o Cyclone
A
47.6
83.7
40.2
56.9
1.42
B
5.90
10.4
C
3.10
5.45
E
0.40
0.70
A
41.6
72.9
Granite
28.7
57.1
1.99
B
5.3
9.2
Creek
C
7.7
13.4
E
2.6
4.5
Middle Fork
Flathead
River
A
15.2
83.1
Skyland
8.3
18.3
2.20
B
1.9
10.3
Creek
C
1.2
6.6
E
0
0
A
64.7
83.6
Morrison
50.5
77.4
1.53
B
8.5
11.0
Creek
C
3.8
4.9
E
0.4
0.5
South Fork
Flathead
River
A
129.8
90.9
Sullivan
72.9
142.8
1.96
B
5.6
3.9
Creek
C
7.1
4.9
E
0.2
0.3
16
-------
Flathead River Headwaters TPA
Watershed Characterization
PalntKldgl)
lIMCOWt
COUNTY
f
~
i
Retfltn Typปป
FLATHEAD
COUNTY
Figure 2-8. Rosgen stream types for selected watersheds in the North Fork Flathead River basin.
JF
FI.ATME.iD
COUNT*'
3/
\
Rosg^n 53pmซt* Tvphs
A /A
Ay B
/v#" Court*#
Stream
f 1 C-ranrt* CmV. Wotcrefwd
"J Skyiar*d Crt#fc Yi'ฃurih#d
j Moms-fli* Crปfk Wjflmhcd
Glacmr NalionaiSParh
j | F div <=!athซ*d Ru*rVป.ajปri.ft^a
Figure 2-9. Rosgen stream types for selected watersheds in the Middle Fork Flathead River basin.
17
-------
Watershed Characterization
Flathead River Headwaters TPA
Figure 2-10. Rosgen stream types for selected watersheds in the South Fork Flathead River
basin.
2.1.4 Topography
The FTPA is within the Northern Rocky Mountain Physiographic Province. There are five major
mountain ranges and intervening narrow valleys. The mountain ranges are the Whitefish, Salish, Mission,
Flathead, and Swan ranges. Elevations in the FTPA range from over 10,000 feet mean sea level (MSL) at
some of the high mountain peaks to a low of approximately 3,000 feet MSL near the confluence of the
three forks with the main stem of the Flathead River (Figure 2-11).
18
-------
Flathead River Headwaters TPA
Watershed Characterization
County
_canada_
UNITED STATES" "
Flathead
County
Lake
County
Glacier
County
Lincoln
County
Missoula
County
Pondera
County
County
t
t
>
t
t
\
\
Lewis and Clark
County
Figure 2-11. Shaded relief of the FTPA.
19
-------
Watershed Characterization
Flathead River Headwaters TPA
2.1.5 Geology
Surface geology in the North Fork Flathead River watersheds (Red Meadow Creek, Whale Creek, Coal
Creek) is composed mostly of slightly metamorphosed sedimentary rocks (Belt supergroup) and
associated tills (Smith, 2002) (Figure 2-12). These formations are relatively old, mostly Precambrian in
age (Proterozoic era, 450-2,500 million years old). Pleistocene-aged glacial tills (1.8 million to 11,000
years old) from the last major glaciation fill the valleys. The Belt group consists mostly of alternating
argillite and siltite beds with some quartzite (Harrison et al., 2000). These rocks are all slightly
metamorphosed and therefore relatively hard (especially quartzite) and resistant to erosion. Dolomites
and limestones are also common in the Belt group. Rocks generally weather to form silty soils that are
neutral to slightly alkaline. Moving north in the North Fork watershed, sandstones and shales become
more prevalent and make up the majority of the lower (downstream) Red Meadow Creek watershed.
These rocks are not metamorphosed, and they are less resistant to weathering than the Belt group rocks.
Whale Creek watershed is similar to Red Meadow Creek watershed, but also has a large percentage of
older glacial and alluvial outwash near the mouth. Coal Creek is made up almost entirely of the Belt
group rocks.
Geology in the Middle Fork Flathead River watershed is similar to that of the North Fork watershed. It is
dominated by Belt group rocks, with some sandstones and shales in the southeastern portion of the
watershed (Figure 2-13). Granite Creek and Skyland Creek watersheds are similar to other watersheds
and are composed mostly of the older Belt group rocks. Morrison Creek watershed is dominated by the
younger shales and sandstones.
The Sullivan Creek watershed, in the South Fork Flathead River watershed, has a geology that is similar
to the North Fork watersheds and is composed mostly of slightly metamorphosed sedimentary rocks
(Figure 2-14).
The effects of geology on watershed and sediment processes are discussed in more detail in Sections 2.1.6
(Landform Groups) and 2.1.8 (Soils).
20
-------
Flathead River Headwaters TPA
Watershed Characterization
_ CANADA
UNITED STATES
GLACIER
COUNTY
CreeK
LINCOLN
COUNTY
'olebridge
FLATHEAD
COUNTY
LtekelMcDonald
Olney
West Glacier
O
Surface Geology
Highly Weathered Belt Till
Lacustrine Sediments
Lakes and Reservoirs
Metasedimentary Tills (Belt)
| Outwash and Other Older Coarse
Alluvial Deposits
| Landslide Deposits
Recent Coarse Alluvium
Recent Fine Alluvium
Sandstone and Shale Tills
~ North Fork Flathead
River Watershed
/\' Counties
O Cities
/\/ Streams
5 Miles
Figure 2-12. General geology of the North Fork Flathead River watershed.
21
-------
Watershed Characterization
Flathead River Headwaters TPA
O Coram
FLATHEAD
COUNTY
r~| Middle Fork Flathead
River Watershed
Counties
O Cities
A/ Streams
Surface Geology
Highly Weathered Belt Till
Lacustrine Sediments
Lakes and Reservoirs
M eta sedimentary Tills (Belt)
Outwash and Other Older Coarse
Alluvial Deposits
J". Landslide Deposits
Recent Coarse Alluvium
Recent Fine Alluvium
Sandstone and Shale Tills
Figure 2-13. General geology
of the
Middle
10 Miles
Fork Flathead River watershed.
O Kiowa
GLACIER
COUNTY
East Glacier Park
o
Summit
PONDERA
COUNTY
22
-------
Flathead River Headwaters TPA
Watershed Characterization
o
OEssex
FLATHEAD
COUNTY
Co
O O
Hungry Ho
Columbia Falig^
Columbia H
Swan Lake
O
LAKE
COUNTY
<
COUNTY I
Salmon PrairieO
1 ~| South Fork Flathead _
River Watershed |
/\ Counties \
O Cities <
/y Streams *y CondorO
Surface Geology MISSOIIIA
ฆฆ Highly Weathered Belt Till rnriiirrv
Lacustrine Sediments COUNTY
Lakes and Reservoirs
M eta sedimentary Tills (Beit)
Outwash and Other Older Coarse
Alluvial Deposits
. Landslide Deposits
j Recent Coarse Alluvium
Recent Fine Alluvium
Sandstone and Shale Tills
23
-------
Watershed Characterization
Flathead River Headwaters TPA
2.1.6 Landform Groups
Landform and vegetation are the dominant physical features that affect watershed functions and
processes. Landforms regulate how and where water flows across the landscape. Ford et al. (1997)
described seven landform groups in the 303(d) listed watersheds in the FTPA: Valley Bottoms,
Breaklands, Steep Alpine Glaciated Land, Glaciated Mountain Slopes, Mountain Slopes and Ridges,
Mass Wasted and Colluvial Deposits, and Frost Shattered Mountain Ridges. Table 2-6 summarizes the
landform groups for each watershed, and the groups are also shown in Figures 2-15 through 2-17. A
description of each landform group is provided in Appendix A.
Table 2-6. Landform Groups in the Flathead River Headwaters TMDL Planning Area
Watershed
Watershed
Name
Area
Valley Bottoms
(VA)
Breaklands (BK)
Steep Alpine
Glaciated (STGLM)
Glaciated Mount,
slopes (GLMS)
Mountain Slopes
Ridges (MSRI)
Mass Wasted
Slopes (MWSL)
Frost Shattered
Mountain Ridges
(FSMR)
North Fork
Flathead
River
Red Meadow
Creek
Acres
861
2,272
10,565
4,334
871
0
0
%
4.6
12
55.9
22.9
4.6
0
0
Whale
Creek
Acres
3,450
3,595
27,027
6,119
653
148
0
%
8.4
00
CO
65.9
14.9
1.6
0.4
0
South Fork
Coal Creek
Acres
205
1,315
8,539
1,513
284
0
0
%
1.7
11.1
72
12.8
2.4
0
0
North Fork
Coal Creek
Acres
353
1,902
11,223
1,176
293
0
0
%
2.4
12.7
75.1
7.9
2
0
0
Coal Creek,
Lower
Acres
2,224
6,078
9,280
5,398
2,602
0
0
%
8.6
23.6
36.1
21
10.1
0
0
Middle
Fork
Flathead
River
Granite
Creek
Acres
355
1,367
12,298
2,931
1,362
0
0
%
1.9
7.5
67.2
16
7.4
0
0
Skyland
Creek
Acres
814
842
15,747
2,632
4,619
125
0
%
3.3
3.4
63.6
10.6
18.6
0.5
0
Morrison
Creek
Acres
958
2,820
20,539
4,652
1,641
786
655
%
3
00
CO
64.1
14.5
5.1
2.5
2
South Fork
Flathead
River
South Fork
Flathead River
below HH dam
Acres
440
1,926
5,356
1,219
1,169
0
0
%
4.3
18.6
51.8
11.8
11.3
0
0
Sullivan
Creek
Acres
0
9,935
27,265
5,961
3,491
0
0
%
0
21.3
58.4
12.8
7.5
0
0
24
-------
Flathead River Headwaters TPA
Watershed Characterization
Figure 2-15. Landform groups for selected watersheds in the North Fork Flathead River basin.
25
-------
Watershed Characterization
Flathead River Headwaters TPA
-------
Flathead River Headwaters TPA
Watershed Characterization
2.1.7 Land Use and Land Cover
Land use and land cover for each of the three watersheds in the FTPA is summarized in Table 2-7 and
shown in Figure 2-18. The land cover in the FTPA is predominately forested with intermittent grasslands
and shrub complexes naturally formed by wildfire or by various configurations due to timber
management. Less than 1 percent of the total FTPA is composed of developed lands (residential or
commercial) or agricultural lands (e.g., row crops, pasture hay).
Table 2-7. Land Use/Land Cover in the FTPA (Source: USGS National Land Cover Dataset based
on 1992 Landsat Thematic Mapper Imagery)
% of Watershed
Cover Type
North Fork
Middle Fork
South Fork
Open Water
1.77
1.61
2.26
Perennial Ice/Snow
0.19
0.13
0.05
Low Intensity Residential
0
0
0.01
High Intensity Residential
0
0
0
Commercial/Industrial
0.04
0.12
0.01
Bare Rock/Sand/Clay
4.33
5.44
3.23
Quarries/Strip Mines/Gravel
0
0
0
Transitional
0.84
0
0.19
Deciduous Forest
0.38
0.51
0.12
Evergreen Forest
75.89
75.62
80.06
Mixed Forest
0.01
0.07
0.1
Shrubland
9.79
9.45
6.28
Orchards/Vineyards/Others
0
0
0
Grassland/Herbaceous
6.03
6.65
7.6
Pasture/Hay
0.2
0.07
0
Row Crops
0
0
0
Small Grains
0
0
0
Fallow
0
0
0
Urban/Recreational Grasses
0
0
0
Woody Wetlands
0.42
0.31
0.1
Emergent Herb. Wetlands
0.1
0.02
0
27
-------
Watershed Characterization
Flathead River Headwaters TPA
N
,_canada
, united states ~
W E
s
Glacier
County
Teton
County
Lewis and Clark
County
/Counties
_and Use
ฆ ฆ
' !
zz
Low Intensity Residential
Orchards/Vineyards/Other
Comrnercial/lndu strial/T ransportation
Grasslands/Herbaceous
zz
Bare R ock/Sand/Clay
Pasture/Hay
Transitional
Fallow
Deciduous Forest
Urban Grasses
Evergreen Forest
Wooded Wetlands
Mixed Forest
Herbaceous Wetlands
Poweii I
County '
Figure 2-18. Land use/land cover in the FTPA.
28
-------
Flathead River Headwaters TPA
Watershed Characterization
2.1.8 Soils
2.1.8.1 Soil Map Units
Soils data and geographic information system (GIS) coverages from the Natural Resources Conservation
Service (NRCS) were used to characterize soils in the FTPA. General soils data and map unit delineation
for the United States are provided as part of the State Soil Geographic (STATSGO) database. The
STATSGO data set was created to provide a general understanding of soils data to be used with large-
scale analyses; small, site-specific analyses with STATSGO data are not appropriate. GIS coverages
provide accurate locations for the soil map units at a scale of 1:250,000 (USDA, 1995). A map unit is
composed of several soil series having similar properties. Identification fields in the GIS coverages can
be linked to a database that provides information on chemical and physical soil characteristics. Figure 2-
19 shows the general map unit boundaries in the FTPA, and the following sections summarize relevant
physical soil data.
29
-------
Watershed Characterization
Flathead River Headwaters TPA
Lincoln
County
Flathead
County
Glacier
County
Major Streams
r"Tj Lakes
Counties
rn hucs
Pondera
County
SOIL MAP UNITS
BATA-COURVILLE-ROCK OUTCROP
BEESKOVE-REPP-FELAN
STEMPLE-GARLET-COWOOD
ฆ COWOOD-ROCK OUTCROP-RUBBLE LAND
| COWOOD-ROCK OUTCROP-GARLET
SCHNOORSON-R AMSDELL-GLACIERCREE K
GLACIERCREEK-YELLOWBAY-TYPIC UDIFLUVENTS
GLACIERS-ROCK OUTCROP-RUBBLE LAND
HOLLOWAY-EVARO-SHARROTT
HI HOLLOWAY-E VARO-MITTEN
| HOLLOWAY-PHILLCHER-ROCK OUTCROP
HOLLOWAY-PHILLCHER-ROCK OUTCROP
| LOBERG-GARLET-EVARO
LOBE RG-G ARLET-HELM VILLE
ROCK OUT CROP-CO EROCK-PHILLC HE R
ROCK OUTCROP-DRYADINE-RUBBLE LAND
ROCK OUTCROP-HOLLOWAY-COEROCK
ROCK OUTCROP-RUBBLE LAND-EVARO
RUM BLECREEK-COURVILLE-WINF ALL
STARLEY-G ARLET -ROCK OUTCROP
STARLE Y-ROCK OUTCROP-GARLET
WHITORE-TROP AL-ROCK OUTCROP
WALD BILLIG-C OUR VILLE-B ATA
WALDBILLIG-ROCK OUTCROP-P HILLCHER
Lake
County
Teton
County
Lewis and Clark
County
Figure 2-19. Major soil units in the FTPA.
30
-------
Flathead River Headwaters TPA
Watershed Characterization
2.1.8.2 Sediment Hazard Ranking
Erosion occurs infrequently on undisturbed forest soils in the FTPA because organic matter blankets the
soil surface, reducing the impacts of precipitation and allowing water to gradually infiltrate into
underlying soils. Below the organic layer, lower soil layers are high in organic matter, loose, porous, and
water moves quickly through and into the root zone of vegetation. However, when management activities
remove the protective organic layer over the soil or when surface soil layers are compacted, soil erosion
occurs. The FNF developed the Sediment Hazard Ranking in an effort to evaluate the potential risk
associated with delivery of eroded sediment from a given site to water associated with management
activities. The Sediment Hazard ranking is based on a given site's erosion hazard and sediment delivery
efficiency.
Erosion hazard ratings (slight, moderate, or severe) describe the relative susceptibility of exposed soil to
erosion and are based on direct observation of erosion and soil properties. Sediment delivery efficiency
(low, moderate, or high) rates the relative probability of eroded soil reaching a stream channel. The
properties of landforms are the basis for the sediment delivery efficiency rating and are determined by
observation and type of landform, slope, and distance between drainages.
A low ranking of sediment hazard indicates slight erosion hazard and low or moderate sediment delivery
efficiency. A slight erosion rating is assigned to soil layers with loamy textures and either 35 percent to
85 percent content of angular rock fragments or 60 percent to 85 percent content of rounded rock
fragments. Soils with parent geologic material of meta-sedimentary rocks have slight erosion hazard.
Mountain ridges, moraines, kames, terraces or landslide deposits, alluvial fans, cirque headwalls, cirque
basins, mid and upper portions of both mountain slopes and glaciated mountain slopes, and upper portions
of trough walls are rated as low sediment delivery efficiency. Slopes are 10 percent to greater than 60
percent, and most eroded soil is deposited before reaching a drainage channel. Less than 10 percent of
these landforms are close enough to drainage channels for eroded soil to enter a stream. A moderate
sediment delivery efficiency rating is given to mid and upper trough walls, mid and lower portions of
rolling and hilly glaciated mountain lobes, lower portions of mountain slope, and moraines. Slopes range
from 10 percent to 60 percent. Streams have dendritic or parallel drainage patterns and are widely spaced.
Approximately 10 percent to 40 percent of these landforms are close enough to a drainage channel for
eroded soil to enter the stream channel.
A moderate ranking of sediment hazard indicates moderate erosion hazard and low to moderate sediment
delivery efficiency or slight erosion hazard and high sediment delivery efficiency. Moderate erosion
hazard is assigned to soils with loamy texture and either 15 percent to 35 percent content angular rock
fragments or 15 percent to 60 percent content rounded rock fragments. Soil types formed in loess-
influenced volcanic ash or in glacial till have moderate erosion hazard ratings. High sediment delivery
efficiency is ranked for dissected mountain slopes, stream breaklands, stream bottoms, the lower portion
of steep, glaciated mountain slopes, or themed and lower portions of trough walls. The dissected
mountain slopes, stream breaklands, and lower portions of trough walls have slopes of 60 percent to 90
percent and eroded soil can travel a relatively long distance into drainage channels. The stream bottom
landform is parallel to large streams, and soil erosion is close enough to the water body to become a
sediment hazard. Approximately 10 percent to 100 percent of these landforms are close enough to a
drainage channel for eroded soil to become sediment.
31
-------
Watershed Characterization
Flathead River Headwaters TPA
A high ranking of sediment hazard indicates moderate erosion hazard and a high sediment delivery
efficiency OR a severe erosion hazard and a low, moderate, or high sediment delivery efficiency. Severe
erosion hazard is assigned to soils with sandy textures or a loamy or clayey texture and less than 15
percent rock fragments, angular or rounded. Soils formed in lacustrine deposits, in sandy glacial outwash,
or from material weathered out of granitic rocks have severe erosion hazard ratings.
Sediment hazard rankings are summarized in Table 2-8 and shown in Figure 2-20, Figure 2-21, and
Figure 2-22.
Table 2-8. Summary of Sediment Hazard
Watershed
Drainage Name
High Sediment
Hazard
Moderate
Sediment
Hazard
Low Sediment
Hazard
Red Meadow
Acres
9,589
1,674
7,640
%
51
9
40
Whale Creek
Acres
211,435
3,952
15,590
%
52
10
38
North Fork Flathead
South Fork Coal Creek
Acres
6,493
907
4,456
River
%
55
8
38
North Fork Coal Creek
Acres
8,142
363
6,441
%
55
2
43
Coal Creek Main Stem
Acres
13,230
3,989
8,496
%
52
16
33
Granite Creek
Acres
7,342
2,778
8,213
%
40
15
45
Middle Fork Flathead
Skyland Creek
Acres
1,833
743
2,753
River
%
34
14
52
Morrison Creek
Acres
13,355
7,019
11,936
%
41
22
37
South Fork Flathead
Sullivan Creek
Acres
27,980
2,170
16,502
River
%
60
5
35
32
-------
Flathead River Headwaters TPA
Watershed Characterization
Figure 2-20. Sediment hazard ratings for selected watersheds in the North Fork Flathead River
basin.
Figure 2-21. Sediment hazard ratings for selected watersheds in the Middle Fork Flathead River
basin.
33
-------
Watershed Characterization
Flathead River Headwaters TPA
Figure 2-22. Sediment hazard ratings for selected watersheds in the South Fork Flathead River
basin.
34
-------
Flathead River Headwaters TPA
Watershed Characterization
2.1.9 Forest Harvest History
Studies from throughout the United States have generally shown that forest harvesting on small
watersheds increases the amount of annual streamflow, or annual water yield. For a given watershed, the
amount of increase is generally proportional to the area of the watershed that is clear-cut. Thinnings and
partial cuts are generally ineffective at changing annual water yields (Beschta and Platts, 1986).
Typically the maximum water yield increase immediately follows harvest. Water yield increases will
decline over time as regenerating trees and other vegetation reoccupy the site. For altered streamflow
characteristics to return to pre-logging levels, more than 20 years might be required. Forest harvest
activities have also been shown to directly increase erosion.
It should be noted that the relationship between harvest and water quality impacts is complex. Increased
harvest intensity does not necessarily correlate with degraded water quality. Consideration of elevation,
aspect, stand age, and hydrologic response is necessary to fully understand the potential for water quality
impact associated with harvest. Nonetheless, there is sufficient information in the literature to indicate
that forest harvest might affect water quality.
Data regarding "clear-cut" harvest trends in the FTPA were evaluated between 1960 and September 2003.
Clear-cuts, as defined herein, include any areas in which FNF records exist for the following harvest
activities: clearcut with reserves, group selection cuts, seed tree final cuts, seed tree final cuts with
reserves, seed tree cuts, seed tree cuts with reserves, shelterwood final cuts, shelterwood final cuts with
reserves, shelterwood removal cuts, shelterwood seed cuts, shelterwood seed cuts with reserves, single
tree selection cuts, and stand clear-cut. Clear-cut harvests since 1960 are shown in Figure 2-23, Figure 2-
24, and Figure 2-25 and are grouped as "intensive harvests." Nonintensive harvests are also shown and
consist of liberation, sanitation, salvage, and thinning cuts. Harvested land is discussed in further detail
for each watershed in Section 3.0 as a supplemental indicator for determining sediment impairments.
35
-------
Watershed Characterization
Flathead River Headwaters TPA
LINCOLN
COUNTY
FLATHEAD
COUNTY
Non-Intensive Harvest
H 1960-1969
| 1970-1979
1980-1989
1990-1999
H 2000- 2003
Intesive Harvest
H 1960-1969
ฆ 1970-1979
1980- 1989
M 1990-1999
H 2000- 2003
2 0 2
O Cities
Lakes
A / Streams
^ Vy Counties
Glacier National Park
I I North Fork Flathead River Watershed
4 Miles
Figure 2-23. Harvest trends in selected watersheds in the North Fork Flathead River basin.
36
-------
Flathead River Headwaters TPA
Watershed Characterization
FLATHEAD
COUNTY
PONDERA
COUNTY
Non-Intensive Harvest
ฆ1 1960 - 1969
| 1970-1979
1980-1989
1990-1999
H 2000 - 2003
Intesive Harvest
H 1960-1969
| 1970-1979
1980-1989
H 1990-1999
H 2000 - 2003
O Cities
Lakes
/v Streams
Counties
Glacier National Park
I | Middle Fork Flathead River Watershed
3 Miles
Figure 2-24. Harvest trends in selected watersheds in the Middle Fork Flathead River basin.
37
-------
Watershed Characterization
Flathead River Headwaters TPA
FLATHEAD
COUNTY
lungry
LAKE
COUNTY
Non-Intensive Harvest
H 1960- 1969
| 1970-1979
1980-1989
1990-1999
H 2000 - 2003
Intesive Harvest
1 1960- 1969
| 1970- 1979
1980-1989
| 1990- 1999
I 2000 - 2003
O Cities
Lakes
/\/ Streams
Counties
] South Fork Flathead River Watershed
Figure 2-25. Harvest trends in selected watersheds in the South Fork Flathead River basin.
38
-------
Flathead River Headwaters TPA
Watershed Characterization
2.1.10 Fire History
Although forest fires are considered a natural phenomenon, they can result in soil erosion, soil nutrient
loss, stream channel effects, and water yield effects. A wildfire has the potential to affect the
characteristics of forest soils by reducing the soil aggregate stability, reducing permeability, increasing
runoff and erosion, and reducing organic matter/nutrient status. These combined effects can cause the
runoff following a storm event to increase significantly, increasing the overland flow available to initiate
soil erosion, as either sheet or rill erosion. The potential for erosion increases with slope and burn
severity. Burn severity is not considered directly in this analysis. Rather, burned areas are depicted in
Figure 2-26, Figure 2-27, and Figure 2-28 to show areas that have burned and therefore might have
functioned, or might be functioning, as natural sediment source areas. Fires are also discussed for each
watershed in Section 3.0 as a supplemental indicator for determining sediment impairments
39
-------
Watershed Characterization
Flathead River Headwaters TPA
CANAHA
limited states
cjTrailcreek
GLACIER
COUNTY
LINCOLN
COUNTY
Of^olebridge
FLATHEAD
COUNTY
DakefWlcDonald
West Glacier
Fire
History
1900-1919
1920-1939
HI
1940-1959
1960-1979
1980-1999
2000 - 2003
O Cities
Lakes
/\/ Streams
^'Counties
~ North Fork Flathead River Watershed
5 Miles
Figure 2-26. Fire history in the North Fork Flathead River watershed.
40
-------
Flathead River Headwaters TPA
Watershed Characterization
o Coram
FLATHEAD
COUNTY
o Kiowa
GLACIER
COUNTY
East Glacier Park
o
Summit
Fire History
H 1900" 1919
1920- 1939
H 1940- 1959
1960- 1979
1980- 1999
2000 - 2003
O Cities
^ Lakes
Streams
/AV/ Counties
~ Middle Fork Flathead River Watershed
PONDERA
COUNTY
Figure 2-27. Fire history in the Middle Fork Flathead River watershed.
41
-------
Watershed Characterization Flathead River Headwaters TPA
I
COUNTY I
Figure 2-28.
10 15 Miles
Fire history in the South Fork Flathead River watershed.
Swan Lake
O
LAKE
COUNTY
Salmon Prairieo
Fire History
ฆฆ 1900 - 1919
| 1920 - 1939
1940 - 1959
1960 - 1979
| 1980 - 1999
2000 - 2003
O Cities
Lakes
Streams
' Counties
/ v
MISSOULA
COUNTY
~ South Fork Flathead River Watershed
V
AND CLARK '
COUNTY
Hungry H
Columbia Fallso
Columbia Hei
OEssex
FLATHEAD
COUNTY
Ferndale
CondonO
42
-------
Flathead River Headwaters TPA
Watershed Characterization
2.1.11 Forest Roads
Improperly designed roads can directly affect aquatic ecosystems. Roads fundamentally disrupt natural
drainage patterns by diverting water and preventing water infiltration into soil. Roads can affect both the
volume of water available as surface runoff and the efficiency with which water flows through a
watershed. Roads can also contribute sediment to waterways from direct erosion on cut-and-fill slopes. In
addition, improperly designed roads can increase the magnitude and frequency of mass failures and
landslides. Adverse effects on natural hydrologic processes in roaded watersheds increase as road
densities increase. Table 2-9 provides a range of risk guidelines regarding road density (Johnson, 2003).
In general, road densities of less than 1.5 to 2.0 miles per square mile are thought to pose a low risk for
water quality impairment.
Table 2-9. Road Density Risk Ratings in Miles per Square Mile
Risk
Kootenai
National Forest''
Idaho
Panhandle
National Forest
Multi-Agency
Bull Trout
Screen
Columbia River Basin Final
EIS"
Low
< 1.5
< 1.7
< 1.5
< 2.0 (proper function)
Moderate
1.5-3.5
1.7-4.7
1.5-3.0
2.0-3.0 (functioning at risk)
High
> 3.5
>4.7
> 3.0
> 3.0 (non proper function)
aThe values reported for the Kootenai National Forest represent the range of values for areas with mean annual
precipitation of 20 to 40 inches (similar to the FTPA; see Section 2.1.1).
The Columbia River Basin Final Environmental Impact Statement (CRB FEIS) reports low, moderate, and high
in terms of proper functioning condition.
Road densities in the subject watersheds range between 0.12 to 1.69 miles per square mile (Table 2-10
and Figures 2-29 through 2-31). The highest road density in the FTPA is in Skyland Creek. All the road
densities within the FTPA fall within the "Low" to "Moderate" risk categories.
Table 2-10. Road Densities in Selected Watersheds Within the FTPA
Watershed
Current Roads (miles)
Number of
Historic Roads (miles)
Closed
Seasonal
Open
Yearlong
Other
Total
Road
Miles
Road-
Stream
Crossings
Watershed
Size (Sq
Mi )
Road
Density
(mi/mi )
Historical
(<1995)
De-
commissioned
(Since 1995)
North Fork
Red
Meadow
Creek
20.3
7.3
4.2
1.6
33.4
58
30.1
1.11
8.9
1.7
Coal Creek
38.7
12.8
20.7
24.1
96.3
132
82.1
1.20
29.0
Whale
Creek
22.3
17
4.2
43.5
58
64.1
0.68
12.8
19.6
Middle Fork
Granite
Creek
14.6
9.5
24.1
14
24.1
1.00
Morrison
Creek
6
0.1
6.1
4
50.5
0.12
Skyland
Creek
8.3
5.7
14.0
17
8.3
1.69
South Fork
Sullivan
Creek
58.7
11.1
69.8
85
72.9
0.96
11.8
Note: Road density reflects current road conditions. Decommissioned and historical roads are not included in the
road totals or road densities.
43
-------
Watershed Characterization
Flathead River Headwaters TPA
LINCOLN
COUNTY
Roads
A/ Closed Yearlong
A/ Decommission Since 1995
/V Historic Prior to 1995
A/ Open Seasonally
Open Yearlong
A/ Other Roads
Y Road-Stream Crossings
I Cities
Lakes
/\J Streams
j Counties
ฆ Glacier National Park
|~~| North Fork Flathead River Watershed
10 12 Miles
FLATHEAD
COUNTY
Figure 2-29. Roads and stream crossings in selected watersheds in the North Fork Flathead
River basin.
44
-------
Flathead River Headwaters TPA
Watershed Characterization
FLATHEAD
COUNTY
PONDERA
COUNTY
Roads
Closed Yearlong
Decommission Since 1995
A/ Historic Prior to 1995
Open Seasonally
/\y Open Yearlong
f\/Other Roads
Y Road-Stream Crossings
I Cities
| Lakes
A/ Streams
j Counties
| Glacier National Park
^ Middle Fork Flathead
River Watershed
Figure 2-30. Roads and stream crossings in selected watersheds in the Middle Fork Flathead
River basin.
45
-------
Watershed Characterization
Flathead River Headwaters TPA
FLATHEAD
COUNTY
Swan Lake
I LAKE
COUNTY
Roads
A/ Closed Yearlong
A/ Decommission Since 1995
A/ Historic Prior to 1995
A/ Open Seasonally
Ay Open Yearlong
A/ Other Roads
Y Road-Stream Crossings
Z Cities
H Lakes
/\/ Streams
j\ j Counties
| Glacier National Park
I I South Fork Flathead River Watershed
10 12 3 Miles
Figure 2-31. Roads and stream crossings in selected watersheds in the South Fork Flathead River
basin.
46
-------
Flathead River Headwaters TPA
Watershed Characterization
2.2 Biological Characteristics
2.2.1 Threatened and Endangered Species
The federally threatened, endangered, and U.S. Forest Service (USFS) sensitive species known to occur
within the FTPA are listed in Table 2-11.
Table 2-11. Federally Threatened, Endangered, and USFS Region 1 Sensitive Species in the FTPA
SPECIES PRESENCE15
North Fork
Middle Fork
South Fork
Species
Status''
Historic
Current
Historic
Current
Historic
Current
Bald Eagle
T
Y
Y
P
Y
Y
Y
Grizzly Bear
T
Y
Y
Y
Y
Y
Y
Gray Wolf
E
Y
Y
Y
Y
Y
Y
Canada Lynx
T
Y
Y
Y
Y
Y
Y
Bull Trout
T
Y
Y
Y
Y
Y
Y
Westslope Cutthroat
Trout
S
Y
Y
Y
Y
Y
Y
Peregrine Falcon
S
P
UNK
P
UNK
Y
UNK
Flammulated Owl
s
Y
P
UNL
UNL
P
UNK
Harlequin Duck
s
Y
Y
Y
Y
Y
Y
Common Loon
s
Y
Y
Y
Y
Y
Y
Townsend's Big-eared
Bat
s
P
P
P
P
P
P
Black-backed
Woodpecker
s
Y
Y
P
P
P
P
Wolverine
s
Y
Y
Y
Y
Y
Y
Fisher
s
Y
Y
Y
P
Y
Y
Northern Goshawk
s
Y
Y
Y
Y
Y
Y
Northern Leopard
Frog
s
UNK
UNK
UNL
UNL
UNL
UNL
Boreal Toad
s
Y
Y
Y
Y
Y
Y
Northern Bog
Lemming
s
UNK
UNK
UNL
UNL
UNL
UNL
aT = Federally Threatened; E = Federally Endangered; S = Forest Service Region 1 listed as sensitive;
bY = yes; N = no; P = probable occurrence based on presence of known habitat requirements; UNL = unlikely based
on absence of known habitat requirements; UNK = unknown.
47
-------
Watershed Characterization
Flathead River Headwaters TPA
2.2.2 Fisheries
According to the 1996 and 2002 303(d) lists, the primary impaired beneficial uses are cold-water fishery
support and aquatic life. Consequently, it is important to understand the current status of these beneficial
uses.
Westslope cutthroat trout, bull trout, and mountain whitefish are the native game species found in the
South, Middle, and North forks of the Flathead River and their tributaries (Deleray et al., 1999). Because
bull trout were directly considered when MDEQ made water quality impairment determinations to
support the 1996 and 2002 303(d) lists, and are also considered herein (Section 3.3.2.4) relative to TMDL
supplemental indicators, bull trout are considered a primary indicator species for the support of the cold-
water fishery beneficial use. Therefore, the remainder of this section is devoted to a summary of the
available data regarding bull trout.
A number of waters in the FTPA have been designated "core" bull trout streams by Montana Fish,
Wildlife, and Parks (MFWP) and "priority watershed" under INFISH (USDA Forest Service, 1995).
Many of these streams were also listed as impaired on the 1996 and 2002 303(d) lists (Table 2-12).
Bull trout in the North and Middle forks of the Flathead watershed are considered one meta-population
because Flathead Lake plays a major part in their life cycle. Most of the bull trout in this population
spawn in headwater tributaries in the North and Middle forks. Juveniles rear in the tributaries for 1 to 3
years and then migrate to the Flathead River, and ultimately to Flathead Lake, to mature. As adults, they
once again return to the tributaries for spawning. It is therefore impossible to consider trends in this bull
trout population without considering the importance of the interconnected lake, river, and tributary
system.
Flathead Lake has gone through a major change over the past two decades. Between 1965 and 1975
MFWP stocked mysis shrimp into three lakes with tributaries into Flathead Lake. By 1981, mysis had
migrated into Flathead Lake. The mysis population peaked in 1986, and by 1987 only 330 kokanee
salmon (major bull trout prey species) were found in McDonald Creek at the southwestern boundary of
Glacier National Park. Kokanee salmon populations peaked from 26,000 to 11,800 between 1979 and
1985. No kokanee have been found on traditional spawning locations during recent surveys.
Lake trout and lake whitefish populations expanded as juveniles benefited from the mysis shrimp. The
expansion of these species has resulted in a decline in bull trout. The mechanisms for the decline are not
well understood. Because only a few bull trout have shown up in lake trout stomachs, competition among
species and direct predation appear to be the most likely causes (USFS, Biological Assessment, 1998).
Since roughly 1980, MFWP has been monitoring the number of bull trout spawning sites (redds) in
representative tributaries in the North and Middle Forks to estimate trends in escapement of adults from
Flathead Lake into the upper watershed tributaries. A significant decline in redd numbers in all tributaries
occurred during the 1990s. This widespread decline is thought to be a result of alteration in the trophic
dynamics in Flathead Lake. However, bull trout eggs and juveniles were also subject to degraded habitat
conditions in spawning tributaries. From 1992 to 1997, the number of bull trout redds remained relatively
stable, but this level was considerably lower than that in the preceding 12-year period (70 percent below
the average for the previous period). The 1998 through 2002 redd counts showed an increase over the
previous 6 years, but they were still on average 45 percent below the pre-mysis levels. Although all
tributaries in the watershed showed a decline in redd numbers in the early 1990s, individual streams have
since responded with varied spawner abundances. For example, redd numbers in Coal Creek have
continued to decline, hitting all-time lows of zero spawners in index reaches in some years. In the
adjacent drainage, however, redd numbers in Big Creek have returned to the pre-mysis levels of the
1980's. This difference suggests that habitat conditions within individual drainages might be affecting
bull trout survival.
48
-------
Flathead River Headwaters TPA
Watershed Characterization
Bull trout in the South Fork above Hungry Horse Dam have been isolated from the rest of the Flathead
Lake system since the dam was constructed in 1953. This population, therefore, is unaffected by
conditions in Flathead Lake. In contrast to the North and Middle Fork population, this population has
been stable or increasing following closure of bull trout angling, although bull trout redd counts have
been conducted only in the South Fork for the past 10 years.
Bull trout and westslope cutthroat trout populations for individual streams are discussed in further detail
in Section 3.0.
Table 2-12. Comparison of 303(d)-Listed Streams With Core and Priority Bull Trout Watersheds
Tributary Name
303(d) Listed
Core/Priority
Basin Creek
X
Bear Creek
X
Big Creek
X
X
Bowl Creek
X
Charlie Creek
X
Clack Creek
X
Coal Creek
X
X
Dolly Varden Creek
X
Granite Creek
X
Lodgepole Creek
Wilderness tributary to Morrison
above Middle Fork
X
Long Creek
X
Morrison Creek
X
X
Red Meadow Creek
X
X
Skyland Creek
X
Shafer Creek
X
Strawberry Creek
X
Sullivan Creek
X
Trail Creek (MF)
X
Trail Creek (NF)
X
Whale Creek
X
X
2.3 Cultural Characteristics
2.3.1 Population
The FTPA is an integral part of the public lands surrounding the Flathead Valley. The recreational
opportunities on the public lands have made Flathead County one of the fastest growing counties in
Montana. Hunting, hiking, swimming, boating, bird and animal watching, and skiing are just a few of the
recreational activities afforded by public lands. However, the full-time residential population of the FTPA
is very low. Based on 2000 Census Block data obtained from the Montana State Library (2001), the 2000
population of the FTPA was 2,278.
49
-------
Watershed Characterization
Flathead River Headwaters TPA
2.3.2 Land Ownership
The FTPA is largely under federal ownership, mainly the US Forest Service and the National Park
Service. A summary of ownership by watershed is provided in Table 2-13 and Figure 2-32. Much of the
South Fork Flathead River watershed is under the Wilderness Area designation (Bob Marshall and Great
Bear wilderness areas).
Table 2-13. Land Ownership and Management by Drainage
Ownership
North Fork
Middle Fork
South Fork
National Park Service
46
48
0
US Forest Service
48
52
100
Montana Department of Natural
Resources and Conservation
3
0
0
Private
3
1
0
50
-------
Flathead River Headwaters TPA
Watershed Characterization
] Watershed Boundary
/ x J ' Counties
5 Lakes
Major Streams
Wilderness Area
Bob Marshall
Great Bear
Land Ownership
National Park Service
US Forest Service
State Land
Private Land
ฆ Water
Flathead
County
County
10 0 10 20 Miles
Lincoln
County
s.
_CANADA
UNITED STATES
Glacier
County
Lewis and Clark
County
Lake
County
Teton
K County
>
Pondera
County
Figure 2-32. Land Ownership in the Flathead River Headwaters TPA.
51
-------
-------
Flathead River Headwaters TPA
Water Quality Impairment Status
3.0 WATER QUALITY IMPAIRMENT STATUS
This section first presents the status of all 303(d)-listed water bodies in the TPA (i.e., which water bodies
are listed as impaired or threatened and for which pollutant). This information is followed by a summary
of the applicable water quality standards and a translation of those standards into proposed water quality
goals or targets. The remainder of the section is devoted to a water body-by-water body review of
available water quality data and an updated water quality impairment status determination for each listed
water body.
3.1 303(d) List Status
A summary of the 303(d) list status and history of listings is provided in Tables 3-1 and 3-2. As
mentioned in Section 1.1, all necessary TMDLs must be completed for all pollutant water body
combinations appearing on Montana's 1996 303(d) list. The 1996 303(d) list reported that Red Meadow
Creek, Whale Creek, Big Creek, Coal Creek, South Fork Coal Creek, North Fork Coal Creek, Granite
Creek, Skyland Creek, Challenge Creek, Morrison Creek, South Fork Flathead River, Sullivan Creek, and
Hungry Horse Reservoir were impaired (Figure 3-1) (MDEQ, 1996). Listed causes of impairment for
these water bodies included habitat alteration, flow alteration, bank erosion, nutrients, siltation, and
suspended solids (Table 3-2). The most common impaired beneficial uses were cold-water fishery and
aquatic life.
Habitat alteration, flow alteration, and bank erosion are considered "pollution," while siltation and
suspended solids are considered "pollutants." It is EPA's position that TMDLs are required only for
"pollutants" that are causing or contributing to water body impairments (Dodson, 2001). Therefore,
because TMDLs are required only for pollutants and flow alteration, habitat alteration, and bank erosion
are not pollutants, the focus of this document is on the sediment-related pollutants (siltation and
suspended solids) and nutrients. Flow alteration, habitat alteration, and bank erosion might certainly
constitute potential sources or causes of sediment related impairments, and while no TMDLs are
established to specifically address these issues, they will be addressed as sources, as appropriate.
53
-------
Water Quality Impairment Status
Flathead River Headwaters TPA
Table 3-1. Impaired Streams Within the Flathead River Headwaters TPA on the 1996 and 2002
Montana 303(d) Lists
Watershed
Sub-Drainage and
Water body No.
Use
Class
Year
Listed
Cold-Water
Fishery
Aquatic Life
Recreation
(Swimmable)
Industry
Agriculture
Drinking
Water
North Fork
Flathead
River
Big Creek
MT76Q002-050
B1
1996
P
P
X
X
X
X
2002
TMDL Completed
Red Meadow Creek
MT76Q002-020
B1
1996
P
P
X
X
X
X
2002
P
P
F
F
F
X
Whale Creek
MT76Q002-030
B1
1996
T
X
X
X
X
X
2002
P
P
F
F
F
X
South Fork Coal Creek
MT76Q002-040
B1
1996
P
P
X
X
X
X
2002
P
P
F
F
F
X
Coal Creek
MT76Q002-080
B1
1996
P
P
X
X
X
X
2002
P
P
F
F
F
X
North Fork Coal Creek
MT76Q002-070
B1
1996
P
P
X
X
X
X
2002
P
P
F
F
F
X
Middle Fork
Flathead
River
Granite Creek
MT76I002-010
B1
1996
X
P
X
X
X
X
2002
P
P
F
F
F
X
Skyland Creek
MT76I002-020
B1
1996
P
P
X
X
X
X
2002
X
X
X
F
F
X
Challenge Creek
MT76I002-040
B1
1996
p
p
X
X
X
X
2002
Fully Supporting
Morrison Creek
MT76I002-050
B1
1996
P
p
X
X
X
X
2002
P
p
F
F
F
X
South Fork
Flathead
River
South Fork
Flathead River
MT76J001-010
B1
1996
P
p
X
X
X
X
2002
X
X
p
F
F
X
Sullivan Creek
MT76J003-010
B1
1996
P
p
X
X
X
X
2002
X
X
F
F
F
X
Hungry Horse Reservoir
MT76J002-1
B1
1996
P
p
F
F
F
F
2002
Fully Supporting
Impairment Status Definitions for Table 3-1:
P = Partial support of Beneficial Use.
F = Full support of Beneficial Use.
T = Threatened support for Beneficial Use.
X = Sufficient Credible Data not available.
54
-------
Flathead River Headwaters TPA
Water Quality Impairment Status
Table 3-2. Causes of Impairment in the Flathead River Headwaters TPA
Watershed
Sub-Drainage and
Water body No.
Use
Class
Year
Listed
Probable
Causes
North Fork
Flathead River
Big Creek
MT76LJ003-050
B1
1996
Habitat alter/siltation
2002
TMDL completed
Red Meadow Creek
MT76Q002-020
B1
1996
Habitat alter/siltation
2002
Habitat alter/siltation
Whale Creek
MT76Q002-030
B1
1996
Habitat alter/siltation
2002
Habitat alter/siltation
South Fork Coal Creek
MT76Q002-040
B1
1996
Habitat alter/siltation
2002
Habitat alter/siltation
Coal Creek
MT76Q002-080
B1
1996
Siltation
2002
Siltation
North Fork Coal Creek
MT76Q002-070
B1
1996
Nutrients/siltation
2002
Siltation
Middle Fork
Flathead River
Granite Creek
MT76I002-010
B1
1996
Habitat alter/ siltation/suspended
solids
2002
Siltation/bank erosion
Skyland Creek
MT76I002-020
B1
1996
Habitat alter/ siltation/suspended
solids
2002
No SCD
Morrison Creek
MT76I002-050
B1
1996
Habitat alter/siltation
2002
Habitat alter/siltation
Challenge Creek
MT76I002-040
B1
1996
Habitat alter/siltation
2002
Not Listed
South Fork
Flathead River
Below HHD
South Fork
Flathead River
MT76J001-010
B1
1996
Habitat alterations
Flow alterations
2002
Flow alterations
Sullivan Creek
MT76J003-010
B1
1996
Habitat alterations
2002
No SCD
Hungry Horse Reservoir
MT76J002-1
B1
1996
Flow alterations
siltation
suspended solids
2002
Not listed
Note: Alter= alternation (s): SCD= sufficient credible data.
55
-------
Water Quality Impairment Status
Flathead River Headwaters TPA
Big Creek.
Lincoln
County
Whale Creelci^
Xy
Red Meadow C,reซk7
North Fork Coal ฃree
South(Fork Coal Creek^f
.CANADA _
, united states"
Glacier
County
Flathead
County
South Fork Flathead Rive
Hungry Horse
Reservoir
j^Skyland Creek
^/Challenge Creek pondera
\ f^PranAe Creek County
ro^wiorrison Creek
Coal Creek;
Lake
County
County
Powell
County
Sullivan Creek
Teton
County
/\J 303(d) Listed Streams
/ * s / Counties
Major Streams
Lakes
Watersheds
North Fork
Middle Fork
South Fork
j Missoula
i County
! Lewis and Clark
Figure 3-1. Location of the 303(d) listed streams.
56
-------
Flathead River Headwaters TPA
Water Quality Impairment Status
3.2 Applicable Water Quality Standards
Water quality standards include the uses designated for a water body, the legally enforceable standards
that ensure that the uses are supported, and a nondegradation policy that protects the high quality of a
water body. The ultimate goal of this water quality assessment, once implemented, is to ensure that all
designated beneficial uses are fully supported and all standards are met. Water quality standards form the
basis for the targets described in Section 3.3. The pollutants addressed in this water quality assessment
are sediment and nutrients. This section provides a summary of the applicable water quality standards for
each of these pollutants.
3.2.1 Classification and Beneficial Uses
Classification is the assignment (designation) of a single use or group of uses to a water body based on
the potential of the water body to support those uses. Designated uses or beneficial uses are simple
narrative descriptions of water quality expectations or water quality goals. There are a variety of "uses"
of state waters, including growth and propagation of fish and associated aquatic life, drinking water,
agriculture, industrial supply, and recreation and wildlife. The Montana Water Quality Act (WQA)
directs the Board of Environmental Review (BER) to establish a classification system for all waters of the
state that includes their present (when the act was originally written) and future beneficial uses
(Administrative Rules of Montana (ARM) 17.30.607-616), and to adopt standards to protect those uses
(ARM 17.30.620-670).
Montana, unlike many other states, uses a watershed-based classification system with some specific
exceptions. As a result, all waters of the state are classified and have designated uses and supporting
standards. All classifications have multiple uses, and in only one case (A-Closed) is a specific use
(drinking water) given preference over the other designated uses. Some waters might not actually be used
for a specific designated use (e.g., as a public drinking water supply); however, the quality of that water
body must be maintained for that designated use. When natural conditions limit or preclude a designated
use, permitted point source discharges or nonpoint source discharges may not make the natural conditions
worse.
Modification of classifications or standards that would lower a water's classification or standards (e.g., a
change from B-l to B-3) or removal of a designated use because of natural conditions may occur only if
the water was originally misclassified. All such modifications must be approved by the BER and are
undertaken through a Use Attainability Analysis (UAA) that must meet EPA requirements (40 CFR
131.10(g), (h), and (j)). The UAA and findings presented to the BER during rulemaking must prove that
the modification is correct and all existing uses are supported. An existing use may not be removed or
made less stringent.
Descriptions of Montana's surface water classifications and designated beneficial uses are presented in
Table 3-3. All water bodies in the Flathead River Headwaters TPA are classified as B-l, except for the
main stems of the North and Middle Forks of the Flathead River, which are classified as A-l.
57
-------
Water Quality Impairment Status
Flathead River Headwaters TPA
Table 3-3. Montana Surface Water Classifications and Designated Beneficial Uses
Classification
Designated Uses
A-CLOSED
Waters classified A-Closed are to be maintained suitable for drinking, culinary and
food processing purposes after simple disinfection.
A-1
Waters classified A-1 are to be maintained suitable for drinking, culinary and
food processing purposes after conventional treatment for removal of
naturally present impurities.
B-1
Waters classified B-1 are to be maintained suitable for drinking, culinary and
food processing purposes after conventional treatment; bathing, swimming
and recreation; growth and propagation of salmonid fishes and associated
aquatic life, waterfowl and furbearers; and agricultural and industrial water
supply.
B-2
Waters classified B-2 are to be maintained suitable for drinking, culinary and food
processing purposes after conventional treatment; bathing, swimming and
recreation; growth and marginal propagation of salmonid fishes and associated
aquatic life, waterfowl and furbearers; and agricultural and industrial water supply.
B-3
Waters classified B-3 are to be maintained suitable for drinking, culinary and food
processing purposes after conventional treatment; bathing, swimming and
recreation; growth and propagation of non-salmonid fishes and associated aquatic
life, waterfowl and furbearers; and agricultural and industrial water supply.
C-1
Waters classified C-1 are to be maintained suitable for bathing, swimming and
recreation; growth and propagation of salmonid fishes and associated aquatic life,
waterfowl and furbearers; and agricultural and industrial water supply.
C-2
Waters classified C-2 are to be maintained suitable for bathing, swimming and
recreation; growth and marginal propagation of salmonid fishes and associated
aquatic life, waterfowl and furbearers; and agricultural and industrial water supply.
C-3
Waters classified C-3 are to be maintained suitable for bathing, swimming and
recreation; growth and propagation of non-salmonid fishes and associated aquatic
life, waterfowl and furbearers. The quality of these waters is naturally marginal for
drinking, culinary and food processing purposes, agriculture and industrial water
supply.
I
The goal of the State of Montana is to have these waters fully support the following
uses: drinking, culinary and food processing purposes after conventional
treatment; bathing, swimming and recreation; growth and propagation of fishes
and associated aquatic life, waterfowl and furbearers; and agricultural and
industrial water supply.
58
-------
Flathead River Headwaters TPA
Water Quality Impairment Status
3.2.2 Standards
Montana's water quality standards include numeric and narrative criteria, as well as a nondegradation
policy that currently applies to the numeric criteria.
Numeric surface water quality standards have been developed for many parameters to protect human
health and aquatic life. These standards are in Department Circular WQB-7 (MDEQ, 2004). The numeric
human health standards have been developed for parameters determined to be toxic, carcinogenic, or
harmful and have been established at levels to be protective of long-term (i.e., lifelong) exposures as well
as exposure through direct contact such as swimming.
The numeric aquatic life standards include chronic and acute values that are based on extensive laboratory
studies including a wide variety of potentially affected species, a variety of life stages, and various
durations of exposure. Chronic aquatic life standards are protective of long-term exposure to a parameter.
The protection afforded by the chronic standards includes reproduction, early life stage survival, and
growth rates. In most cases the chronic standard is more stringent than the corresponding acute standard.
Acute aquatic life standards are protective of short-term exposures to a parameter and are not to be
exceeded.
High-quality waters are afforded an additional level of protection by the nondegradation rules (ARM
17.30.701 et. seq.,) and in statute 75-5-303 MCA. Changes in water quality must be "non-significant" or
an authorization to degrade must be granted by MDEQ. Under no circumstance, however, may standards
be exceeded. It is important to note that waters that meet or are of better quality than a standard are high-
quality for that parameter, and nondegradation policies apply to new or increased discharges to the water
body.
Narrative standards have been developed for substances or conditions for which sufficient information
does not exist to develop specific numeric standards. The term narrative standards commonly refers to
the General Prohibitions in ARM 17.30.637 and other descriptive portions of the surface water quality
standards. The General Prohibitions are also called the "free from" standards; that is, the surface waters
of the state must be free from substances attributable to discharges that impair the beneficial uses of a
water body. Uses can be impaired by toxic or harmful conditions (from one parameter or a combination
of parameters) or conditions that produce undesirable aquatic life. Undesirable aquatic life includes
bacteria, fungi, and algae.
The standards applicable to the pollutants addressed in the Flathead River Headwaters TPA are
summarized below.
3.2.2.1 Sediment
Sediment (coarse and fine bed sediment), siltation, and suspended solids are addressed through the
narrative criteria identified in Table 3-4. The relevant narrative criteria do not allow for harmful or other
undesirable conditions related to increases above naturally occurring levels or from discharges to state
surface waters. This is interpreted to mean that water quality goals should strive toward a reference
condition that reflects a water body's greatest potential for water quality given current and historical land
use activities where all reasonable land, soil, and water conservation practices have been applied. (See
definitions in Table 3-4.)
59
-------
Water Quality Impairment Status
Flathead River Headwaters TPA
Table 3-4. Applicable Rules for Sediment-Related Pollutants
Rule(s)
Standard
17.30.623(2)
No person may violate the following specific water quality standards for waters classified
B-1.
17.30.623(2)(f)
No increases are allowed above naturally occurring concentrations of sediment or
suspended sediment (except as permitted in 75-5-318, MCA), settleable solids, oils, or
floating solids, which will or are likely to create a nuisance or render the waters harmful,
detrimental, or injurious to public health, recreation, safety, welfare, livestock, wild animals,
birds, fish, or other wildlife.
17.30.637(1)
State surface waters must be free from substances attributable to municipal, industrial,
agricultural practices or other discharges that will:
17.30.637(1 )(a)
Settle to form objectionable sludge deposits or emulsions beneath the surface of the water
or upon adjoining shorelines.
17.30.637(1 )(d)
Create concentrations or combinations of materials that are toxic or harmful to human,
animal, plant, or aquatic life.
The maximum allowable increase above naturally occurring turbidity is: 0 NTU for A-
closed; 5 NTU for A-1, B-1, and C-1; 10 NTU for B-2, C-2, and C-3
17.30.602(17)
"Naturally occurring" means conditions or material present from runoff or percolation over
which man has no control or from developed land where all reasonable land, soil, and
water conservation practices have been applied.
17.30.602(21)
"Reasonable land, soil, and water conservation practices" means methods, measures, or
practices that protect present and reasonably anticipated beneficial uses. These practices
include but are not limited to structural and nonstructural controls and operation and
maintenance procedures. Appropriate practices may be applied before, during, or after
pollution-producing activities.
3.2.2.2 Nutrients
The term nutrients generally refers to the various forms of nitrogen and phosphorus found in a water
body. Both nitrogen and phosphorus are necessary for aquatic life, and both elements are needed at some
level in a water body to sustain life. The natural amount of nutrients in a water body varies depending on
the type of system. A pristine mountain spring might have little to almost no nutrients, whereas a lowland,
mature stream flowing through wetland areas might have naturally high nutrient concentrations. Most
waters of Montana are protected from excessive nutrient concentrations by narrative standards. The
exception is the Clark Fork River above the confluence with the Flathead River, where numeric water
quality standards for total nitrogen (300 j_tg/L) and total phosphorus (20 (ig/L upstream of the confluence
with the Blackfoot River and 39 jug/L downstream of the confluence) as well as algal biomass measured
as chlorophyll a (summer mean and maximum of 100 and 150 mg/m2, respectively) have been
established.
The narrative standards applicable to nutrients elsewhere in Montana are contained in the General
Prohibitions of the surface water quality standards (ARM 17.30.637 et seq.). The prohibition against the
creation of "conditions which produce undesirable aquatic life" is generally the most relevant to nutrients.
Nutrients generally do not pose a direct threat to the beneficial uses of a water body. However, excess
nutrients can cause an undesirable abundance of plant and algae growth. This process is called
eutrophication or organic enrichment, and it can have many effects on a stream or lake. One possible
effect is low dissolved oxygen concentrations. Aquatic organisms require oxygen to live, and they can
experience mortality and lowered reproduction rates with lowered dissolved oxygen concentrations.
Montana has numeric criteria for dissolved oxygen concentrations, and they are discussed in Montana
Water Quality Standards Circular WQB-7. The dissolved oxygen criteria are summarized in Table 3-5.
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Table 3-5. Numeric Dissolved Oxygen Criteria.
Time Period
Early Life Stages'' (mg/L)
Other Life Stages (mg/L)
30-Day Mean
NA
6.5
7-Day Mean
9.5 (6.5)
NA
7-Day Mean (min)
NA
5.0
1 Day Min
8.0 (5.0)
4.0
a These are water column concentrations recommended to achieve the required inter-gravel dissolved oxygen
concentrations shown in parentheses. For species that have early life stages exposed directly to the water column,
the figures in parentheses apply.
Source: MDEQ, 2004.
3.3 Water Quality Goals and Indicators
To develop a TMDL, it is necessary to establish quantitative water quality goals referred to in this
document as targets. TMDL targets must represent the applicable numeric or narrative water quality
standards and full support of all associated beneficial uses. For many pollutants with established numeric
water quality standards, the water quality standard is used directly as the TMDL target. However, none of
the pollutants of concern in the FTPA (i.e., siltation and nutrients) have established numeric water quality
standards that can be directly applied as TMDL targets. Where targets are established for pollutants with
only narrative standards, the target must be a water body-specific, measurable interpretation of the
narrative standard.
In the case of the FTPA, there is no single parameter that can be applied alone to provide a direct measure
of beneficial use impairment associated with sediment or nutrients. As a result, a suite of targets and
supplemental indicators has been selected to help determine when impairments are present (Tables 3-6
and 3-7). In consideration of the available data for the FTPA, the targets are the most reliable and robust
measures of impairment and beneficial use support available. As described in the one-by-one discussions
of individual targets presented in the following paragraphs, there is a documented relationship between
the selected target values and beneficial use support, or sufficient reference data are available to establish
a threshold value representing "natural" conditions. In addition to having a documented relationship with
the suspected impaired beneficial use, the targets have direct relevance to the pollutant of concern. The
targets, therefore, are relied on as threshold values that if exceeded (based on sufficient data), indicate
water quality impairment. The targets are also applied as water quality goals by which the ultimate
success of implementation of this plan will be measured in the future.
The supplemental indicators provide supporting and/or collaborative information when used in
combination with the targets. In addition, some of the supplemental indicators are necessary to determine
whether exceedances of targets are a result of natural versus anthropogenic causes. However, the
proposed supplemental indicators are not sufficiently reliable to be used alone as a measure of impairment
because (1) the cause-effect relationship between the supplemental indicator(s) and beneficial use
impairments is weak or uncertain; (2) the supplemental indicator(s) cannot be used to isolate impairment
associated with individual pollutants (e.g., to differentiate between an impairment caused by excessive
levels of sediment and an impairment caused by high concentrations of metals); or (3) there is too much
uncertainty associated with the supplemental indicator(s) to have a high level of confidence in the result.
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Table 3-6. Summary of the Proposed Sediment Targets and Supplemental Indicators for the
Flathead TPA
Targets
Threshold
5-year Mean McNeil Core Percentage of Subsurface Fines <
6.35 mm
35%
5-year Mean Substrate Score
> 10
Percentage of Surface Fines < 2 mm
< 20%
Clinger Richness
> 14
Supplemental Indicators
Recommended Value
Juvenile Bull Trout and Westslope Cutthroat Trout Density
Documented increasing or stable trend
Bull Trout Redd Counts
Documented increasing or stable trend
Suspended Sediment Concentration Mean
Suspended Sediment Concentration Mean Annual Maximum
Suspended Sediment Concentration Maximum
3.2 ฑ5.2 mg/L
14.6 mg/L
61.6 mg/L
Turbidity
High flow-50 NTU instantaneous maximum
Summer base flow - 10 NTU instantaneous
maximum
Pfankuch Mass Wasting Score
"good"
Pfankuch Bank Vegetation Score
"good"
Pfankuch Cutting Score
"good"
Pfankuch Deposition Score
"good"
Montana Mountain Macroinvertebrate Index of Biological
Integrity
> 75%
Percentage of Clinger Taxa
"High"
EPT Richness
>22
Periphyton Siltation Index
<20
Fire
Evaluated on a case-by-case basis
Equivalent Clear-Cut Acres
< 25%
Water Yield
< 10%
Roads
Evaluated on a case-by-case basis
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Table 3-7. Summary of the Proposed Nutrient Targets and Supplemental Indicators for the
Flathead TPA
Targets
Threshold
Benthic Chlorophyll-a (Median)
< 33 mg/m2
EPA Ecoregion II, Total Phosphorus (Median)
<0.01 mg/L
EPA Ecoregion II, TKN (Median)
< 0.05 mg/L
EPA Ecoregion II, Nitrate+Nitrite (NO2/NO3) (Median)
< 0.014 mg/L
EPA Ecoregion II, Total Nitrogen (Median)
<0.12 mg/L
Supplemental Indicators
Recommended Value
Macroinvertebrate Hilsenhoff Biotic Index (HBI)
< 3.5
Montana Mountain Macroinvertebrate Index of Biological Integrity
> 75%
Dissolved Oxygen, 7-Day Mean
>9.5 mg/L
Dissolved Oxygen, 1-Day Minimum
> 8.0 mg/L
EPA Ecoregion II, Chlorophyll-a, Water Column (Median)
< 1.08 |jg/L
Fire
Evaluated on a case-by-case basis
Equivalent Clear-Cut Acres
< 25%
Water Yield
< 10%
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Targets and Supplemental Indicators Applied to Beneficial Use Impairment
Determinations
The beneficial use impairment determinations presented in Section 3.4 are based a weight-of-evidence
approach in combination with the application of best professional judgment. The weight-of-evidence
approach outlined in Figure 3-2, is applied as follows. If none of the target values are exceeded, the water
is considered to be fully supporting its beneficial uses and a TMDL is not required. This is true even if
one or more of the supplemental indicator values are exceeded. On the other hand, if one or more of the
target values are exceeded, the circumstances around the exceedance are investigated and the
supplemental indicators are used to provide additional information to support a determination of
impairment/non-impairment. In this case, the circumstances around the exceedance of a target value are
investigated and it is not automatically assumed that the exceedance represents anthropogenic impairment
(e.g., Are the data reliable and representative of the entire reach? Might the exceedance be a result of
natural causes such as floods, drought, fire, or the physical character of the watershed?). This is also the
case where the supplemental indicators assist by providing collaborative and supplemental information,
and the weight-of-evidence of the complete suite of targets and supplemental indicators is used to make
the impairment determination. A conservative approach is used if the supplemental indicators are
inconclusive. When the supplemental indicators support neither impairment nor non-impairment, it is
assumed that the water is impaired.
Figure 3-2. Weight-of-evidence approach for determining beneficial use impairments.
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Targets and Supplemental Indicators as Water Quality Goals
In accordance with the Montana Water Quality Act (MCA 75-5-703(7) and (9)), the MDEQ is required to
assess the waters for which TMDLs have been completed to determine whether compliance with water
quality standards has been attained. This assessment will use the suite of targets specified in Tables 3-6
and 3-7 to measure compliance with water quality standards and achievement of full support of all
applicable beneficial uses (Figure 3-3). The supplemental indicators will not be used directly as water
quality goals to measure the success of this water quality restoration plan. If all of the target threshold
values are met, it will be assumed that beneficial uses are fully supported and water quality standards
have been achieved. Alternatively, if one or more of the target threshold values are exceeded, it will be
assumed that beneficial uses are not fully supported and water quality standards have not been achieved.
However, it will not be automatically assumed that implementation of a TMDL was unsuccessful just
because one or more of the target threshold values have been exceeded. As noted above, the
circumstances around the exceedance will be investigated. For example, might the exceedance be a result
of natural causes such as floods, drought, fire, or the physical character of the watershed? In addition, in
accordance with MCA 75-5-703(9), an evaluation will be conducted to determine whether:
the implementation of a new or improved suite of control measures is necessary
more time is needed to achieve water quality standards, or
revisions to components of the TMDL are necessary.
Detailed discussions regarding each of the targets and supplemental indicators are presented below.
All targets are met
One or more of the targets are
exceeded
t
Evaluate Circumstances
Around Exceedance
Have "BMPs" Been
Implemented and
are they workinn?
Been Is More Time
and Needed to Achieve
inn? WQS?
Based on new
data/circumstances,
are revisions to the
TMDL necessary?
.~
~
DECISION: Do the Circumstances
Suggest Impairment or Are the
Exceedances Sufficiently Explained?
Not Impaired
Impaired
Figure 3-3. Methodology for determining compliance with water quality standards.
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3.3.1 Sediment Targets
The proposed sediment targets include McNeil core substrate fines, substrate scores, pebble counts
(percent surface fines), and macroinvertebrate metrics.
3.3.1.1 McNeil Core - Percent Subsurface Substrate Fines < 6.35 mm
McNeil core Sampling involves the use of a standard 15.2-centimeter hollow core sampler to collect
subsurface sediments in stream bottom substrates (Deleray et al., 1999). Measurements of the size range
of subsurface substrate material in the streambed are indicative of salmonid spawning and incubation
habitat quality. Substrate fine materials smaller than 6.35 millimeters are commonly used to describe
spawning gravel quality, and they include the size range typically generated by land management
activities (Weaver and Fraley, 1991). Weaver and Fraley (1991) observed a significant inverse
relationship between the percentage of material smaller than 6.35 millimeters and the emergence success
of westslope cutthroat trout and bull trout. Further, they demonstrated a linkage between ground-
disturbing activities and spawning habitat quality.
Recommendations from the Flathead Basin Cooperative Forest Practice Study noted that fine sediment
(< 6.35 millimeters) levels exceeding 35 percent threaten bull trout and westslope cutthroat trout embryo
survival. This value is also similar to reference conditions described by Weaver and Fraley (31.7 ฑ 2.9)
(Weaver and Fraley, 1991). A running 5-year average of 35 percent fines smaller than 6.35 millimeters is
proposed as a target for the Flathead River Headwaters TPA.
A running average was selected for the McNeil core target to account for the year-to-year variability.
Year to year variability appears to be a function of a number of both natural and potentially human-
caused factors and ranges up to 20 percentage points based on the data that has been evaluated (see Table
D-l in Appendix D). It is thought that natural events such as flushing flows or low-flow periods may
account for much of this variability. The running average target was proposed to account for this
variability.
There are extensive McNeil core data for some streams (20+ years). The full period of record for all data
was used to identify trends, variability, and long-term averages (See Appendix D). Trends, where
identified, are discussed in the waterbody-by-waterbody discussions in Section 3.4. However, a McNeil
core value from the early 1980s does not necessarily represent current conditions in any stream, and the
purpose of this analysis is to determine if beneficial uses are currently impaired. Because of the dynamic
nature of activities in the watershed, historic data, while useful, should not be used when making a current
impairment determination. Therefore, data from the past five-years was chosen to represent "current
conditions" in the watershed.
3.3.1.2 Substrate Scores
Since the early 1980s, MFWP has calculated substrate scores for many of the streams within the FTPA to
provide an overall description of juvenile bull trout rearing habitat quality and observe trends over the
period of record.
A detailed description of substrate scores is presented in the Flathead Lake and River System Fisheries
Status Report (Deleray et al., 1999). In general, substrate scoring involves visually assessing the
dominant and subdominant streambed substrate particles, along with embeddedness in a series of cells
across transects. Surveyors assign a rank to both the dominant and subdominant particle size classes in
each cell. They also rank the degree to which the dominant particle size is embedded. The three ranks
are summed, yielding a single variable for each cell. All cells across each transect are averaged and a
mean of all transects results in the substrate score.
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Recommendations resulting from the Flathead Basin Cooperative Forest Practices Study observed that
substrate scores of 10.0 or less "threatened" juvenile bull trout rearing capacity; at scores less than 9.0,
rearing capacity was considered "impaired" (FBC 1991). A running five-year average score of > 10.0 has
been chosen as the target value for the FTPA. Similar to the McNeil core data (Section 3.3.1.1), the 5-
year average substrate score target was selected to account for natural variability in the data and to ensure
that current conditions are evaluated.
3.3.1.3 Macroiinvertebrates
Macroinvertebrate data help to provide a better understanding of the cumulative and intermittent impacts
that might have occurred over time in a stream, and they are a direct measure of the aquatic life beneficial
use. Analytical methods used to interpret macroinvertebrate data are constantly evolving, based on new
data and information offered from research. With this in mind, the macroinvertebrate targets and
supplemental indicators are intended to integrate multiple stressors and pollutants to provide an
assessment of the overall aquatic life use condition. The macroinvertebrate targets are also intended to
provide information regarding which pollutant(s) might be causing the impairment.
Several biological indicators were considered for the FTPA. These indicators include the Mountain Index
of Biological Integrity (IBI) (Bukantis, 1998), several individual biological metrics, and the relative
stressor tolerance of dominant benthic and macroinvertebrate taxa. Many of these provide an indication
of overall water quality, but do not specifically identify sediment as the cause of the impairment. Of the
evaluated metrics, the number of dinger taxa provides the strongest indication of a sediment impairment.
Clinger taxa have morphological and behavioral adaptations that allow individuals to maintain position on
an object in the substrate even in the face of potentially shearing flows. These taxa are sensitive to fine
sediments that fill interstitial spaces, one of the main niches. This metric is calculated as the number of
clinger taxa in a sample, and decreases in the presence of stressors. A minimum of 14 clinger taxa are
expected in unimpaired Montana streams, and this number is proposed as the target threshold value for
streams in the FTPA (Bollman, 1998). Other biological metrics and indices are discussed as
supplemental indicators in Section 3.3.2.
3.3.1.4 Surface Fines
Pebble counts provide an indication of the type and distribution of bed material (surface fines) in a
stream. Streams naturally have a wide variety of bed material, however, streams with too much fine
material can have lowered spawning rates for many fish species, especially salmonids. Too much fine
material also degrades the habitat of aquatic invertebrates, and can cause a shift in the invertebrate
population if conditions deteriorate from natural conditions. The state in which there is too much fine
sediment in a streambed is often referred to as "embeddedness" or "siltation." It is desirable (and usually
natural in the FTPA) that streams have a low percentage of bed material smaller than 2 millimeters in
diameter.
The Wolman pebble count method is one method for determining the amount of surface fines in a water
body. Wolman pebble counts involve wading across a transect in a riffle section from bankfull to
bankfull width. The field person places one foot in front of the other and, without looking down, selects a
particle and measures the intermediate diameter of the rock. This information is recorded and the
procedure followed until a minimum of 100 particles per transect are counted (Wolman, 1954). Pebble
count data can be interpreted to compare median particle sizes between streams, evaluate the percentage
of surface fines smaller than a specific size, and compare particle distributions between streams. Wolman
pebble counts were collected at several sites within the FTPA in 2002 and 2003.
Threshold surface fine sediment values have not been fully developed by MDEQ. Recent work
completed in the Boise National Forest in Idaho showed a strong correlation between the health of
macroinvertebrate communities and the percent surface fines, where fine sediments are defined as all
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particles less than 2 millimeters in diameter. The most sensitive species were affected at 20 percent
surface fines and a definite threshold was observed at 30 percent surface fines (Relyea, personal
communication, April 28, 2004). The New Mexico Environmental Department has also established a
percent surface fines target of less than 20 percent for TMDL development (NMED, 2002).
The percent surface fines provide a good measure of the siltation of a river system and, when combined
with biological indicators and other measures, is a direct measure of stream bottom aquatic habitat.
Although it is difficult to directly correlate the percent surface fines with loadings in mass per time, the
Clean Water Act allows "other applicable measures" for the development of TMDLs, and percent surface
fines have been used successfully in other TMDLs where stream bottom deposits, siltation, and aquatic
life uses are the major issues of concern (USEPA, 1993; USEPA, 1998; USEPA, 1999). Based on these
considerations, less than 20 percent surface fines (2 millimeters) is proposed as one of the TMDL target
for the FTPA. A maximum not-to-exceed target threshold value was chosen for percent surface fines
because there are no long-term surface fines data to evaluate natural variability. At the time of this report,
surface fines data were only available for one or two years at each site.
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Sediment Supplemental Indicators
As stated previously, the proposed supplemental indicators are not sufficiently reliable to be used alone as
a measure of sediment impairment in the streams within the FTPA. These indicators are used as
supplemental information, in combination with the targets, to provide better definition of potential
sediment impairments.
3.3.1.5 Macroinvertebrates
Mutimetric Index
Macroinvertebrate data are typically organized according to a multimetric index of biological integrity
(IBI). Individual metrics (e.g., dinger taxa, the percent EPT) are designed to indicate biological response
to human-induced stressors. Scores are assigned to individual metrics, summed across several of them,
and the total used to make comparisons among samples or sampling sites. Three possible multimetric
indices have been developed for Montana: (1) Mountain; (2) Foothill Valley and Plains (MFVP); and (3)
Plains. The Mountain IBI was chosen for streams in the FTPA based on site characteristics, primarily
elevation. The sites in the FTPA are located within the Northern Rockies ecoregion (Woods et al., 1999)
and range in elevation from 4,000 to 6,000 feet. MDEQ uses a scoring procedure with a maximum
possible score of 100 percent. Total scores greater than 75percent are considered within the range of
expected natural variability and represent full support of their beneficial use (aquatic life). A minimum
score of 75 percent was therefore chosen as a supplemental indicator. Streams scoring between 25
percent and 75 percent are considered partially supporting their aquatic life uses and scores lower than 25
percent represent non-supported uses.
Individual Metrics
To date, the strongest candidate metric relating to possible sediment impacts is the number of dinger taxa
(See Section 3.3.1.3). Additional metrics were collectively evaluated and used as supplemental
information to assess overall stream condition. The number of EPT taxa is a metric describing the
richness of mayflies (Ephemeroptera), stoneflies (Plecoptera), or caddisflies (Trichoptera) in a sample.
Invertebrates that are members of these groups are generally understood to be sensitive to stressors in
streams, whether physical, chemical, or biological. Consequently, they are less common in degraded
streams. Metric values decrease in the presence of stressors. Bahls et al. (1992) determined that the
average EPT taxa richness for mountain streams in Montana was 22 taxa. A minimum of 22 EPT taxa is
proposed as a supplemental indicator in the FTPA. A minimum threshold value was chosen for EPT taxa
because there are no long-term data to evaluate natural variability. At the time of this report,
macroinvertebrate data were only available for one or two years at each site.
The percentage of dinger taxa in a sample is also proposed as a supplemental indicator. This metric is
calculated as the number of individuals categorized as belonging to dinger taxa as a proportion of the
total sample, and the value decreases in the presence of stressors. There are no values published in the
scientific literature or other information on the expected percentage of dingers for the area. A high
percentage of dingers suggests little impact from sediment. This metric, used in conjunction with the
number of dinger taxa (Section 3.3.1.3), will provide supplemental information on the overall impacts of
sediment.
Other individual macroinvertebrate metrics were evaluated based on their recognized response to certain
stressors (Barbour, 1999). Continued research is needed to refine and document the diagnostic
capabilities of these metrics and the response of individual species to specific pollutants. For that reason,
the following metrics are included in the macroinvertebrate discussions to provide supporting
information, but they are not intended to be used as targets or supplemental indicators for sediment
impairments.
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Percent tolerant taxa. The tolerance value designation is an estimate of the relative
capacity of a taxon to survive and reproduce in the presence of stressors (for more
discussion of tolerance values, see below). This metric is calculated as the number of
tolerant taxa as a proportion of the total taxa richness in a sample, and it increases in the
presence of stressors. A higher proportion of tolerant taxa suggests impacts to the
biological condition. Since a threshold value for percent tolerant taxa has not been
determined, this metric provides supplemental information regarding the possible
impacts of other stressors.
Tolerance Values (TV) of the Dominant Taxa. The TV of the dominant taxa in a
sample can also provide some indication of the presence of stressors at the site.
Tolerance values for Montana benthic macroinvertebrate taxa were provided by Marshall
and Kerans (2003 [draft]). Although the objectivity used in developing TVs is often
unknown, the TVs of the dominant taxa were used as additional information to help
interpret reach status. For each sampling site, the five dominant taxa in each sample and
their associated stressor tolerance values were examined.
Hilsenhoff Biotic Index (HBI). The HBI is an abundance weighted index developed to
assess impacts from organic pollution (Hilsenhoff 1987). Bahls et al. (1992) determined
the average HBI value for mountain streams was less than 4. A conservative value of
3.5 is recommended for comparison.
3.3.1.6 Periphyton
MDEQ has collected periphyton samples at sites throughout the state for more than 15 years. Periphyton
are recommended as an additional biological assemblage (USEPA, 1997, 2003) and diatoms, in
particular, are considered useful water quality indicators because so much is known about the relative
pollution tolerances of different taxa and the water quality preferences of common species (Bahls, 2003;
Barbour et al., 1999). MDEQ uses several different diatom indices to assess stream condition.
Analysis of the periphyton data focused on the siltation index, which provides an indication of periphyton
health with respect to sediment impact. The siltation index is the sum of the percent abundance of all
species in the silt-tolerant diatom genera Navicula, Nitzschia, and Surirella. A high value (> 20.0) for this
index indicates potential sediment impacts in mountain streams, and this was chosen as a supplemental
indicator of impairment (Bahls, 2003). An annual not to exceed maximum supplemental indicator value
was chosen because there are no long-term data to evaluate natural variability. At the time of this report,
periphyton data were only available for one or two years at each site.
Summary findings from the periphyton data will provide additional information and could suggest the
presence of other stressors. Both the siltation index and these summary findings will be used to derive
conclusions regarding water quality at each site.
3.3.1.7 Pfankuch Ratings
The Pfankuch Stream Channel Stability rating was developed to "systemize measurements and
evaluations of the resistive capacity of mountain stream channels to the detachment of bed and bank
materials and to provide information about the capacity of streams to adjust and recover from potential
changes in flow and/or increases in sediment production" (Pfankuch, 1978). This procedure uses a
qualitative measurement with associated mathematical values to reflect stream conditions. The rating is
based on 15 categories: 6 categories related to the bottom of the stream channel (the part of the channel
covered by water yearlong), 5 related to the lower banks (covered by water only during spring runoff),
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and 4 related to the upper banks (covered by water only during flood stages). Prime fish habitat usually
occurs in streams with a good rating.
The proposed supplemental indicators focus on two of the four categories related to the upper banks (i.e.,
mass wasting and vegetative bank protection), and two of the five categories related to the lower banks
(i.e., cutting and deposition). These four categories are felt to provide the best information for
interpretation of potential sediment impairments at selected sites within the FTPA. However, it should be
noted that the results of these analyses do not differentiate between natural and anthropogenic causes.
Also, the scores do not provide any indication of the natural potential of a stream (i.e., a stream's natural
potential may only be "fair" for bank cutting). Pfankuch ratings are based on visual interpretation and,
therefore, subject to observer bias. For these reasons, the ratings are considered supplemental indicators
as opposed to targets and are used as supporting evidence of potential sediment impairments. In lieu of
information that indicates the potential of a stream, a rating of "good" or better is proposed as an indicator
value for the Pfankuch ratings.
Mass Wasting provides a visual estimate of the degree to which mass wasting has
occurred at a site or has the potential to occur in the future. Scores are assigned from
1 to 12, as defined in Table 3-8.
Vegetative Bank Protection provides a visual estimate of vegetative density and the
soil binding properties of the vegetation on the upper banks. As with Mass Wasting,
scores are assigned from 1 to 12, as defined in Table 3-9.
Cutting refers to the degree the lower bank the lower banks have eroded. Scores are
assigned from 4 tol6, as defined in Table 3-10.
Deposition provides a visual estimate of the extent to which deposition has occurred
on the lower banks. Scores are assigned from 4 to 16, as defined in Table 3-11.
Table 3-8. Mass Wasting Rating Description
Condition Description
Score
Rating
No evidence of past or future mass wasting
Infrequent. Mostly healed over. Low future potential
Frequent or large, causing sediment nearly yearlong
Frequent or large, causing sediment nearly yearlong or imminent danger of same
6
9
12
Excellent
Good
Fair
Poor
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Table 3-9. Vegetative Bank Protection Description
Condition Description
Score
Rating
90%+ plant density. Vigor and variety suggests a deep dense soil binding root mass
70-90% plant density. Fewer species or less vigor suggest less dense or deep root mass
< 50-70% plant density. Lower vigor and fewer species for a shallow, discontinuous root
3
6
9
Excellent
Good
Fair
< 50% plant density. Less vigor and fewer species indicate poor, discontinuous, and
shallow root mass
12
Poor
Table 3-10. Cutting Description
Condition Description
Score
Rating
Little or none. Infrequent Raw banks less than 6 inches
Some, intermittently at outcurves and constrictions. Raw banks up to 12 inches
Significant. Cuts 12-24 inches high. Root mat overhangs and sloughing evident
Almost continuous cuts, some over 24 inches high. Failure of overhangs frequent
4
6
12
16
Excellent
Good
Fair
Poor
Table 3-11. Deposition Description
Condition Description
Score
Rating
Little or no enlargement of channel or point bars
Some new increase in bar formation, mostly from coarse gravels
Moderate deposition of new gravel and coarse sands on old and some new bars
Extensive deposits of predominantly fine particles. Accelerated bar development
4
8
12
16
Excellent
Good
Fair
Poor
3.3.1.8 Fish Population
Fisheries are an important designated use in freshwater streams. Fish represent the higher trophic levels in
streams and lakes. They serve as a surrogate for many physical and biological parameters such as
adequate flow, spawning and rearing habitat, appropriate food sources, and proper environmental
conditions.
MFWP has collected bull trout redd counts and juvenile bull trout and westslope cutthroat trout
population estimates in many of the FTPA streams since the early 1980s (Deleray et al., 1999). Both redd
counts and juvenile population densities provide a direct measure of the cold-water fishery beneficial use
and therefore provide an important indicator of stream impairment. The proposed supplemental indicator
is stable or increasing trends in redd counts and juvenile population densities.
Both the redd count and juvenile population density data are used with caution herein due to a number of
complicating factors that have little to do with the condition of the spawning tributaries. As described in
Section 2.2.2, migratory populations of bull trout, for example, have fluctuated due to food web changes
in Flathead Lake. A major decline in redd counts in those tributaries contiguous with Flathead Lake (all
North and Middle Fork tributaries) occurred in the 1990s as a result. In addition, fish populations might
change due to effects outside of management control such as temperature, peak runoff, primary
productivity, and competition from other fish species and invertebrate populations. For this reason, the
proposed fisheries indicators must be used in combination with the full suite of targets to avoid
misinterpretation.
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3.3.1.9 Suspended Sediment Concentration
Considerable historical suspended sediment concentration data is available in several streams in the
FTPA. These data have been evaluated and were considered as collaborative evidence in support of the
water quality impairment status conclusions reached in Section 3.4.
Chepat Creek is a 3.4-mile long first-order tributary with a 1,112-acre watershed in the Upper Stillwater
River Basin. The Montana Department of Natural Resources and Conservation (DNRC) (Mathieus,
2001) have collected flow and total suspended solids data in Chepat Creek annually since 1976 (n = 253).
The catchment area of Chepat Creek has experienced only very minor timber harvest and contains few
roads. The monitoring data from this water body are therefore considered baseline; that is, indicative of
the water quality of an undisturbed watershed. The mean total suspended solids concentration for the
period of record is 3.15 ฑ 5.83. The maximum reported value is 61.60 mg/L and the mean annual
maximum is 14.56 mg/L. Theses values were chosen as supplemental indicators.
The above values are presented as metrics for comparison to the 303(d)-listed waters in the Flathead
River Headwaters TPA. It is recognized herein that the Chepat Creek Basin is smaller than most of the
subject basins within the FTPA. It is also recognized that the results for Chepat Creek are based on total
suspended solids (TSS) concentrations as opposed to suspended solids concentration (SSC). SSC values
have been shown to exceed TSS values in paired studies (Gray et. al., 2000). Therefore, comparison of
the Flathead Headwaters SSC data with the Chepat Creek TSS data will result in a conservative
comparison. However, these values are used only for comparison purposes and as collaborating
evidence when combined with other more robust measures of sediment impairment.
3.3.1.10 Turbidity
Montana's water quality standard for turbidity varies according to stream classification. The subject
waters within the FTPA are all classified as B-l. For B-l waters, the standard is no more than a 5 NTU
(instantaneous) increase above naturally occurring turbidity. In the absence of sufficient data to
characterize "naturally occurring turbidity," it is not possible to directly apply this standard as a TMDL
target.
As a result, although turbidity data are available they will be used only as collaborating evidence when
combined with other more robust measures of sediment impairment. The State of Idaho's standard to
protect cold-water aquatic life will be used as the proposed supplemental indicator value. In accordance
with Idaho's Water Quality Standards and Wastewater Treatment Requirements (Section
58.01.02.250.02.e), turbidity below any applicable mixing zone should not be greater than 50 NTU
(instantaneous). This value will be applied to high flow events or during the time of annual runoff. Some
evidence suggests that detrimental effects on biota can occur with turbidity as low as 10 NTU. The State
of Idaho therefore has recommended that chronic turbidity not exceed 10 NTU during summer base flow.
To be conservative, both of these values are applied as instantaneous maximum supplemental indicators
in the Flathead River Headwaters Planning Area.
3.3.1.11 Sediment Sources
The FTPA is sparsely populated and relatively remote with substantial areas under the protection of the
National Park Service or Wilderness Designation. Therefore, it is not appropriate to assume that
deviations from the targets and/or supplemental indicators are necessarily a result of human actions.
Consideration of sources, therefore, is important given that TMDLs are necessary only for impairments
caused by anthropogenic sources.
The FNF conducted a detailed sediment source assessment in 2002 and 2003 focusing on the
identification of active sediment sources associated with their past and current management activities and
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road networks (Appendix B). A GIS and aerial photography assessment was conducted to identify
managed areas with the potential for erosion and sediment delivery to streams. This was followed by site
reconnaissance visits to verify the results of the remote investigation in roughly 50 percent of the areas
considered potential source areas.
Several indicators were chosen to describe the impact of potential sources of sediment in the FTPA.
Each indicator is described below in more detail.
Fire. Fire is a common occurrence in the western Montana landscape and it can be
the cause of impaired beneficial uses in a stream. A burned landscape can result in
increased water yield, increased sediment runoff, and increased organic loading, and
it can cause changes to the stream channel (log jams, increased woody debris). In the
TMDL process, it is important to understand the fire history of a watershed as it
relates to measured in-stream data. In-stream data, such as data on
macroinvertebrates or percent fines data, can indicate an impairment that is
completely due to natural sources, such as fire. Because of this, the fire history is
described in the source assessment section for each watershed to provide a better
understanding of natural sources of sediment.
Equivalent Clear-Cut Acres. The impact of forest harvest was evaluated for each
watershed by calculating the equivalent clear-cut acreage (ECA). ECA is an estimate
of the cumulative effect of multiple years of forest crown removal (including both
harvest and fire), and is calculated by considering the timing, amount, and location of
cut acres in the watershed. In general, an ECA of greater than 25 percent suggests a
potential for increased water and sediment yield (Jones and Grant, 1996). Region 1
of the Forest Service also suggests that watersheds with an ECA greater than 25
percent are at risk for having detrimental increased water yields (Bengeyfield,
personal comm., June 11, 2004). FNF calculated ECAs for the spring of 2004 using
a modified WATSED model.
Water Yield. An increase in water yield can lead to increased flows, higher bank
erosion rates, more scouring, and sediment imbalances in a stream. The Montana
DNRC calculated water yields using a modified version of WATSED for six
watersheds in the FTPA: Coal Creek, Lower Coal Creek, Cyclone Creek, Dead Horse
Creek, Upper Coal Creek, and South Fork Coal Creek (FNF, 2004). In general, water
yield increases greater than 10 percent in Rosgen "C" type channels indicate that
increased sediment yield and channel altering flows might be present. Increases in
water yield generally have less impact on A and B stream types (see section 2.1.3 for
an explanation of stream types) because of their gradient and channel dimensions.
Roads. The FNF crew completed driving and walking surveys on all open, closed,
and decommissioned roads in the 303(d)-listed watersheds. Roads were evaluated to
determine the condition and number of road/stream crossings, and the number of road
miles in need of best management practices (BMPs). Total road miles within 125
feet of the stream, total road miles within 300 feet of the stream, and road density
were then evaluated in a geographic information system (GIS). Road density was
compared to the Forest Service rankings described in Table 2-9. As a supplemental
indicator, roads were evaluated on a case-by-case basis for each 303(d) listed
watershed to determine potential effects.
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These supplemental indicators have been proposed to assist in verifying water quality impairment
determinations. No water quality goals or endpoints involving sources are proposed. A detailed
consideration of sources is provided in Section 4.0 for those waters described as impaired in Section 3.4.
3.3.2 Nutrient Targets
The proposed nutrient targets reflect EPA's nutrient criteria and benthic chlorophyll-a for Nutrient
Ecoregion II (Western Forested Mountain) streams.
3.3.2.1 EPA Ecoregion Nutrient Criteria
EPA has proposed nutrient criteria for ecoregions throughout the United States. Criteria for Nutrient
Ecoregion II (Western Forested Mountains) are proposed here as targets for North Fork Coal Creek
(USEPA, 2000). Recommendations are for median total phosphorus, total nitrogen, nitrate plus nitrite,
and total Kjeldahl nitrogen (TKN) concentrations, and are proposed here as 5-year median targets for the
North Fork Coal Creek (Table 3-12).
Table 3-12. Nutrient Concentration Targets for the North Fork Coal Creek
Nutrient Parameter
Threshold Value
Total Phosphorus
< 0.01 mg/L
Total Nitrogen
<0.12 mg/L
Nitrate+Nitrite (N02/N03)
< 0.014 mg/L
Total Kjeldahl Nitrogen (TKN)
< 0.05 mg/L
3.3.2.2 Benthic Chlorophyll-a
Benthic algae (also known as periphyton) are found growing on substrate surfaces in streams, unlike free-
floating organisms found in the water column (phytoplankton). Benthic algae data help to provide a
better understanding of the cumulative and intermittent impacts that may have occurred over time in a
stream, and are useful for determining whether impairments due to nutrients are present. EPA has
proposed benthic algae criteria for Nutrient Ecoregion II streams (Western Forested Mountains) based on
the measured amount of chlorophyll-a (in milligrams) divided by the total substrate area (in square
meters). The EPA's proposed criterion, based on the 25th percentile of an ecoregional dataset, is a median
value of less than 33 mg/m2. A value of less than 33 mg/m2 is proposed as a target.
3.3.3 Nutrient Supplemental Indicators
The proposed supplemental indicators are not sufficiently reliable to be used alone as a measure of
nutrient impairment in the streams within the FTPA. These indicators are used as supplemental
information, in combination with the targets, to provide better definition to potential nutrient
impairments.
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3.3.3.1 Hilsenhoff Biotic Index
The HBI is an abundance-weighted macroinvertebrate index developed to assess impacts from organic
pollution and associated low dissolved oxygen in streams (Hilsenhoff, 1987). The index assesses the
tolerance value and abundance of various macroinvertebrates with specific sensitivities to organic
loading. A low index score indicates good water quality with no indication of organic enrichment. A
high HBI score suggests that long-term low dissolved oxygen concentrations are present, usually due to
organic loading. Bahls et al. (1992) determined that the average HBI value for reference Montana
mountain streams was less than 4. Bollman (2002, 2003) has also applied the HBI index to various
streams through out northwest Montana to assess the presence of organic loading. A conservative
maximum value of 3.5 is recommended for comparison.
3.3.3.2 Mountain IBI
Macroinvertebrate data are typically organized according to a multimetric index of biological integrity
(IBI). Individual metrics (e.g., dinger taxa, percent EPT) are designed to indicate biological response to
human-induced stressors. Scores are assigned to individual metrics, summed across several of them, and
the total used to compare samples or sampling sites. Three possible multimetric indices have been
developed for Montana: (1) Mountain; (2) Foothill Valley and Plains (MFVP); and (3) Plains. The
Mountain IBI was chosen for streams in the FTPA based on site characteristics, primarily elevation. The
sites in the FTPA are located within the Northern Rockies ecoregion (Woods et al., 1999) and range in
elevation from 4,000 to 6,000 feet. MDEQ uses a scoring procedure with a maximum possible score of
100 percent. Total scores greater than 75 percent are considered within the range of expected natural
variability and represent full support of their beneficial use (aquatic life). This score is proposed as a
supplemental indicator for streams in the FTPA. Streams scoring between 25 percent and 75 percent are
considered partially supporting their aquatic life uses and scores lower than 25 percent represent
unsupported uses.
3.3.3.3 Water Column Chlorophyll-a
EPA has proposed water column chlorophyll-a concentrations as part of the ecoregional nutrient criteria.
Concentrations are measured as the amount of chlorophyll-a in the water column, and can provide an
indication of the amount of algal biomass in the stream. High chlorophyll-a concentrations suggest that
there is an excessive amount of algae in a stream, which further suggests that excessive organic loading is
present. Water column chlorophyll-a is referred to as a response variable as opposed to a direct nutrient
measurement and, as such, is included as a supplemental indicator. EPA (2000) suggested that median
water column chlorophyll-a values for Western Forested Mountain streams should not exceed 1.08 (ig/L.
This is proposed as a supplemental indicator for the North Fork Coal Creek.
3.3.3.4 Dissolved Oxygen
Nutrients generally do not pose a direct threat to the beneficial uses of a water body. However, excess
nutrients can cause an undesirable abundance of plant and algae growth. This process is called
eutrophication or organic enrichment. Organic enrichment can have many effects on a stream or lake.
One possible effect is low dissolved oxygen concentrations. Aquatic organisms require oxygen to live and
they can experience lowered reproduction rates and mortality with lower dissolved oxygen
concentrations.
MDEQ's numeric dissolved oxygen criteria are shown in Table 3-13, and are proposed as supplemental
indicators for the determination of nutrient impairments (MDEQ, 2004). Because North Fork Coal Creek
is used by several species of fish for spawning (including bull trout), the more stringent water column
criteria are proposed to ensure that inter-gravel dissolved oxygen concentrations are met.
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Table 3-13. Numeric Dissolved Oxygen Criteria.
Time Period
Early Life Stages''
Other Life Stages"
30-Day Mean (mg/L)
NA
6.5
7-Day Mean (mg/L)
9.5
NA
7-Day Mean (minimum) (mg/L)
NA
5.0
1-Day Minimum (mg/L)
8.0
4.0
a Dissolved oxygen criteria applicable when early life stages are present.
B Dissolved oxygen criteria applicable when early life stages are not present.
3.3.3.5 Nutrient Sources
As with sediment, it is not appropriate to assume that deviations from the targets and/or other
supplemental indicators are necessarily a result of man's actions. Consideration of sources, therefore, is
important given that TMDLs are necessary only for nutrient impairments that have anthropogenic causes.
Three indicators were chosen: Fire, Equivalent Clear-Cut Acres (ECA), and Water Yield. Fires have the
potential to directly increase inorganic nutrient loading to a stream by converting organic matter to
soluble, inorganic nutrients. ECA also captures the effects of fire, and therefore is included as a
supplemental indicator. Furthermore, clear-cuts and increased water yield can result in increased nutrient
concentrations in a stream (Hauer et al., 1991). Each of those supplemental indicators is discussed in
more detail in Section 3.3.2.7.
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3.4 Current Water Quality Impairment Status
This section presents summaries and evaluations of all available water quality data for waters appearing
on Montana's 1996 and 2002 303(d) lists. The weight-of-evidence approach described above in Section
3.3, using a suite of targets and supplemental indicators, has been applied to verify each of the water
quality impairments listed in 1996 and 2002. This section provides supporting documentation for each
water body within each of the three major drainages.
3.4.1 North Fork Flathead River Watershed
The North Fork Flathead River watershed (which lies within both Canada and the United States) spans
997,176 acres, or 1,558 square miles (Figure 3-4). The North Fork Flathead River flows for 53.8 miles in
Canada and 54.2 miles in the United States for a total of 108 river miles. The Canadian portion of the
drainage spans 375,919 acres or 593 square miles. The U.S. portion of the drainage spans 617,598 acres
or 965 square miles.
To paraphrase from Stanford (2000), the North Fork differs substantially from the Middle Fork, South
Fork, and the main stem of the Flathead River. The North Fork flows through a broad alluvial valley with
braided and anastomosed channels and expansive floodplains. The North Fork primarily drains lands
underlain by Precambrian Belt series bedrocks. The North Fork river corridor offers nearly intact
ecological connectivity. Biota are able to migrate longitudinally from headwaters to the confluence with
the Middle Fork and on to Flathead Lake. The expansive floodplains of the river link the channel to the
uplands and foster movements between Glacier National Park and the Whitefish Range.
Streams listed as impaired on Montana's 303(d) list in the North Fork Flathead River watershed are Big
Creek, Red Meadow Creek, Whale Creek, the South Fork Coal Creek, North Fork Coal Creek, and Lower
Coal Creek - Main stem.
3.4.1.1 Big Creek
The cold-water fishery and aquatic life beneficial uses in Big Creek were listed as impaired on the 1996
303(d) list. The FNF completed a Watershed Restoration Plan for Big Creek, including all necessary
TMDLs. EPA approved the TMDL for Big Creek on May 9, 2003. As a result, Big Creek is not
discussed further herein.
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/\/303(d) Listed Segments
O Cities
| Lakes
, ' Counties
/, v
Streams
~ North Fork Flathead River Watershed
2 0 2 4 6 Miles
Figure 3-4. North Fork Flathead River watershed.
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3.4.1.2 Red Meadow Creek
Red Meadow Creek is a second-order tributary flowing approximately 12 miles from its origin at Red
Meadow Lake to its confluence with the North Fork Flathead River (Figure 3-5). The total watershed
area covers roughly 30 square miles. The cold-water fishery and aquatic life beneficial uses were listed as
impaired by habitat alterations and siltation on both the 1996 and 2002 303(d) lists. The basis for the 1996
listing is unknown. According to MDEQs Assessment Record Sheet (Chesnut, 1999), the 2002 listing
was based primarily on the results of a 1989 MDEQ stream assessment conducted in two reaches of Red
Meadow Creek. For the headwaters reach, MDEQ concluded the following:
"... large amount of debris in channel, especially cut logs. Excessive sediment
accumulation in pools behind debris jams. Scouring is also present. The channel has
undergone migration due to debris. Several jams large enough to prevent fish passage.
Impairments most likely due to logging operation. There is also litter from recreation
users near the upper end. "
MDEQs Assessment Record Sheet also cited a decline in fish populations since 1983. It should be noted
that MDEQ's 1989 stream assessment was conducted 1 year after the Red Bench Fire occurred in the
lower reaches of this watershed, reflecting a large amount of large woody debris following the fire
(Deleray et al.. 1999). Because of the fire, MDEQ noted that it was difficult to attribute sediment-related
impairments in the lower reaches of Red Meadow Creek to anthropogenic sources.
A review of the available data is presented below. Available data include substrate scores, McNeil cores,
Pfankuch ratings, pebble counts, sources (fires, harvest, roads), macroinvertebrates, and fish population
estimates. The SSC and turbidity data are outdated and are too limited in number to be useful, and
therefore, they are not considered further.
ฆ Towns
A 2003 Biology Sampling Sites
4 2003 Physical Sampling Sites
l-alues
/V Stซamป
/\f 1996 303(d) Listed Streams
Roads
2 MIh
Figure 3-5. Red Meadow Creek watershed.
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McNeil Core
MFWP collected McNeil core samples in Red Meadow Creek in 1988 and 1989 (Weaver et al., 2003). A
mean value of 40.1 percent fines smaller than 6.35 mm was reported. As in the 1989 MDEQ field
assessment, the data were collected soon after the Red Bench Fire. No conclusions can be reached
regarding this target in the absence of recent data.
Substrate Scores
Substrate scores were calculated based on MFWP stream surveys conducted from 1988 through 2002
(Deleray, et al., 1999). From 1998 to 2002, the mean substrate score was 11.9, indicating good juvenile
bull trout rearing habitat quality. The mean substrate score for the period of record (1984-2002) was
also 11.9.
Pebble Counts
Pebble counts were conducted at two sites: one on the South Fork of Red Meadow Creek on July 10,
2003, and one on the main stem of Red Meadow Creek on July 8, 2003. The percent surface fines smaller
than 2 millimeters at the South Fork and main-stem sites were 18.75 percent and 12.71 percent,
respectively. Both values are below the 20 percent target, and suggest no impairment from siltation.
Macroin vertebrates
Macroinvertebrate sampling was performed at one site on Red Meadow Creek in August 2003. The
number of dinger taxa (23) was above the target of 14, which suggests that sediment impacts were not
present. The Mountain IBI was 81, which is above the 75 percent recommended value to be considered
fully supporting aquatic life beneficial uses. There were a high number of EPT taxa (27) and a high
percentage of dinger taxa (69 percent). Other supporting metrics also suggest that no water quality
impairments were present. No tolerant taxa were found in the sample. The HBI score was 2.63, which is
below the recommended value of 3.5. The five most dominant taxa (Heterlimnius, Arctopsyche grcindis,
Drunella doddsi, Epeorus deceptivus, and Baetis tricaudatus) had low tolerance values and are sensitive to
pollution. The entire suite of macroinvertebrate metrics suggests that the site on Red Meadow Creek
shows no evidence of siltation or any other water quality problems.
Fish Population
MFWP conducted electrofishing surveys between 1983 and 2002 in Red Meadow Creek (Deleray et al.,
2003). Densities of bull trout 1 year old or more have declined from a high of 5.9 per 100 square meters
in 1983 to 0.16 per 100 square meters in 1995 (Figure 3-6). Bull trout redd counts (1980-2000) also
showed a declining trend. However, declines in the bull trout population may be due to changes in the
Flathead Lake ecosystem, and do not necessarily indicate beneficial use impairment (see Section 2.2.2).
Westslope cutthroat trout populations fluctuated over the same period of record, but unlike the bull trout,
showed no overall trend (Figure 3-6). This indicates that the cause of the declining bull trout population
is not similarly affecting the westslope cutthroat trout population.
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i 1 1 i~
Year
Figure 3-6. Age 1 and older bull trout and Westslope cutthroat trout densities in Red Meadow
Creek.
Pfankuch Ratings
Pfankuch ratings were estimated at three locations along an approximately 1,000-foot-long reach of Red
Meadow Creek on July 9, 2003. The three ratings were averaged to provide a single value for each of the
four Pfankuch categories listed in Table 3-14. Although these results are based on visual observation and
are therefore qualitative, they suggest that the stream banks are in relatively good shape (i.e., good and
excellent scores for mass wasting and cutting) with excellent vegetative bank protection. Deposition of
fine material along the lower banks is minor.
Table 3-14. Selected Pfankuch Ratings for Red Meadow Creek
Pfankuch Category
Score
Rating
Mass Wasting
Vegetative Bank Protection
Cutting
Deposition
4
2.67
Good
Excellent
Good
Good
Sources
As shown in Figure 2-26, approximately 24 percent of the watershed burned in 1988 in the Red Bench
Fire. There have been no significant fires in Red Meadow Creek since then. Since 1960, clear-cut
harvest has occurred in approximately 13 percent of the watershed. Clear-cut harvest trends have
declined substantially since 1960, with the last harvest occurring in 1990 when 1.5 percent of the
watershed was clear-cut. The calculated equivalent clear-cut acreage (ECA) for 2004 is 12.2 percent
The FNF identified active upland erosion areas during a source assessment survey conducted in 2003
(Appendix B). Total road density in the Red Meadow watershed is 1.1 miles/square mile, and a total of
76 road/stream crossings were identified and evaluated (FNF, 2003). None were considered at risk of
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failure. Nine miles of roads are in need of BMPs or upgrading. Most of this road length (8 miles) is a
stretch of the main access road (Road 115), which needs improved drainage at first-order stream crossings
and more ditch relief culverts to reduce sediment. One mile of Road 115A might be contributing
sediment, and it is in need of grading, ditch relief, water bars, and culvert maintenance. Almost half the
roads in the watershed are located within 125 feet of a stream channel (14.6 out of 33.4 miles). Although
road density is fairly low, it appears that roads are contributing some sediment to streams.
Red Meadow Creek Water Quality Impairment Summary
Red Meadow Creek was listed on the 1996 and 2002 303(d) lists as impaired because of siltation and
habitat alterations. Aquatic life and cold-water fishery beneficial uses were the listed impaired beneficial
uses.
It appears that beneficial uses are not currently impaired by siltation in Red Meadow Creek. The target
and supplemental indicator values are met for all parameters except McNeil cores and bull trout
populations. Based on the FNF's source assessment survey, there are some actively eroding sediment
sources in the Red Meadow Creek watershed; however, no evidence exists of sediment-caused
impairment in the macroinvertebrate data. Macroinvertebrate scores indicate that the aquatic life
beneficial uses are not impaired, and the high dinger values suggest that there are no aquatic life
impairments associated with sediment. Neither the substrate scores nor the percent surface fines suggest
sediment impairment. Finally, none of the visual estimates of mass wasting, vegetative bank protection,
bank cutting, and lower bank deposition suggest sediment-related water quality impairments.
Although the mean McNeil core value (40.1 percent subsurface fines smaller than 6.35 millimeters)
exceeds the target, the McNeil cores were collected roughly 14 years ago (two samples), soon after a fire
that burned 24 percent of the watershed. Therefore, the McNeil core data are not considered valid for
making current beneficial use impairment determinations. The decline in bull trout redd counts and
juvenile population cannot necessarily be attributed to water quality conditions in Red Meadow Creek
because of the possible influences of Flathead Lake on the bull trout population. The fact that juvenile
cutthroat populations have not declined over the same period of record suggests that habitat conditions in
Red Meadow Creek are good.
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Table 3-15. Comparison of Available Data with the Proposed Targets and Supplemental Indicators
for Red Meadow Creek
Targets
Threshold
Available Data
5-year Mean McNeil Core Percent Subsurface Fines
< 6.35 mm
35%
40.1%*
5-year Mean Substrate Scores
> 10
11.9
Percent Surface Fines < 2 mm
< 20%
12.7%
Clinger Richness
> 14
23
Supplemental Indicators
Recommended Value
Available Data
Juvenile Bull Trout and Westslope Cutthroat Trout
Density
Documented increasing or stable
trend
Stable (Cutthroat)
Decline (Bull)
Bull Trout Redd Counts
Documented increasing or stable
trend
Decline
SSC Mean
SSC Mean Annual Maximum
SSC Maximum
3.2 + 5.2
14.6
61.6
NA
Turbidity
High flow-50 NTU instantaneous
maximum
Summer base flow - 10 NTU
NA
Pfankuch Mass Wasting Score
"good"
Good
Pfankuch Bank Vegetation Score
"good"
Excellent
Pfankuch Cutting Score
"good"
Good
Pfankuch Deposition Score
"good"
Good
Montana Mountain Macroinvertebrate Index of
Biological Integrity
> 75%
81%
Percentage of Clinger Taxa
"high"
69%
EPT Richness
>22
27
Periphyton Siltation Index
<20
NA
Fire
Evaluated on a case-by-case basis
Year: 1988
% Burned: 24
Equivalent Clear-Cut Acres
< 25%
12.2%
Water Yield
< 10%
NA
Roads
Evaluated on a case-by-case basis
Some roads in need
of BMPs
*Historical data from 1988/1989
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3.4.1.3 Whale Creek
Whale Creek is a third-order tributary of the North Fork Flathead River flowing 21 miles from the
headwaters to the mouth (Figure 3-7). The total watershed area covers approximately 78 square miles.
The cold-water fishery beneficial use was listed as threatened on the 1996 303(d) list because of habitat
alterations and siltation. The basis for the 1996 listing is unknown. Cold-water fishery and aquatic life
beneficial uses were listed as impaired on the 2002 303(d) list because of habitat alterations and siltation.
According to MDEQ's Assessment Record Sheet (Chestnut, 1999), the 2002 listing was based primarily
on the results of a 1989 MDEQ stream assessment that indicated that the impaired reach extends from the
headwaters to the confluence with Shorty Creek, and
"Sedimentation problems, stream braiding, cut logs in channel all attribute to impairment. Improper
logging procedures are most likely cause of the problems. "
A review of the available data is presented below. Available data include substrate scores, McNeil cores,
Pfankuch ratings, pebble counts, sources (fires, harvest, roads), macroinvertebrates, suspended sediment
concentration data, turbidity data, and fish population estimates.
Figure 3-7. Whale Creek watershed.
ฆ Towns
ฃ 2003 Biology Sampling Sites
0 2003 Physical Sampling Sites
m Lakes
/\J Streams
/\y 1996 303(d) Listed Streams
Rpปds
t I Whale Creek Watershed
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McNeil Core
MFWP collected McNeil core samples in Whale Creek between 1981 and 2001 (Weaver et al., 2003).
The mean value for the past 5 years is 31.3 percent fines smallerthan 6.35 millimeters. In 2001, the
McNeil core value was 31.6 percent and the maximum for the past 5 years is 31.9. All of these values are
below the proposed target.
Substrate Scores
Substrate scores were calculated based on MFWP stream surveys conducted in 1988 through 2002
(Deleray et al., 1999). From 1998 to 2002, the mean substrate score was 12.2, indicating good juvenile
bull trout rearing habitat quality. The mean substrate score for the period of record was 11.8.
Pebble Counts
Pebble counts were conducted in two reaches ( at three locations in each reach - upper, cross section, and
lower) in Whale Creek in 2003. Whale Creek reach # 1 is the downstream reach near the confluence with
Hornet Creek (Figure 3-7). The percent surface fines smaller than 2 millimeters at reach #1 were 11
percent (upper), 27 percent (cross section), and 19 percent (lower). The average percent surface fines for
this reach was 19 percent, which is below the proposed target of 20 percent.
Whale Creek reach #2 just upstream of the confluence with Akinkoka Creek (Figure 3-7). The percent
surface fines smallerthan 2 millimeters at reach #2 were 21.6 percent (upper), 13.3 percent (cross
section), and 15.7 percent (lower). The average percent surface fines for this reach was 16.9 percent,
which is below the proposed target of 20 percent.
Overall, the percent surface fines in Whale Creek suggest that the stream is not impaired because of
siltation.
Macroin vertebrates
Macroinvertebrates were collected at two sites in Whale Creek in August 2003 (Figure 3-7). Organisms
at the upstream site suggest cold, clean water and little anthropogenic influences (Bollman, 2003b). The
number of dinger taxa (20) was above the target of 14, which suggests that sediment impacts were not
present. Also, the Mountain IBI score (81) and percentage of dingers (70) were greater than the
recommended values. Both suggest good water quality with no impairment from sediment. Only the
number of EPT taxa (20) was slightly lower than the indicator value. Other supporting metrics also
suggest that no water quality impairments were present. The sample was dominated by sensitive taxa,
and the HBI score (2.41) was lower than the recommended value of 3.5. The five most dominant taxa
(Rhithrogena, Eukiefferiella Brehmi Gr., Drunella doddsi, Epeorus deceptivus, and Epeorus grandis) all
had low tolerance values and are intolerant to pollution. Overall, the data suggest that aquatic life at the
upstream site on Whale Creek is not impaired because of sediment.
Macroinvertebrates were also collected at a downstream site in Whale Creek near the North Fork Road
Bridge. Clinger data (16 taxa, 89 percent of the sample) indicated that sediment was not a cause of
impairment at this site. However, the Mountain IBI score (57) is below the 75 percent supplemental
indicator, suggesting that some sort of stressor might be present. The number of EPT taxa was also
slightly lower than expected (18 taxa). One possible explanation for this is the 2003 fires in the lower
Whale Creek watershed. Sampling occurred immediately after the fires, and the macroinvertebrate
population may reflect post-fire impacts. Other supporting metrics suggest that no water quality
impairments were present. The HBI score was good (2.45). Of the five most dominant taxa (Simulium,
Epeorus deceptivus, Rhithrogena, Prosimulium, and Drunella doddsi), three are very sensitive to
pollution. It was noted in the field notes and in the taxonomic analysis that this site was dominated by
86
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Flathead River Headwaters TPA
Water Quality Impairment Status
blackfly larvae (48 percent), which resulted in a decreased overall index score due to their relative
abundance and pollution tolerant characteristics. Bollman (2003b) noted that given the clustering of
blackfly larvae, a "large number can compromise the availability of substrate space for other dingers/'
Geology at this site is also significantly different from the upstream site, and is composed of glacial
outwash and alluvium as opposed to the older Belt Rocks. These factors, along with the 2003 fires, could
explain the decreased IBI score.
Overall, it appears that aquatic life at the downstream site on Whale Creek might be slightly impaired
because of natural causes. Sediment does not appear to be a cause of impairment.
Fisheries Data
Bull trout redd counts between 1980 and 1997 in Whale Creek suggest a declining trend (Weaver et al.,
2003) (Figure 3-8). Redd count declines in the early 1990s are thought to reflect the overall trend in the
North and Middle Fork Flathead River watersheds due to changes in the Flathead Lake ecosystem and
food chain (see Section 2.2.2). However, redd counts show an increasing trend from 1998 to 2002, and
indicate a recent rebound in the bull trout population. This may be partially due to the fact that bull trout
were listed as a threatened species during this time period, and harvest became illegal, or could be a
function of improving habitat/water quality conditions in this stream. Unlike the redds, juvenile bull trout
populations have fluctuated and showed no overall trend during the same time period (Figure 3-9).
250
OT-c\ico^-Lncor--ooCT>OT-c\jco^-Ln(Oh-oo o o t- cn
OOOOOOOOOOOOOOOOOOOO 0)0)0)0)0)0)0)0)0) 0)000
0)0)0)0) 0)0)0)0)0)0)0) 0)0)0)0)0)0)0)0) 0)000
Figure 3-8. Bull trout redd counts in Whale Creek.
87
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Water Quality Impairment Status
Flathead River Headwaters TPA
9
S"
CD 8
H<
o) 1 --
< n
0 i 1 i 1 1 1-1 i 1-1 i 1 1-1 i 1-1 i i *1i ui u i ui ui u i ui u i ui u i u
t-C\|CO-(D(D(D(D(DO)O)O)O)O)0>OOO
Year
Figure 3-9. Age 1 and older bull trout densities in Whale Creek.
Pfankuch Ratings
Pfankuch ratings were estimated at six locations in Whale Creek between 1976 and 2003. A summary of
the four Pfankuch indicators is provided in Table 3-16. Good to excellent mass wasting and vegetative
protection was observed in 2003. Some bank cutting and sediment deposition was also noted in 2003.
Table 3-16. Pfankuch Ratings for Segments of Whale Creek
Stream Segment
Year
Mass Wasting
Vegetative Bank
Protection
Cutting
Deposition
RM 8.8
1976
Excellent
Good
Fair/Good
Fair
RM 8.8
1979
Excellent
Good
Fair/Good
Good
RM 12.1
1976
Excellent
Good
Excellent
Excellent
RM 12.1
1979
Excellent
Excellent
Excellent
Good
RM 7.0
1994
Poor
Good
Fair
Good
Whale1-UL
2003
Good
Excellent
Fair/Good
Fair
Whale1-CS
2003
Good
Excellent
Fair/Good
Fair
Whale1-LL
2003
Good
Excellent
Fair/Good
Good
RM= river mile.
88
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Flathead River Headwaters TPA
Water Quality Impairment Status
Suspended Sediment Concentration
Suspended sediment concentration (SSC) data were collected in Whale Creek on nearly an annual basis
between 1978 and 1994 (n = 221). In general, samples were collected to capture spring runoff (in April,
May, and June) as well as base flow conditions (in July, August, September, October, and November).
However, the frequency of sampling varied from year to year.
The absence of current SSC data prohibits the use of the older data for making a current impairment
determination. However, the data are useful in evaluating long-term trends and in making historical
comparisons with other streams in the FTPA. The mean for the period of record, mean annual maximum,
and maximum reported values are presented in Table 3-17. The mean SSC concentration was below the
range for the supplemental indicator mean concentration. The mean annual maximum was similar (but
slightly higher) to the supplemental indicator value and the maximum value was higher than the
supplemental indicator value. It is expected that Whale Creek should have slightly higher sediment
concentrations because the watershed is much larger than Chepat Creek. Nonetheless, the maximum
values were exceeded.
Table 3-17. Comparison of Available SSC Data for Whale Creek with the Supplemental Indicator
Values
SSC Metric
Observed Value
(mg/L)
Indicator Value for Comparison (mg/L)
Mean (mg/L)
4.03
3.15 + 5.83
Mean Annual Maximum (mg/L)
21.29
14.56
Maximum (mg/L)
97.80
61.60
Turbidity
Turbidity data were collected in Whale Creek for roughly the same period of record as the SSC data
(1978-1994, n = 192). As with the SSC data, a lack of current data prohibits the use of the older data for
making a current impairment determination, but the data are useful in evaluating long-term and historical
trends. The mean turbidity for the period of record is 1.21 NTU and the median is 0.90 NTU. The
maximum recorded value was 17 NTU in May 1987. The average and median turbidity values are well
below the proposed target of 10 NTU during summer base flow. The turbidity data suggest that sediment
is not impairing beneficial uses in Whale Creek.
Sources
There was a 32-acre fire in the Shorty Creek watershed in 1973 and much of the lower (downstream)
watershed burned in the 2003 fires (4,802 acres, 12 percent). The large burned area from the 2003 fires
will most likely contribute natural amounts of increased sediment to Whale Creek over the next several
years.
Since 1960, clear-cut harvest occurred on approximately 4,800 acres (16 percent) of the Whale Creek
watershed (FNF, 2003). The most recent clear-cut occurred in 2000. On average, approximately 171
acres were clear-cut per year between 1960 and 2003. Clear-cut acreage was higher during the 1960s and
1970s, and has tapered off from 1980 through 2003. The calculated equivalent clear-cut acreage (ECA)
for 2004 is 14 percent, which is below the indicator value of 25 percent. Overall, clear-cut land does not
appear to be a significant source of sediment.
In 2003, the FNF identified several areas where roads are contributing sediment to Whale Creek or its
tributaries: 8 out of 84 road/stream crossings are at risk for failure, mostly on Route 589 in the Shorty
89
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Water Quality Impairment Status
Flathead River Headwaters TPA
Creek watershed (FNF, 2003); 11 closed and 10 open road miles need improved BMPs to reduce
sediment delivery, and several culverts were found to be contributing sediment; and 27 out of 44 road
miles are within 125 feet of a stream (30 miles within 300 feet). However, half the roads in the Whale
Creek watershed are closed (22 out of 44 miles), and the road density is very low (0.68 miles/square
mile).
Whale Creek Water Quality Impairment Summary
Whale Creek was listed on the 1996 and 2002 303(d) lists as impaired because of habitat alterations and
siltation. Aquatic life and cold-water fisheries were the listed impaired beneficial uses. The previous
sections reviewed the available data for making a refined impairment determination, and those data are
summarized below and in Table 3-18.
Overall, it appears that siltation is not currently impairing beneficial uses in Whale Creek. None of the
target values were exceeded. McNeil core and substrate scores were collected at one site over multiple
years, and both sets of data indicate good substrate conditions. Good substrate conditions were also noted
in the percent surface fines at two different sites. There is no indication of sediment impairment in the
macroinvertebrate data, as the number of dinger taxa was high (more than 14) at two sites in Whale
Creek. Because none of the targets were exceeded, beneficial uses in Whale Creek are not considered
impaired because of sediment or siltation.
The supplemental indicators generally support this conclusion. Macroinvertebrate data suggest that
healthy, complex systems were present at the upstream site and there was no indication of impairment
from any pollutants. An unknown stressor appears to be affecting macroinvertebrates at the downstream
site (low IBI score), but individual metrics suggest that sediment and siltation are not the cause of the
impairment. Bull trout redds declined from 1987 to 1997. However, counts have increased every year
since 1998, and the declines noted in the mid 1990s coincide with the documented changes to the bull
trout fishery connected to Flathead Lake. Although the turbidity data are old, they do not suggest water
quality impairment due to siltation. Data from the Pfankuch surveys indicated little mass wasting and
good riparian conditions were present, with some sediment deposition and bank cutting observed.
Potential sources exist throughout the watershed (fire, clear-cuts, roads); however, the ECA indicator was
not exceeded.
90
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Flathead River Headwaters TPA
Water Quality Impairment Status
Table 3-18. Comparison of Available Data with the Proposed Targets and Supplemental Indicators
for Whale Creek
Targets
Threshold
Upper Whale
Lower Whale
5-year Mean McNeil Core Percent
Subsurface Fines < 6.35 mm
35%
31.3%
5-year Mean Substrate Scores
> 10
12.2
Percent Surface Fines < 2 mm
< 20%
19%
17%
Clinger Richness
> 14
20
16
Supplemental Indicators
Recommended Value
Upper Whale
Lower Whale
Juvenile Bull Trout and Westslope
Cutthroat Trout Density
Documented increasing or stable
trend
NA (Cutthroat)
Stable (Bull)
Bull Trout Redd Counts
Documented increasing or stable
trend
Increasing Since 1998
SSC Mean
SSC Mean Annual Maximum
SSC Maximum
3.2 + 5.2 mg/L
14.6 mg/L
61.6 mg/L
4.0 mg/L
21.3 mg/L
97.8 mg/L
Pfankuch Mass Wasting Score
"good"
Good
NA
Pfankuch Bank Vegetation Score
"good"
Excellent
NA
Pfankuch Cutting Score
"good"
Fair/Good
NA
Pfankuch Deposition Score
"good"
Fair/Good
NA
Turbidity
High flow-50 NTU
instantaneous max
Summer base flow - 10 NTU
Mean -1.21
Median - 0.90
Max - 17.0
Montana Mountain Macroinvertebrate Index
of Biological Integrity
> 75%
81
57
Percentage of Clinger Taxa
"high"
70%
89%
EPT Richness
>22
20
18
Periphyton Siltation Index
<20
NA
NA
Fire
Evaluated on a case-by-case
basis
No recent fires
Year: 2003
% Burned: 12
Equivalent Clear-Cut Acres
< 25%
14%
Water Yield
< 10%
NA
Roads
Evaluated on a case-by-case
basis
Some roads in need of BMPs
91
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Water Quality Impairment Status
Flathead River Headwaters TPA
3.4.1.4 South Fork of Coal Creek
South Fork Coal Creek flows approximately 9 miles from the headwaters to the confluence with Coal
Creek, encompassing an area of 18.5 square miles. Aquatic life and cold-water fishery beneficial uses
were listed as impaired on the 1996 303(d) list. Other habitat alterations and siltation were the listed
causes of impairment. The same listing appeared on the 2002 303(d) list, as well as riparian degradation.
According to MDEQ's Data Assessment Record Sheet, the basis for the 2002 303(d) listing include
declining bull trout densities between 1989 and 1998, habitat alteration and bank erosion associated with
historical logging activities, and observed substrate fines greater than 35 percent in 2 of 10 McNeil core
samples (Phillips, 2000).
A review of the available data is presented below. The available data include suspended sediment
concentration, turbidity data, substrate scores, McNeil cores, Pfankuch ratings, pebble counts, sources
(fires, harvest, roads), macroinvertebrates, and fish population estimates.
4 2003 Biology Sampling Sites
8 2003 Physical Sampling Sites
ฆฆ Lakes
Streams
/S/ 303(d) Listed Streams
. 1 o 1 Miles
I 1 Soutti Fork Coal Creek Watershed
Figure 3-10. South Fork Coal Creek watershed.
92
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Flathead River Headwaters TPA
Water Quality Impairment Status
McNeil Core
MFWP collected McNeil core samples in South Fork Coal Creek between 1985 and 2001 (Weaver et al.,
2003). The mean value for the past 5 years is 30.2 percent fines smaller than 6.35 millimeters. In 2001,
the percent fines smaller than 6.35 millimeters was reported at 30.9 percent, and the maximum for the
past 5 years is 30.9 percent. All these values are below the proposed target.
Substrate Scores
Substrate scores were calculated based on MFWP stream surveys conducted from 1985 through 2002
(Deleray et al., 1999). The mean substrate score for the past 5 years (1998-2002) was 12.7, indicating
good juvenile bull trout rearing habitat quality (greater than 10). The mean score for the entire period of
record was 12.2.
Pebble Counts
Pebble counts were collected from one reach on the South Fork Coal Creek in 2003 (at three sites within
each reach). The percent surface fines smaller than 2 millimeters were 12.6 percent (upper), 11.3 percent
(cross section), and 4.7 percent (lower). All three figures are lower than the proposed target of 20
percent. The data suggest that siltation is not impairing beneficial uses at this site.
Macroinvertebrates
One macroinvertebrate sample was collected in the South Fork Coal Creek in August 2003. Clinger data
(19 taxa, 66 percent of the sample) suggest that sediment was not a cause of impairment at this site. The
Mountain IBI was 87, which indicates that aquatic life beneficial uses were fully supported. However,
the number of EPT taxa (21) was slightly below the recommended value of 22.
Other supporting macroinvertebrate metrics also suggest that no water quality impairments were present.
The HBI score was 2.25, which is lower than the recommended value of 3.5. All of the five most
dominant taxa (Drunella doddsi, Baetis tricaudatus, Rhithrogena, Epeorus grandis, and Epeorus
deceptivus), are sensitive to pollution. Overall, the data suggest that aquatic life beneficial uses were fully
supported.
Fisheries Data
MFWP conducted electrofishing surveys from 1985 through 2002 (Deleray et al., 1999). Densities of
bull trout 1 year and older have fluctuated throughout the period of record, ranging from a high of 5.91
per 100 square meters in 1985 to a low of 0.16 per 100 square meters in 1998 (Figure 3-11). Like other
Flathead River headwater streams, bull trout densities were lowest during the mid 1990s, and have
generally been increasing since 1998. During the same period, the more resident westslope cutthroat
populations showed a relatively similar trend in densities of fish 1 year and older. Bull trout redd counts
were conducted in 1980, 1981, 1982, 1986, 1991, 1992, 1997, and 2000. Redd counts show a declining
trend from a high of 24 in 1981 to 1 in 2000. It is not known whether the redd count declines reflect the
overall trend in the North and Middle Fork Flathead River watersheds due to changes in the Flathead
Lake ecosystem and food chain, or are a result of factors within the South Fork Coal Creek watershed.
93
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Water Quality Impairment Status
Flathead River Headwaters TPA
!2
o
+ฆป
o
E
a
ns
3
O"
(/>
o
o
C# <$> c# c# c# c# c# # #
Year
Figure 3-11. Age 1 and older bull trout and Westslope cutthroat trout densities in South Fork
Coal Creek.
Pfankuch Ratings
Pfankuch ratings were estimated at several sites in the South Fork Coal Creek between 1976 and 2003. A
summary of the findings is shown in Table 3-19. Recent data (collected in 2003) suggests that vegetative
bank protection and sediment deposition were good or better at all sites surveyed. Some sites were
ranked "fair" for bank cutting or mass wasting, but there was no indication as to the cause of the fair
ratings. Historic data (1976 to 1985) indicates that conditions may have been worse in the past, having
more fair or poor ratings, especially in the 1985 survey.
94
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Flathead River Headwaters TPA
Water Quality Impairment Status
Table 3-19. Pfankuch Ratings for Segments of South Fork Coal Creek
Stream Segment
Year
Mass Wasting
Vegetative Bank
Protection
Cutting
Deposition
RM 1.0
1976
Good
Good
Good
Excellent/Good
RM 4.2
1976
Good
Good
Good
Excellent
RM 7.2
1976
Excellent
Good
Excellent
Excellent
RM 4.2
1979
Excellent
Excellent
Excellent
Good
RM 0.3
1985
Poor
Fair
Fair/Poor
Fair
RM 1.1
1985
Good
Good
Good
Excellent/Good
RM 1.5
1985
Good
Good
Good/Fair
Good
RM 2.3
1985
Good
Good
Fair/Good
Good
RM 3.0
1985
Fair
Fair
Poor
Fair/Poor
RM 3.2
1985
Good/Fair
Fair
Good/Fair
Good
RM 4.0
1985
Fair
Fair
Fair/Good
Fair
RM 5.2
1985
Poor
Poor
Good/Fair
Poor
RM 6.8
1985
Fair
Fair
Good/Fair
Excellent/Good
Profile #1 LL
2003
Excellent
Excellent
Good/Fair
Excellent
Profile #1 CS
2003
Excellent
Excellent
Excellent
Excellent
Profile #1 UL
2003
Excellent
Excellent
Excellent
Good
Profile #2 LL
2003
Fair
Good
Fair
Good
Profile #2 CS
2003
Excellent
Good
Fair
Good
Profile #2 UL
2003
Good
Excellent
Good/Fair
Excellent
Mathias Creek
1976
Excellent
Good
Good
Excellent
RM= river mile.
Suspended Sediment Concentration
Suspended sediment concentration (SSC) data were collected in the South Fork Coal Creek almost yearly
between 1983 and 1995 (n = 190). In general, samples were collected to capture spring runoff (in April,
May, and June) as well as base flow conditions (in July, August, September, October, and November).
However, the frequency of sampling varied from year to year.
The absence of current SSC data prohibits the use of these data for making a current impairment
determination. However, the data are useful in evaluating long-term trends and in making historical
comparisons with other streams in the FTPA. The mean for the period of record, mean annual
maximum, and maximum reported values are presented in Table 3-20. All values are below the proposed
indicator values, indicating that suspended sediment was not likely contributing to sediment impairment
in South Fork Coal Creek prior to the end of the period of record in 1995.
Table 3-20. Comparison of Available SSC Data for South Fork Coal Creek with the Supplemental
Indicator Values
SSC Metric
Observed Value (mg/L)
Indicator Value for Comparison (mg/L)
Mean (mg/L)
2.83
3.15 + 5.83
Mean Annual Maximum (mg/L)
10.8
14.56
Maximum (mg/L)
31.2
61.60
95
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Water Quality Impairment Status
Flathead River Headwaters TPA
Turbidity
Turbidity data were collected in South Fork Coal Creek for roughly the same period of record as for the
SSC data (1983-1995, n = 190). As with the SSC data, a lack of current data prohibits the use of the
older data for making a current impairment determination, but the data are useful in evaluating long-term
and historical trends.
The mean turbidity for the period of record is 1.06 NTU and the median is 0.80 NTU. The maximum
recorded value was 15 NTU in May 1984. The average and median turbidity values are well below the
proposed summer base flow target of 10 NTU. The turbidity data suggest that sediment was not
impairing beneficial uses in the South Fork Coal Creek during the period of record. More current
information is not available.
Sources
There have been no recent fires in the South Fork of Coal Creek. The last recorded major fire occurred in
1910, when 893 acres burned.
Since 1955, 743 acres (6 percent) have been clear-cut in the South Fork watershed, and no clear-cutting
has occurred since 1991. The calculated equivalent clear-cut acreage for 2004 is 4.3 percent, which is
below the proposed indicator of 25 percent. An analysis by the Montana DNRC indicated that water
yields are only 2.5 percent greater than naturally occurring yields (Nelson, personal communication
March 11, 2004). Overall, harvested land does not appear to be a significant source of sediment.
Road density in the South Fork Coal Creek watershed is very low (0.82 miles/square mile), and almost all
of the roads are closed yearlong. The FNF survey found that several road-stream crossings are at risk of
failure, and several miles of roads are in need of BMPs. MFWP also identified several potential sources
of sediment in the South Fork watershed. Skid trails and heavy equipment operation have caused
increased erosion in the Mathias Creek watershed (MFWP, 2004), and portions of the South Fork have
been straightened and channelized from past logging activities. Overall, it appears that some sediment
from anthropogenic sources is reaching the South Fork of Coal Creek.
South Fork Coal Creek Water Quality Impairment Summary
The South Fork of Coal Creek was listed on the 1996 and 2002 303(d) lists as impaired because of
siltation and habitat alterations. Riparian degradation was also a listed impairment on the 2002 303(d)
list. Aquatic life and fishery beneficial uses were listed as impaired. A summary of the available data is
presented below and in Table 3-21.
It appears that siltation is not currently impairing beneficial uses in the South Fork of Coal Creek. None
of the target values were exceeded. McNeil core and substrate scores were collected at one site over
multiple years, and both sets of data indicate good substrate conditions. Good substrate conditions were
also noted in the percent surface fines at three different sites. There was no indication of sediment
impairment in the macroinvertebrate data, as the number of dinger taxa was high (more than 14).
Because none of the targets were exceeded, beneficial uses in the South Fork of Coal Creek are not
considered impaired because of sediment or siltation.
Supplemental indicators generally support this conclusion. Macroinvertebrate data suggest that healthy,
complex systems were present with no indication of impairment from any pollutants (high IBI score).
The available fisheries data suggest that the bull trout population declined in the mid 1990s and then
showed an improving trend starting in 1998. Although the SSC and turbidity data are old, they do not
suggest water quality impairment due to siltation. Surveys found that there are several road and road-
stream crossings potentially contributing sediment to the stream; however, there is no evidence of stream
96
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Flathead River Headwaters TPA
Water Quality Impairment Status
impairment. Clear-cut land is most likely not a major source of sediment, because only a small
percentage of the watershed has historically been clear-cut, and none since 1991. The ECA and water
yield supplemental indicators suggest no impairment from clear-cut areas.
Table 3-21. Comparison of Available Data to the Proposed Targets and Supplemental Indicators for
South Fork Coal Creek.
Targets
Threshold
Available Data
5-year Mean McNeil Core Percent Subsurface
Fines < 6.35 mm
35%
30.2%
5-year Mean Substrate Scores
> 10
12.7
Percent Surface Fines < 2 mm
< 20%
9.54%
Clinger Richness
> 14
19
Supplemental Indicators
Recommended Value
Available Data
Juvenile Bull Trout and Westslope Cutthroat
Trout Density
Documented increasing or
stable trend
Increasing Since 1998
(Cutthroat)
Increasing Since 1998 (Bull)
Bull Trout Redd Counts
Documented increasing or
stable trend
Decline
SSC Mean
SSC Mean Annual Maximum
SSC Maximum
3.2 + 5.2 mg/L
14.6 mg/L
61.6 mg/L
2.83 mg/L
10.8 mg/L
31.2 mg/L
Pfankuch Mass Wasting Score
"good"
Excellent
Pfankuch Bank Vegetation Score
"good"
Excellent
Pfankuch Cutting Score
"good"
Good
Pfankuch Deposition Score
"good"
Good
Turbidity
High Flow-50 NTU
instantaneous maximum
Summer base flow - 10 NTU
Mean-1.1 NTU
Median -0.8 NTU
Max - 15 NTU
Montana Mountain Macroinvertebrate Index of
Biological Integrity
> 75%
87%
Percentage of Clinger Taxa
"high"
66%
EPT Richness
>22
21
Periphyton Siltation Index
<20
NA
Fire
Evaluated on a case-by-case
basis
No recent fires
Equivalent Clear-Cut Acres
< 25%
4%
Water Yield
< 10%
2.5%
Roads
Evaluated on a case-by-case
basis
Some roads in need of
BMPs
97
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Water Quality Impairment Status
Flathead River Headwaters TPA
3.4.1.5 North Fork Coal Creek: Siitation
The North Fork Coal Creek watershed covers approximately 23.2 square miles (14,895 acres), all of
which is in the FNF. It was listed on the 1996 303(d) list as impaired because of siitation and nutrients.
The basis for the 1996 listing is unknown. Cold-water fishery and aquatic life beneficial uses were listed
on the 2002 303(d) list as impaired as a result of siitation. Nutrients were not listed as a cause of
impairment on the 2002 303(d) list. According to MDEQ's Data Assessment Record, a significant
decline in bull trout since 1990, along with indications of sedimentation problems in the watershed, is the
primary basis for the 2002 303(d) listing (Suplee, 1999a).
A review of the available sediment and siitation data is provided below. Available data include
suspended sediment concentration, turbidity data, substrate scores, McNeil cores, Pfankuch ratings,
pebble counts, sources (fires, harvest, roads), macroinvertebrates, and fish population estimates. Nutrient
data are discussed in Section 3.4.1.6.
t
ฉ 2003 Physical Sites
A 2003 Biology Sites
Roads
303(d) Listed Streams
Lakes
Streams
North Fork Coal Creek Watershed
Figure 3-12. North Fork Coal Creek watershed.
98
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Flathead River Headwaters TPA
Water Quality Impairment Status
McNeil Core
MFWP collected McNeil core samples in the North Fork between 1985 and 2001 (Weaver et al., 2003).
The mean value for the past 5 years in the North Fork was 31.0, indicating good substrate conditions.
The maximum value for the past 5 years was 31.8.
Substrate Scores
Substrate scores were calculated for the North Fork Coal Creek based on MFWP stream surveys
conducted from 1984 through 2002 (Deleray et al., 1999). The mean substrate score for 1998 through
2002 was 13.7. This score indicates good juvenile bull trout rearing habitat quality. Over the entire
period of record, the mean substrate score was 13.3.
Pebble Counts
Pebble counts were collected from two reaches on the North Fork Coal Creek in 2003. The percent
surface fines smaller than 2 millimeters at the upper reach were 7.9 percent (lower), 9.4 percent (cross
section), and 2.8 percent (upper). At the lower North Fork reach, the percent surface fines smaller than 2
millimeters were 14.4 percent (lower), 7.6 percent (cross section), and 19.3 percent (upper). All values
were below the supplemental indicator of 20 percent.
Macroin vertebrates
Macroinvertebrate data were collected at one site on the North Fork of Coal Creek in August 2003
(Figure 3-12). There was no indication of water quality impairment at this site. The number of dinger
taxa was high (25 taxa, 80 percent), which indicates no impact on the macroinvertebrate community from
siltation. Both the number of EPT taxa (27) and Mountain IBI (90 percent) were above the recommended
supplemental indicators. The HBI score was 2.18 (i.e., no apparent nutrient or sediment influences). All
five of the most dominant taxa are intolerant to pollution (Rhithrogena, Heterlimnius Epeorus grandis,,
Epeorus deceptivus, and Parapsyche elsis). The entire suite of macroinvertebrate metrics suggests that
aquatic life beneficial uses are not impaired because of siltation in the North Fork of Coal Creek.
Fish Population
MFWP conducted electrofishing surveys between 1982 and 2002 in North Fork Coal Creek (Deleray et
al., 2003). Densities of bull trout 1 year old or more have declined from a high of 4.9 per 100 square
meters in 1989 to 0.08 per 100 square meters in 1997 (Figure 3-13). The numbers have remained low
since 1997. During the same period, westslope cutthroat populations appeared to have an increasing trend.
This indicates that the cause of the declining bull trout population is not similarly affecting the westslope
cutthroat trout population. No redd data were available for North Fork Coal Creek. Declines in the bull
trout population may be due to changes in the Flathead Lake ecosystem, and do not necessarily indicate
beneficial use impairment (see Section 2.2.2).
99
-------
Water Quality Impairment Status
Flathead River Headwaters TPA
oCl/
&
& r& r# cฎ
&
K\
JP c# q#
K5 Ip3 ^
Year
Figure 3-13. Age 1 and older bull trout and Westslope cutthroat trout densities in North Fork
Coal Creek.
Pfankuch Ratings
Pfankuch ratings were estimated at several sites in the North Fork Coal Creek watershed between 1976
and 2003. A summary of the findings is shown in Table 3-22. The most recent samples (2003) show few
problems relating to mass wasting, vegetative bank protection, and deposition. However, significant bank
cutting (fair/good rating) was observed at several sites.
Suspended Sediment Concentration
Suspended sediment concentration (SSC) data were collected in the North Fork Coal Creek almost yearly
between 1982 and 1995 (n = 215). In general, samples were collected to capture spring runoff (in April,
May, and June) as well as base flow conditions (in July, August, September, October, and November).
However, the frequency of sampling varied from year to year.
The absence of current SSC data prohibits the use of the older data for making a current impairment
determination. However, the data are useful in evaluating long-term trends and in making historical
comparisons with other streams in the TPA. The mean for the period of record, mean annual maximum,
mean annual load, and maximum reported values are presented in Table 3-23. All three values were
within an acceptable range of the reference data. The data suggest that sediment concentrations in the
North Fork Coal Creek were generally similar to reference conditions during the period of record. More
current information is unavailable.
100
-------
Flathead River Headwaters TPA
Water Quality Impairment Status
Table 3-22. Pfankuch Ratings for Segments of North Fork Coal Creek
Stream Segment
Year
Mass Wasting
Vegetative Bank
Protection
Cutting
Deposition
RM 12.18
1976
Excellent
Good
Good
Excellent
RM 16.19
1976
Good
Good
Fair/Good
Good/Excellent
RM 18.57
1976
Good
Good
Good
Excellent
RM 20.22
1976
Excellent
Excellent
Fair/Good
Good/Excellent
RM 12.18
1979
Excellent
Fair
Fair/Good
Excellent
RM 16.19
1979
Excellent
Fair
Fair/Good
Good
RM 18.57
1979
Excellent
Excellent
Excellent
Excellent
RM 20.22
1979
Excellent
Good
Fair/Good
Good
RM 9.47
1985
Good
Good
Fair/Good
Good
RM 9.72
1985
Poor
Fair
Poor
Good/Fair
RM 9.95
1985
Poor
Fair
Poor
Fair
RM 10.26
1985
Poor
Good
Fair
Good
RM 10.42
1985
Fair/Poor
Fair
Fair
Good/Fair
RM 10.91
1985
Poor
Poor
Fair/Good
Poor
RM 11.69
1985
Poor
Good
Fair
Fair
RM 12.84
1985
Good
Fair
Fair/Good
Good
RM 15.11
1985
Fair
Poor
Fair/Poor
Fair
Profile #1 UL
2003
Good
Good
Fair/Good
Fair
Profile #1 CS
2003
Good
Excellent
Fair/Good
Good
Profile #1 LL
2003
Excellent
Good
Fair/Good
Good
Profile #2 UL
2003
Fair
Good
Fair
Good
Profile #2 CS
2003
Excellent
Excellent
Excellent
Excellent
Profile #2 LL
2003
Good
Excellent
Fair
Good
RM = river mile.
Table 3-23. Comparison of Available SSC Data for North Fork Coal Creek with the Supplemental
Indicators.
SSC Metric
Observed Value (mg/L)
Indicator Value for Comparison (mg/L)
Mean (mg/L)
3 73
3.15 + 5.83
Mean Annual Maximum (mg/L)
19.56
14.56
Maximum (mg/L)
40.60
61.60
Turbidity
Turbidity data were collected in the North Fork for roughly the same period of record as for the SSC data
(1982-1995, n = 213). As with the SSC data, a lack of current data prohibits the use of the older data for
making a current impairment determination, but the data are useful in evaluating long-term and historical
trends.
The mean turbidity for the period of record is 1.17 NTU and the median is 0.85 NTU. The maximum
recorded value was 8 NTU in May 1984. None of the values exceed the proposed target of 10 NTU
during summer base flow. The data suggest that sediment was not impairing beneficial uses during the
period of record. More current data are not available.
101
-------
Water Quality Impairment Status
Flathead River Headwaters TPA
Sources
There have been few recent fires in the North Fork watershed. One fire occurred in 1988, burning
approximately 100 acres, and another fire occurred in 1970, burning approximately 160 acres. No fires
have occurred in the North Fork since 1988.
Since 1960, 822 acres of land have been clear-cut (6 percent of the total watershed). The last clear-cut
occurred in 1990, when 125 acres were cut. The ECA for the watershed was 6.7, which indicates that
harvested land is not likely a major source of sediment. The percent water yield increase was also low
(3.2 percent). Some riparian harvests have occurred historically, and MFWP noted that this activity has
caused increased bank erosion in the stream (MFWP, 2004). No streamside management zone was
created at the time of the riparian harvests.
The FNF survey found that several roads in the North Fork of Coal Creek (Roads 5270 and 5278) have
plugged culverts, sediment slumps, and actively eroding surfaces. Road density is relatively high in the
North Fork of Coal Creek compared to other watersheds in the planning area (1.6 miles per square mile)
(see Section 2.1.11). Within the entire Coal Creek watershed, the survey indicated that some heavily
traveled roads require ditch drainage improvements, and approximately 17 miles of bermed, closed roads
need additional BMPs. (FNF, 2003).
North Fork Coal Creek Water Quality Impairment Summary: Sediment/Siltation
The North Fork of Coal Creek was listed on the 1996 and 2002 303(d) lists as having impaired aquatic
life and fishery beneficial uses. The causes of impairment listed in 1996 were siltation and nutrients. A
summary of the sediment related data is presented below and in Table 3-24. Nutrient impairments are
discussed in Section 3.4.1.6.
It appears that siltation is not currently impairing beneficial uses in the North Fork of Coal Creek. None
of the target values were exceeded. McNeil core and substrate scores were collected at one site over
multiple years, and both sets of data indicate good substrate conditions. Good substrate conditions were
also noted in the percent surface fines at two different sites. There is no indication of sediment
impairment in the macroinvertebrate data: the number of dinger taxa was high (greater than 14). Because
none of the targets were exceeded, beneficial uses in the North Fork of Coal Creek are not impaired
because of sediment or siltation.
Supplemental indicators generally supported this conclusion. Macroinvertebrate data suggest that
healthy, complex systems were present at the upstream site and there is no indication of impairment from
any pollutants (high IBI score). Westslope cutthroat trout densities appear to be increasing over the
period of record, and turbidity and SSC historically do not suggest sediment impairments. Pfankuch
surveys found good physical stream conditions, and road density, ECA, and water yield were low (good).
Although data indicate that bull trout populations are declining in North Fork Coal Creek, the cause of the
decline is unknown, and the cause of impairment does not appear to be similarly affecting the westslope
cutthroat trout population. Some potential road sources of sediment were identified in the watershed;
however, there does not appear to be an effect on beneficial uses.
102
-------
Flathead River Headwaters TPA
Water Quality Impairment Status
Table 3-24. Comparison of Available Data with the Proposed Targets and Supplemental Indicators
for North Fork Coal Creek (Sediment)
Targets
Threshold
Available Data
5-year Mean McNeil Core Percent Subsurface Fines <
6.35 mm
35%
31.0%
5-year Mean Substrate Scores
> 10
13.7
Percent Surface Fines < 2 mm
< 20%
6.7% and 13.7%
Clinger Richness
> 14
25
Supplemental Indicators
Recommended Value
Available Data
Juvenile Bull Trout and Westslope Cutthroat Trout
Density
Documented increasing or stable
trend
Cutthroat: increasing
Bull: decline
Bull Trout Redd Counts
Documented increasing or stable
trend
NA
SSC Mean
SSC Mean Annual Maximum
SSC Maximum
3.2 ฑ 5.2 mg/L
14.6 mg/L
61.6 mg/L
3.7 mg/L
19.6 mg/L
40.6 mg/L
Turbidity
High flow-50 NTU instantaneous
maximum
Summer base flow - 10 NTU
Mean: 1.17 NTU
Median: 0.85 NTU
Maximum: 8.0 NTU
Pfankuch Mass Wasting Score
"good"
Good
Pfankuch Bank Vegetation Score
"good"
Good
Pfankuch Cutting Score
"good"
Fair/Good
Pfankuch Deposition Score
"good"
Good
Montana Mountain Macroinvertebrate Index of
Biological Integrity
> 75%
90
Percentage of Clinger Taxa
"high"
80%
EPT Richness
>22
27
Periphyton Siltation Index
< 20
NA
Fire
Evaluated on a case-by-case basis
Year: 1988
Acres: 96
Equivalent Clear-Cut Acres
< 25%
6.7%
Water Yield
< 10%
3.2%
Roads
Evaluated on a case-by-case basis
Some roads in need of
BMPs
103
-------
Water Quality Impairment Status
Flathead River Headwaters TPA
3.4.1.6 North Fork Coal Creek: Nutrients
As stated previously, the North Fork Coal Creek also appeared on the 1996 303(d) list for nutrients. A
general watershed overview of the North Fork Coal Creek watershed is presented in Section 3.4.1.5. A
review of the available nutrient data is provided below. The available data include nutrient
concentrations, dissolved oxygen concentrations, macroinvertebrates, and sources (fires, harvest, roads).
Nutrient Concentrations
Nutrient data were collected at one site in the North Fork Coal Creek between 1982 and 1987. The
frequency of sampling and type of parameters sampled varied from year to year. The absence of current
data limits the use in making a current impairment determination. However, the data are useful for
evaluating historical trends. Table 3-25 shows that phosphorus concentrations were below the proposed
indicator, however, some nitrate (and nitrate/nitrate) concentrations exceeded the proposed indicators. It
should be noted that nutrient concentrations could reflect inaccuracies in data collection and analysis, as
field and laboratory methods have significantly improved since 1987.
A study conducted by Hauer and Hill (1997) found that total phosphorus (TP) loads in lower Coal Creek
were higher than loads in similarly sized watersheds; however, there was no indication that loads were
impairing beneficial uses. The maximum TP concentration in the North Fork Coal Creek over a 2-year
period (1994-1995) was 0.014 mg/L, which is slightly above the target. However, the age of the data
limits their use in making impairment determinations.
Table 3-25. Nutrient Data and Comparison with the Targets
Parameter
Count
Mean (mg/L)
Median (mg/L)
Max (mg/L)
Target (mg/L)
Nitrate
9
0.06
0.05
0.19
NA
Nitrite
1
0.0002
0.0002
0.0002
NA
Nitrate + Nitrite
1
0.031
0.031
0.031
0.014
Total Nitrogen
NA
NA
NA
NA
0.12
Total Phosphorus
3
0.0047
0.004
0.0067
0.01
Benthic Algae
No data have been collected.
Macroin vertebrates
Macroinvertebrate data were collected at one site on the North Fork of Coal Creek in August 2003. The
HBI score was 2.18, indicating no apparent impairment from nutrients. Also, the Mountain IBI score was
very high (90 percent), which indicates that there were no overall impairments present in the North Fork
of Coal Creek.
104
-------
Flathead River Headwaters TPA
Water Quality Impairment Status
Dissolved Oxygen
Dissolved oxygen data were collected at one site on the North Fork Coal Creek between 1982 and 1987
(n = 84). The mean concentration over the time period was 10.3, which is above the target of 9.5, and
suggests the nutrients were not impairing aquatic life or fish communities. The minimum concentration
was 8.0, which also suggests that dissolved oxygen concentrations were not impairing beneficial uses.
Sources
There have been few recent fires in the North Fork watershed. One fire occurred in 1988, burning
approximately 100 acres, and another fire occurred in 1970, burning approximately 160 acres. No fires
have occurred in the North Fork since 1988. Since 1960, 822 acres of land have been clear-cut (6 percent
of the total watershed). The last clear-cut occurred in 1990, when 125 acres were cut. The ECA for the
watershed was 6.7, which indicates that harvested land is not a major source of sediment. The percent
water yield increase was also low (3.2 percent). Overall, it does not appear that fire, increased water
yield, or increased sediment loading has significantly contributed to nutrient impairments in the North
Fork of Coal Creek.
No other potential sources of nutrients have been identified in the North Fork Coal Creek watershed.
Aside from roads, there is no development, and no potential for nutrient loadings related to human
activities (such as wastewater systems, agriculture, fertilizers). Moreover, streams in heavily forested
mountain systems in northwestern Montana tend to be nutrient poor, as most nutrients are tied up in
organic matter and forest litter.
North Fork Coal Creek Water Quality Impairment Summary: Nutrients
The North Fork of Coal Creek was listed on the 1996 303(d) list as having impaired aquatic life and cold-
water fishery beneficial uses. The causes of impairment were siltation and nutrients. A summary of the
nutrient data is presented below and in Table 3-26.
In light of available data, it does not appear that nutrients are impairing beneficial uses in the North Fork
of Coal Creek. Macroinvertebrate data indicate that excellent aquatic life communities are present (high
IBI score) with no indication of nutrient impairment (low HBI score). Also, westslope cutthroat trout
densities are high and increasing, indicating that no water quality impairments are present. None of the
recent biological data indicate impairments of any kind in the North Fork of Coal Creek. Also, there are
virtually no anthropogenic sources of nutrients (such as wastewater treatment, agriculture, fertilizers) in
the watershed. The ECA and water yield for the watershed is low, and suggest that fires and clear-cuts
have not impaired beneficial uses.
The overall lack of sources, combined with the excellent recent data on macroinvertebrate communities,
suggests that the North Fork of Coal Creek is not impaired because of nutrients. However, additional data
are necessary to verify this conclusion (refer to Section 4.4 for details regarding proposed monitoring).
105
-------
Water Quality Impairment Status
Flathead River Headwaters TPA
Table 3-26. Comparison of Available Data with the Proposed Targets and Supplemental Indicators
for North Fork Coal Creek (Nutrients)
Targets
Threshold
Available Data
Benthic Algae (Median)
< 33 mg/m2
NA
EPA Ecoregion II, Total Phosphorus (Median)
< 0.01 mg/L
0.004
(No recent data)
EPA Ecoregion II, TKN (Median)
< 0.05 mg/L
NA
EPA Ecoregion II, Nitrate+Nitrite (NO2/NO3) (Median)
< 0.014 mg/L
0.031
(No recent data)
EPA Ecoregion II, Total Nitrogen (Median)
<0.12 mg/L
NA
Supplemental Indicators
Recommended Value
Available Data
Macroinvertebrate Hilsenhoff Biotic Index (HBI)
< 3.5
2.18
EPA Ecoregion II, Chlorophyll- a, Water Column
(Median)
< 1.08
NA
Dissolved Oxygen, 7-Day Mean
> 9.5
10.3
(No recent data)
Dissolved Oxygen, 1-Day Minimum
> 8.0
8.0
(No recent data)
Fire
Evaluated on a case-by-case basis
Year: 1988
Acres: 96
Equivalent Clear-Cut Acres
< 25%
6.7%
Water Yield
< 10%
3.2%
106
-------
Flathead River Headwaters TPA
Water Quality Impairment Status
3.4.1.7 Lower Coal Creek
Coal Creek is a third-order tributary of the North Fork Flathead River flowing 18 miles from the
headwaters to the mouth (Figure 3-14). The total watershed area covers approximately 82 square miles.
Primary tributaries include South Fork Coal Creek, Deadhorse Creek, and Cyclone Creek. The reach
downstream of the confluence with the North and South Forks is referred to as "Lower Coal Creek," and
will be referred to as such herein. Most of Lower Coal Creek flows through the Coal Creek State Forest.
Cold-water fishery and aquatic life beneficial uses in Lower Coal Creek were listed on both the 1996 and
2002 303(d) lists as impaired because of siltation. No information is available regarding the basis for the
1996 listing of Lower Coal Creek. According to MDEQ"s Data Assessment Record, sedimentation,
embeddedness, bank erosion, and logging activities are the primary basis for the 2002 303(d) listing
(Suplee, 1999b).
A review of the available data is provided below. The available data include substrate scores, McNeil
cores, Pfankuch ratings, pebble counts, sources (fires, harvests, roads), macroinvertebrates, and fish
population estimates.
2003 Physical Sites
2093 Biology Sites
Towns
Roads
'Lower Coal Creek
'303(d) Listed Stream*
Lakes
Streams
Coal Creek Watershed
107
-------
Water Quality Impairment Status
Flathead River Headwaters TPA
McNeil Core
MFWP collected McNeil core samples in the lower segment of Coal Creek between 1981 and 2001
(Weaver et al., 2003). A summary of the data is presented in Figure 3-15. The mean McNeil core value
for the past 5 years in Lower Coal Creek is 37.1 percent fines smaller than 6.35 millimeters. In 2001, the
percent fines smaller than 6.35 millimeters was reported to be 37.6 percent, and the maximum for the past
5 years was 37.6 percent.
Bull trout redd counts and densities were relatively high throughout the 1980s and early 1990s (see the
subsection below on fish population and Figure 3-16). During this period, McNeil core values regularly
exceeded the target value, with a maximum McNeil core value of 42.1 occurring in 1990 (Figure 3-16).
This information suggests that functional bull trout populations existed in Lower Coal Creek with McNeil
core values as high as 42.1. Furthermore, there does not appear to be a visible trend in the McNeil core
data over time, or a correlation between bull trout redd counts and the McNeil core values (Figure 3-16).
The only visible trend is the fact that the year-to-year variability in McNeil cores has decreased since
1995 (Figure 3-15). This, however, is not unique to Lower Coal Creek. As shown in Figure 3-17, the
year-to-year variability in many of the tributaries within the Flathead Headwaters has decreased similarly.
Unlike Lower Coal Creek, however, in these other tributaries have seen their bull trout redd counts
increase in recent years.
Although the mean McNeil cores exceed the target, there is no definitive indication that high percentages
of subsurface fines are impairing bull trout populations in Lower Coal Creek or that the high values are
necessarily a result of human activities. The extent to which the minor (+2.1 percent) exceedance of this
threshold value is or was the cause of bull trout impairment is unknown.
44.0
o
O
42.0 -
lo 40.0
CO
CD
V
CO
-------
Flathead River Headwaters TPA
Water Quality Impairment Status
70
o
T
CM
CO
"3"
CD
h-
00
O)
o
T
CM
CO
"3"
CD
00
O)
o
T
CM
00
00
00
00
00
00
00
00
00
00
O)
O)
O)
O)
O)
O)
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O)
O)
o
o
o
T-
T-
T-
T-
T-
T-
T-
T-
T-
CM
CM
CM
Figure 3-16. McNeil core and bull trout redd count trends in Lower Coal Creek.
50.0
45.0 -
X~"
E
E
w
\
\ '*
40.0 - f -
J '! <
- -
Main Stem Coal
m -
North Fork Coal
South Fork Coal
X -
Whale
-
*-
Granite
- -
Challenge
S 35-ฐ
Q)
O
O
'q)
? 30.0
3fc* ~ - * * -
Uซ. ฆ -V' X... *
25.0 -
20.0
T-(NC0^-L0(DI^000)O^-(NC0^-in(DI^00a)O^-
OOOOOOOOOOOOCOCOOO 0)0)0)0)0)0)0)0)0)0)00
0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)00
Figure 3-17. McNeil core values at six sites in the Flathead River Headwaters TPA.
109
-------
Water Quality Impairment Status
Flathead River Headwaters TPA
Substrate Scores
Substrate scores were calculated for Lower Coal Creek based on MFWP stream surveys conducted in
1984 through 2002 (Deleray et al., 1999). The 5-year mean substrate score was 9.9, which is slightly
lower than the target. The mean value for the entire period of record was 10.4. Overall, the 5-year mean
substrate score is only slightly lower than the target, which itself is a conservative indicator that suggests
that a threatened condition might be present.
Pebble Counts
Pebble counts were collected from two reaches on Lower Coal Creek. All of the pebble counts on the
lower segments of Coal Creek slightly exceeded the proposed target of 20 percent. At the upstream
reach, the percent surface fines smaller than 2 millimeters were 22.1 percent (upper), 20.2 percent (cross
section), and 22.9 percent (lower). One pebble count was performed on the lower site (22.9 percent).
Although the 20 percent threshold is exceeded at several sites, the exceedance is minor, and the 20
percent target is a conservative value that suggests that a threatened condition might be present. Other
studies suggest that a percent surface fines indicator of 30 percent is more appropriate for making
sediment impairment decisions.
Macroin vertebrates
Macroinvertebrate data were collected at two sites on Lower Coal Creek in August 2003 (Figure 3-14).
The data are summarized below.
Lower Coal Creek at Deadhorse Creek (Upstream)
Macroinvertebrates at the upstream Lower Coal Creek site were similar to those on the North Fork site.
EPT taxa (23), dinger taxa (23), and dinger percent (71 percent) were all high, indicating good water
quality with no evidence of siltation. The Mountain IBI score was very high (90 percent) and did not
indicate any water quality impairments. The HBI score was 2.64 (i.e., no apparent nutrient or sediment
influences). All five of the most dominant taxa (Epeorus deceptivus, Baetis tricaudatus, Heterlimnius,
Cinygmula, Eclipidrilus) are intolerant to pollution. The entire suite of macroinvertebrate metrics
suggests that aquatic life beneficial uses are not impaired because of siltation at the Deadhorse Creek site.
Lower Coal Creek at North Fork Road near the Mouth (Downstream)
Data from the downstream Lower Coal Creek site indicate that aquatic life was not impaired because of
sediment. The number of dinger taxa (16) and percentage of dingers (83 percent) were both high,
indicating good water quality with no evidence of siltation. The Montana Mountain IBI score was 86
percent, which is considered fully supporting aquatic life beneficial uses. One tolerant taxon was found
(0.6 percent of the total sample), but this alone does not suggest a water quality impairment. The number
of EPT taxa (19) was slightly lower than the recommended value. The HBI score was 2.79 (i.e., no
apparent nutrient or sediment influences). All five of the most dominant taxa (Glossosoma, Drunella
doddsi, Simulium, Epeorus deceptivus, Baetis tricaudatus) are intolerant to pollution. Overall, the
macroinvertebrate data do not suggest a water quality impairment because of siltation.
110
-------
Flathead River Headwaters TPA
Water Quality Impairment Status
Fish Population
Historically, the Coal Creek watershed supported one of the most productive bull trout populations in the
Flathead River watershed. MFWP conducted electrofishing surveys from 1982 through 2002 in Lower
Coal Creek (Deleray et al., 1999). Densities of bull trout 1 year old and older have declined throughout
the period of record (Figure 3-18). Bull trout redd counts have also declined over the same period of
record (Figure 3-19). It is not known whether the bull trout declines reflect the overall trend in the North
and Middle Fork Flathead River watersheds due to changes to the Flathead Lake ecosystem and food
chain, or are a result of conditions within the Coal Creek watershed.
2 8
0
1 ^
S 6
D
cr c
t/> o
o
o
3
o
DO
4
3
2
1 -HI
.,n,^,n,n,n,ll,n
CM
CO
LO
CD
r-~
00
CD
O
T
CM
CO
LO
CD
r-~
00
CD
O
T
CM
00
00
00
00
00
00
00
00
CD
CD
CD
CD
CD
CD
CD
CD
CD
CD
o
o
O
G)
CD
CD
CD
CD
CD
CD
CD
CD
CD
CD
CD
CD
CD
CD
CD
CD
CD
o
o
O
CM
CM
CM
Year
Figure 3-18. Age 1 and older bull trout densities in Lower Coal Creek.
Figure 3-19. Bull trout redd counts in Lower Coal Creek.
111
-------
Water Quality Impairment Status
Flathead River Headwaters TPA
Pfankuch Ratings
Pfankuch ratings were estimated at several sites in the Coal Creek watershed between 1976 and 2003. A
summary of the findings is shown in Table 3-27. In 2003, Lower Coal Creek had excessive deposition at
one site and significant bank cutting at most of the sites. Overall, the data suggest that bank cutting might
be a source of sediment in the lower segments of Coal Creek. However, there is no information to
suggest that this is necessarily a result of human activities. It may or may not be a natural phenomenon
(see Section 4.1).
Table 3-27. Pfankuch Ratings for Segments of Lower Coal Creek
Stream Segment
Year
Mass Wasting
Vegetative Bank
Protection
Cutting
Deposition
RM 0.294
1976
Good
Good
Good/Fair
Excellent
RM 8.492
1976
Excellent
Excellent
Excellent
Excellent
RM 0.294
1979
Excellent
Fair
Fair
Excellent
RM 8.49
1979
Excellent
Excellent
Excellent
RM 8.44
1985
Good
Good
Good/Fair
Excellent/Good
RM 8.68
1985
Good
Good
Fair
Fair
RM 8.53
1994
Good
Excellent
Good/Fair
Excellent
RM 7.92
1997
Excellent
Good
Fair
Fair
Profile #1 UL
2003
Good
Good
Fair
Poor
Profile #1 CS
2003
Excellent
Good
Good/Fair
Fair
Profile #1 LL
2003
Excellent
Excellent
Good/Fair
Poor
Profile #2 CS
2003
Excellent
Good
Fair
Good
RM = river mile.
Suspended Sediment Concentration
No data have been collected.
Turbidity
No data have been collected.
Sources
A detailed source assessment for the entire Coal Creek watershed is presented in Section 4.1. A summary
is presented in the following paragraphs to facilitate the use of this information in the context of the
weight-of-evidence determination of water quality impairment.
Almost 30 percent of the Coal Creek watershed (14,938 acres) burned in the 2001 Moose Fire, mostly in
the lower third of the watershed from the confluence of Dead Horse Creek downstream to the mouth.
Much of the Dead Horse Creek and Cyclone Creek watersheds also burned in that fire. The Forest
Service Water Erosion Prediction Model (WEPP-Disturbed) estimated that 53,000 tons of sediment
would enter streams in the Coal Creek watershed in 2003 because of the Moose Fire (3.6 tons
sediment/acre). However, the model assumes that average rainfall fell in the Coal Creek watershed in
2002 and 2003. This was not the case, as both 2002 and 2003 were extremely dry years. Forest service
personnel estimated that less than one ton of sediment per acre of land was actually delivered to streams
112
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Flathead River Headwaters TPA
Water Quality Impairment Status
in 2003 (Sirucek, personal communication, September 20, 2004). The amount of sediment eroded
because of the fire will continue to decrease in the future as vegetation reestablishes and soils stabilize.
Since 1954, 4,809 acres of land have been clear-cut (9 percent of the total watershed), with an average of
94 acres of land cut per year. The most recent clear-cut occurred in 2000, when 512 acres were cut from
the Coal Creek State Forest. The ECA for the Coal Creek watershed is 18 percent, which is lower than
the proposed supplemental indicator of 25 percent. This ECA value is heavily influenced by fire, a
natural occurrence, and is higher than expected largely because of the 2001 Moose Fire. Water yield
increase (7.0 percent above natural) was also lower than the proposed supplemental indicator. Pre-fire
water yield for the entire Coal Creek watershed was 2.5 percent.
The WEPP-Disturbed model estimated that 34 tons of sediment reached Coal Creek in 2003 because of
historical harvest activities. However, is it recognized that much more sediment may have been
contributed in the past. These historical harvest loads may be contributing to the high percentage of fine
material in the stream substrate as identified by the McNeil core and substrate sampling.
The FNF survey found that 10 road sites are actively contributing sediment to stream channels in the Coal
Creek watershed. The WEPP-Roads model estimated that these roads contribute approximately one-half
ton of sediment per year. Other roads were identified as needing BMPs; however, none of these appeared
to be contributing sediment directly to a stream channel. The road density in the Coal Creek watershed is
relatively low (1.17 miles/square mile), and is rated fully functioning using Forest Service criteria. It
should be noted that road conditions have greatly improved in the FNF over the past several years, and
historical roads and historical road building activities may have contributed a much greater load of
sediment to streams in the past. This historical sediment load may be contributing to the high percentage
of fine material in the stream substrate as identified by the McNeil core and substrate sampling.
MFWP found that the lower segment of Coal Creek was a major depositional area, with high amounts of
large woody debris (partially from the Moose Fire) retaining pockets of sediment (MFWP, 2004). An
imbalance of large woody debris (LWD) was noted in this survey, where some segments appeared to have
too much and others not enough. Channelization, historical riparian clear-cuts, and a lack of streamside
management zone were also noted in various sections of Coal Creek. This was verified by FNF
personnel, who suggested that channel alterations in association with large woody debris distribution
could be impairing the fishery beneficial use in Coal Creek (Stevens and Sirucek, personal
communications, June 23, 2004). Bank erosion sites were also noted during this survey, although not all
streams were surveyed. Approximately 697 tons of sediment per year come from the identified bank
erosion sites. Bank erosion loads are most likely much higher than estimated because of the incomplete
survey.
Overall, there appears to be very few current anthropogenic sources of sediment in the Coal Creek
watershed. However, current sediment sources may not be the cause of the high percentage of fine
substrate material observed in Coal Creek. Historical sources, such as roads, road building, and harvests,
may have contributed much more sediment in the past than is currently observed today. Because in-
stream sediment can move slowly through a system, the conditions observed today may be a result of
historic natural and anthropogenic sediment loading.
Lower Coal Creek Water Quality Impairment Summary
The available data for Lower Coal Creek are compared with the proposed thresholds and supplemental
indicators in Table 3-28. As stated in Section 3.3, the approach for the FTPA is to evaluate a suite of
targets and supplemental indicators to make beneficial use determinations. When one or more of the
targets are exceeded, the circumstances around the exceedance are investigated, and the supplemental
indicators are used to provide additional information to support a determination of impairment/non-
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impairment. In the lower segment of Coal Creek, three out of the four targets were exceeded (McNeil
cores, substrate scores, and percent surface fines).
When examined in the absence of the supplemental indicators or without examining all of the available
evidence, the targets in Lower Coal Creek clearly suggest water quality impairment associated with
sediment. The McNeil core, substrate score, and percent surface fines all suggest impairment associated
with sediment. Further, bull trout densities and red counts have declined substantially in Lower Coal
Creek, and counts have not rebounded in recent years as they have in the other North Fork Flathead Basin
tributaries.
However, more than 20 years of McNeil core and substrate score data are available for Lower Coal
Creek, and no trends are apparent over that time period. Bull trout redd counts and densities from 1980 to
1991 show that high bull trout densities existed with historical McNeil core values as high as 42.1 and
substrate scores as low as 9.6. Did slightly high subsurface substrate fines (as measured by McNeil cores)
cause the decline in bull trout in Lower Coal Creek? The information suggests that that bull trout
populations historically were not affected by high amounts of subsurface fine sediment (>35 percent
McNeil core) in Lower Coal Creek, and it does not appear that the substrate condition caused the
observed decline in bull trout. It is possible that bull trout declines were not caused by sediment, but by
some other stressor (or combination of stressors), such as the overall decline in the Flathead Lake bull
trout meta-population (see Section 2.2.2), temperature, or habitat alterations.
It is possible that substrate conditions are currently preventing the bull trout population in Lower Coal
Creek from rebounding, but examination of the available data does not provide a black-and-white answer.
The percent surface fines and macroinvertebrate data provide additional information regarding the
situation. The surface fines proposed threshold value (20 percent), a conservative value that suggests
beneficial uses might be threatened by sediment, is barely exceeded in Coal Creek. Other information
suggests that macroinvertebrate populations are impaired when the percent surface fines reaches 30
percent (see Section 3.3.1). In the case of Coal Creek, macroinvertebrate data were collected at the same
time as the surface fines data. The macroinvertebrate data showed that excellent communities were
present at both sites in Coal Creek, and at the two sites in the North and South Forks. This information
shows that healthy macroinvertebrate populations existed with percent surface fines data as high as 22.9
percent, and suggests that percent surface fines are not impairing beneficial uses. Also, out of all of the
macroinvertebrate data collected in the Flathead River Headwaters TPA, the four best Mountain IBI
scores were found in the Coal Creek watershed. Clinger taxa were high at all four sites in the Coal Creek
watershed, and did not indicate any impairment because of sediment or siltation. These data support the
conclusion that aquatic life beneficial uses are not impaired because of current sediment conditions in
Lower Coal Creek.
It appears that aquatic life health (as evaluated by various macroinvertebrate metrics) is not impaired in
Lower Coal Creek. The cold-water fishery, however, is currently impaired. Bull trout populations have
failed to rebound in Lower Coal Creek as they have in many of the other North Fork Flathead tributaries.
The cause of this impairment is unknown. The fact that the substrate conditions are slightly less than
optimal based on comparison with the proposed threshold values may or may not be contributing to this
impairment. Other factors such as temperature, physical habitat condition (e.g., large woody debris,
number of pools, barriers, stream temperature) or high loads of sediment delivered to the stream from
natural sources such as eroding banks or the recent Moose Fire may be the cause. Or, perhaps, it is a
combination of factors, including historical sediment loading that has not moved through the system.
Given this uncertainty, a TMDL focusing on addressing all known anthropogenic sediment sources has
been prepared and is presented in Section 4.0. A plan for a future study to identify the cause(s) of the bull
trout population decline has been prepared and is also presented in Section 4.0.
114
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Water Quality Impairment Status
Table 3-28. Comparison of Available Data with the Proposed Targets and Supplemental Indicators
for Lower Coal Creek
Targets
Threshold
Upper
Lower
5-year Mean McNeil Core Percent
Subsurface Fines < 6.35 mm
35%
37.1%
5-year Mean Substrate Scores
> 10
9.9
Percent Surface Fines < 2 mm
< 20%
21.7%
22.9%
Clinger Richness
> 14
23
16
Supplemental Indicators
Recommended Value
Upper
Lower
Juvenile Bull Trout and Westslope
Cutthroat Trout Density
Documented increasing or
stable trend
Cutthroat: NA
Bull: Decline
Bull Trout Redd Counts
Documented increasing or
stable trend
Decline
SSC Mean
SSC Mean Annual Maximum
SSC Maximum
3.2 ฑ5.2 mg/L
14.6 mg/L
61.6 mg/L
NA
Turbidity
High flow-50 NTU
instantaneous maximum
Summer base flow - 10 NTU
NA
Pfankuch Mass Wasting Score
"good"
Excellent
Pfankuch Bank Vegetation Score
"good"
Good
Pfankuch Cutting Score
"good"
Fair
Pfankuch Deposition Score
"good"
Fair
Montana Mountain
Macroinvertebrate Index of
Biological Integrity
> 75%
90
86
Percentage of Clinger Taxa
"high"
71
83
EPT Richness
>22
23
19
Periphyton Siltation Index
< 20
NA
Fire
Evaluated on a case-by-case
basis
Year: 2001
Acres: 14,938
% Burned: 30
Equivalent Clear-Cut Acres
< 25%
18%
Water Yield
< 10%
7.0% (2.5%)1
Roads
Evaluated on a case-by-case
basis
Some roads in need of BMPs
'Pre-Moose Fire water yield.
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Water Quality Impairment Status
Flathead River Headwaters TPA
3.4.2 Middle Fork Flathead River Watershed
The Middle Fork Flathead River watershed encompasses 723,161 acres (1,130 square miles) of land in
Flathead County, Montana (Figure 3-20). The Middle Fork Flathead River flows southeast to northwest
for 55 miles from the continental divide to the confluence with the North Fork Flathead River, eventually
flowing into Flathead Lake. Approximately half of the watershed is in Glacier National Park. With the
Bob Marshall Wilderness (90,441 acres) and Great Bear Wilderness Area (212,104 acres), almost the
entire watershed is federally protected.
Montana's 1996 303(d) list showed four streams in the Middle Fork Flathead River watershed as
impaired: Challenge Creek, Granite Creek, Skyland Creek, and Morrison Creek. Aquatic life and/or
fishery beneficial uses were listed as impaired because of habitat alterations and siltation in all four
streams. Skyland Creek and Granite Creek were also listed as impaired because of suspended solids in
1996. MDEQ reported on the 2002 303(d) list that Challenge Creek fully supported all beneficial uses,
and no TMDLs were required at that time. Granite Creek was listed for siltation and bank erosion on the
2002 303(d) list, MDEQ did not have sufficient credible data for Skyland Creek. Morrison Creek was
listed for habitat alterations and siltation.
3.4.2.1 Challenge Creek
Challenge Creek is a first-order tributary flowing approximately 4.3 miles from its origin to its confluence
with Granite Creek. The cold-water fishery and aquatic life beneficial uses in Challenge Creek were
listed on the 1996 303(d) list as impaired because of habitat alteration and siltation. The basis for the
1996 listing is unknown. In 2002, MDEQ removed Challenge Creek from the 303(d) list and indicated
that it was "fully supporting" its designated uses based on the following explanation:
"There are no indications of impairments to the stream. Some logging has been done, but
there are no overwhelming impacts. Sedimentation appears to be natural. Chemistry and
fish data give no indication of a problem. "
Challenge Creek has been removed from the 303(d) list. Since it has been demonstrated that Challenge
Creek is fully supporting its beneficial uses, no TMDL is necessary.
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Flathead River Headwaters TPA
Water Quality Impairment Status
GLACIER
COUNTY
O Kiowa
TETON
COUNTY
/\/303(d) Listed Segments
o Cities
'Counties
Lakes
Streams
Wilderness Area
Glacier National Park
] Middle Fork Flathead River Watershed
O Coram
O Martin City
East Glacier Park
O
FLATHEAD
COUNTY
Creek
PONDERA
COUNTY
Figure 3-20. Middle Fork Flathead River watershed.
117
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Water Quality Impairment Status
Flathead River Headwaters TPA
3.4.2.2 Granite Creek
Granite Creek is a second order tributary flowing approximately 8.2 miles from its origin at the
confluence of Dodge and Challenge creeks to its confluence with the Middle Fork Flathead River (Figure
3-21). The total watershed area is 18,339 acres (28.7 square miles), one third of which is in the Great
Bear Wilderness Area. Because of the Wilderness Area, sampling efforts have focused on the upstream
portion of Granite Creek in the FNF. It is assumed that there are few to no anthropogenic sources in the
Wilderness Area. Based on field observations, portions of Granite Creek are intermittent in the
headwaters region (Laidlaw, 2003).
The aquatic life beneficial use in Granite Creek was listed on the 1996 303(d) list as impaired because of
habitat alterations, suspended solids, and siltation. The basis for the 1996 listing is unknown. Bank
erosion, other habitat alterations, siltation, and fish habitat degradation were the causes of impairment
cited on the 2002 303(d) list; cold water fishery and aquatic life beneficial uses were listed as impaired.
According to MDEQ's Assessment Record Sheet, the 2002 listing was based primarily on a 1991 Forest
Service report citing moderate impairment "because of excessive sedimentation from logging road runoff
and past silviculture " (Chestnut 2000). MDEQ's Assessment Record Sheet also cited a decline in bull
trout populations.
A review of the available data is provided below. The available data include substrate scores, McNeil
cores, Pfankuch ratings, pebble counts, sources (fires, harvest, roads), macroinvertebrates, and fish
population estimates. SSC and turbidity data from Challenge and Dodge creeks are also discussed in this
section because these streams are the main headwater tributaries to Granite Creek.
118
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Flathead River Headwaters TPA
Water Quality Impairment Status
McNeil Core
MFWP collected McNeil core samples in Granite Creek in 1982 and in 1986 through 2001 (Weaver et al.,
2003). The mean from 1997 to 2001 was 33.6, which is below the target of 35 percent. There is also a
decreasing trend in the McNeil core data from 1986 through 2001. The maximum value recorded for the
past five years is 35.1, and the most current data (2001) indicates a value of 33.7 percent fines.
Substrate Scores
Substrate scores were calculated based on MFWP stream surveys conducted in 2001 and 2002 (Deleray et
al., 1999). The mean substrate score for the period of record was 11.5, indicating good juvenile bull trout
rearing habitat quality.
Pebble Counts
Pebble counts were collected from one reach in the Granite Creek watershed in 2003. The percent fines
smaller than 2 millimeters were 24.8 percent (upper), 18.2 percent (cross section), and 10.4 percent
(lower). The average for the reach was 17.8, which is below the supplemental indicator of 20 percent.
The data suggest that surface fines are not impairing beneficial uses in Granite Creek.
119
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Water Quality Impairment Status
Flathead River Headwaters TPA
Macroin vertebrates
Macroinvertebrates were collected at one site on Granite Creek in August 2003. Clinger taxa (15) and
percent dingers (77 percent) suggest good water quality with no evidence of siltation. The Mountain IBI
score (81 percent) indicates that the aquatic life beneficial uses are not impaired, although the number of
EPT taxa (19) was slightly lower than the supplemental indicator. Other supporting metrics suggest that
no water quality impairments were present. The HBI score was 1.85, which is lower than the
recommended value of 3.5. The dominant taxa were Drunella doddsi, Yoraperla, Baetis tricaudatus,
Epeorus deceptivus, and Heterlimnius, and all had low tolerance values and are sensitive to pollution. In
general, the macroinvertebrate data suggest that aquatic life beneficial uses in Granite Creek are not
impaired because of siltation.
Macroinvertebrates were also collected in Challenge Creek in August 2003. Data are presented here as
supplemental information for Granite Creek, because Challenge Creek is a major headwaters tributary to
Granite Creek, and is likely to reflect water quality in Granite Creek. Macroinvertebrate populations at
this site were very similar to Granite Creek's. The number of Clinger taxa (18) and clinger percent (70
percent) suggest good water quality with no evidence of siltation. The Mountain IBI score was 86 percent
and did not indicate a water quality impairment. As in Granite Creek, the number of EPT taxa (20) was
below the recommended supplemental indicator. Other supporting metrics indicated good water quality.
The HBI score was 2.65, which is lowerthanthe recommended value of 3.5 (i.e., no apparent nutrient or
sediment influences). The majority of the most dominant taxa (Drunella doddsi, Rhithrogena, Zapada
columbiana, Brachycentrus americanus) are intolerant to pollution. In general, the macroinvertebrate
data suggest that the aquatic life beneficial use of Challenge Creek is not impaired because of siltation.
Fish Population
MFWP conducted bull trout redd count surveys from 1980 through 2002 (Weaver et al., 2003). Counts
ranged from 47 in 1984 to a low of 4 in 1996, and generally declined from 1986 to 1996 (Figure 3-22).
However, redd counts appear to be increasing again from 1997 to the present. It is possible that the
declining redd count trend reflects the overall trend in the North and Middle Fork Flathead River
watersheds due to changes in the Flathead Lake ecosystem and food chain.
MFWP began conducting juvenile population surveys on Granite Creek in 2001 and 2002. The bull trout
densities in 2001 and 2002 were 5.99 juveniles per 100 square meters and 4.13 juveniles per 100 square
meters, respectively. Unfortunately, in the absence of a longer period of record, it is not possible to use
the population data to evaluate trends.
120
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Flathead River Headwaters TPA
Water Quality Impairment Status
50
45 ฆ n
40 -
en _
I 35 - n n
o n n n i-i
ฐ 30 - n n n
I, ... n n
0 20 - n n n
i- n n n
1 15 - n
oq n
10 ~ n
5 -
0 1iiiiiiiiiiiiiiJLiiiii
OrMn^lfl(DNOJO)Oi-(MP)tlB(DNtOO)Or(N
ooooooooooooooooooooa>a>a>a>a>a>a>a>a>a>ooo
0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)000
Figure 3-22. Bull trout redd counts for Granite Creek.
Pfankuch Ratings
Stream channel stability ratings were completed at one site in Granite Creek in 2003. No other historical
data are available for Granite Creek. However, historical ratings are available for Challenge Creek and
Dodge Creek, and are included in Appendix C. Indications of mass wasting, bank erosion, and deposition
were noted at the Granite Creek reach in 2003 (Table 3-29). However, streams in the Middle Fork
Flathead River watershed (i.e., Granite Creek, Skyland Creek, Morrison Creek) tend to have greater rates
of erosion because of bedrock geology. Sandstones and shales in the region are more erodible than the
metamorphic rocks and soils, and therefore the maximum natural potential of the stream channel is most
likely only good or fair for the evaluated parameters.
Table 3-29. Pfankuch Ratings for Segments of Granite Creek.
Stream Segment
Year
Mass Wasting
Vegetative Bank
Protection
Cutting
Deposition
Profile #1 UL
2003
Fair
Good
Fair
Fair
Profile #1 CS
2003
Good
Good
Fair
Fair
Profile #1 LL
2003
Fair
Good
Fair
Fair
RM = river mile.
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Suspended Sediment Concentration
No suspended sediment concentration data exist for the main stem of Granite Creek; however, suspended
sediment concentration (SSC) data were collected in Challenge and Dodge creeks, the two primary
headwater tributaries, from year to year between 1980 and 1995 (n = 146 for Challenge and 144 for
Dodge). In general, samples were collected to capture spring runoff (in April, May, and June) as well as
base flow conditions (in July, August, September, October, and November). However, the frequency of
sampling varied from year to year.
The absence of current SSC data and data from the main stem of Granite Creek prohibits the use of the
older data in making a current impairment determination. However, the data are useful in evaluating
long-term trends and in making historical comparisons with other streams in the TPA. The mean for the
period of record, mean annual maximum, and maximum reported values are presented in Tables 3-30 and
3-31. All values are below the proposed supplemental indicators.
Table 3-30. Comparison of Available SSC Data for Challenge Creek with the Supplemental
Indicator Values
SSC Metric
Observed
Value (mg/L)
Indicator Value for Comparison (mg/L)
Mean (mg/L)
3.37
3.15 + 5.83
Mean Annual Maximum (mg/L)
13.48
14.56
Maximum (mg/L)
37.10
61.60
Table 3-31. Comparison of Available SSC Data for Dodge Creek with the Supplemental Indicator
Values
SSC Metric
Observed
Value (mg/L)
Indicator Value for Comparison (mg/L)
Mean (mg/L)
2.57
3.15 + 5.83
Mean Annual Maximum (mg/L)
8.69
14.56
Maximum (mg/L)
24.42
61.60
Turbidity
No turbidity data are available for Granite Creek; however, turbidity data were collected in Challenge
Creek for approximately the same period of record as the SSC data (1980-1995, n = 149). As with the
SSC data, a lack of current data prohibits the use of the older data in making a current impairment
determination, but they are useful in evaluating long-term and historical trends.
The mean turbidity in Challenge Creek for the period of record is 1.79 NTU and the median is 0.99 NTU.
The maximum recorded value was 17 NTU in May 1987. These data do not suggest that Challenge
Creek, one of the primary headwaters tributaries, was likely contributing to potential sediment
impairment in Granite Creek.
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Flathead River Headwaters TPA
Water Quality Impairment Status
Sources
In 1998 a large fire burned 2,230 acres of land (12 percent) in the headwaters region of the Granite Creek
watershed. Most of this was in the Dodge Creek drainage and in the lower portion of the Challenge Creek
drainage. Prior to 1998, no other major fires had occurred in the watershed since 1919. The large burned
area will most likely contribute increased amounts of sediment and will increase water yield to Granite
Creek for several more years.
Since 1960, clear-cutting has occurred on 1,167 acres of land (6 percent), with the most recent clear-cut
occurring in 1987. The harvests occurred during two major time periods: 1970-1975 and 1984-1987.
No other clear-cutting has occurred. However, the FNF sources report indicates that the stream channel
occupies a wide alluvial valley that has experienced historical riparian harvests (FNF, 2003). Historic
timber management units are well vegetated and the historical haul roads are bermed or gated to prevent
traffic. The ECA for 2004 is 14.6 percent, which is below the supplemental indicator of 25 percent.
Overall, clear-cut land does not appear to be a significant source of sediment.
The lower Granite Creek watershed is part of the Great Bear Wilderness Area, and therefore has no
sediment contributions from roads. Upper Granite Creek has roads that are either closed year long or only
open seasonally. The FNF survey found that 2 out of 16 road-stream crossings were at risk of failure
(FNF, 2003). In addition, 18 out of 24.1 miles of roads are in need of BMPs or upgrading. Only 1.5
miles of roads are within 125 feet of a stream. Overall road density is low (1.0 mile per square mile) and
the FNF survey concluded that roads were not a major source of sediment to Granite Creek. However, it
appears that roads in the headwaters region area an anthropogenic source of sediment.
Granite Creek Water Quality Impairment Summary
Granite Creek was listed on the 1996 303(d) list as impaired because of habitat alteration, siltation, and
suspended solids. Bank erosion, other habitat alterations, fish habitat degradation, and siltation were the
listed causes of impairment on the 2002 303(d) list. The impaired beneficial uses were aquatic life and
fisheries. A summary of the data for Granite Creek is presented below and in Table 3-32.
Overall, it appears that siltation and suspended solids are not currently impairing beneficial uses in
Granite Creek. None of the target values were exceeded. McNeil core and substrate scores were
collected at one site over multiple years, and both sets of data indicate good substrate conditions. Good
substrate conditions were also noted in the surface fines data. There is no indication of sediment
impairment in the macroinvertebrate data, as the number of dinger taxa was high (greater than 14).
Because none of the targets were exceeded, it can be concluded that beneficial uses in Granite Creek are
not impaired by sediment or siltation.
The supplemental indicators generally support this conclusion. Macroinvertebrate data suggest that
healthy, complex systems were present and there was no indication of impairment from any pollutants
(high IBI score). The available fisheries data suggest that the bull trout population, after declining in the
1990s, is now rebounding. The cause of the decline is unknown, but it coincides with the documented
changes to the bull trout fishery connected to Flathead Lake. ECA (15 percent) was less than the
proposed indicator and the road density was low. Twelve percent of the watershed burned in 1998, and
likely has contributed increased natural sediment and water yield to the system. However, any effects
from the fire do not appear to be impairing beneficial uses.
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Table 3-32. Comparison of Available Data with the Proposed Targets and Supplemental Indicators
for Granite Creek
Targets
Threshold
Available Data
5-year Mean McNeil Core Percent Subsurface Fines <
6.35 mm
35%
33.6%
5-Year Mean Substrate Scores
> 10
11.5
Percent Surface Fines < 2 mm
< 20%
17.8%
Clinger Richness
> 14
15
Supplemental Indicators
Recommended Value
Available Data
Juvenile Bull Trout and Westslope Cutthroat Trout
Density
Documented increasing or stable
trend
< <
Bull Trout Redd Counts
Documented increasing or stable
trend
Fluctuating, but Stable
Trend
SSC Mean
SSC Mean Annual Maximum
SSC Maximum
+ 5.2 mg/L
14.6 mg/L
61.6 mg/L
NA
Turbidity
High flow-50 NTU instantaneous
maximum
Summer base flow - 10 NTU
NA
Pfankuch Mass Wasting Score
"good"
Fair
Pfankuch Bank Vegetation Score
"good"
Good
Pfankuch Cutting Score
"good"
Fair
Pfankuch Deposition Score
"good"
Fair
Montana Mountain Macroinvertebrate Index of
Biological Integrity
> 75%
81
Percentage of Clinger Taxa
"high"
77%
EPT Richness
>22
19
Periphyton Siltation Index
< 20
NA
Fire
Evaluated on a case-by-case basis
Year: 1998
Acres: 2230
% Burned: 12
Equivalent Clear-Cut Acres
< 25%
14.6%
Water Yield
< 10%
NA
Roads
Evaluated on a case-by-case basis
Some roads in need of
BMPs
124
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Flathead River Headwaters TPA
Water Quality Impairment Status
3.4.2.3 Skyland Creek
Skyland Creek is a second-order tributary flowing approximately 5.5 miles from its origin to the
confluence with Bear Creek (Figure 3-23). It is a small, high-altitude stream that historically has not been
managed as a bull trout fishery. The total watershed area is 5,343 acres (8.3 square miles), all of which is
in the FNF. In 1998, 75 percent of the watershed burned, and most data collected since then reflect the
impacts of the large burned area.
The cold-water fishery and aquatic life beneficial uses in Skyland Creek were listed on the 1996 303(d)
list as impaired as a result of habitat alteration, suspended solids, and siltation. The basis for the 1996
listing is unknown. MDEQ lacked sufficient credible data to include this water body on the 2002 303(d)
list. As a result, reassessment sampling was completed for Skyland Creek in August 2002.
A review of the available data is provided below. The available data include Pfankuch ratings, a pebble
count, channel dimensions, sources (fires, harvest, roads), SSC concentrations, turbidity data,
macroinvertebrates, periphyton, water chemistry, and riparian assessments.
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Flathead River Headwaters TPA
McNeil Core
No McNeil core samples have been collected.
Substrate Scores
No substrate samples have been collected.
Pebble Counts
One pebble count was completed on Skyland Creek in 2002. The percent fines smaller than 2 millimeters
was 5.71 percent, indicating that siltation is not impairing beneficial uses.
Macroin vertebrates
Macroinvertebrates were collected at one site on Skyland Creek in August of 2002. The number of
dinger taxa (13) was slightly below the target, and the percentage of dinger taxa was relatively low (39
percent). These data indicate that a sediment stressor might be present. The macroinvertebrate
supplemental indicators did not meet recommended values as well. The Mountain IBI score was 71
percent, which suggests that aquatic biota are slightly impaired. In addition, the number of EPT taxa (18)
was below the proposed supplemental indicator value.
Other supporting macroinvertebrate metrics suggest that there were no impairments in the biological
community. The five most dominant taxa (Baetis tricaudatus, Orthocladius sp., Epeorus deceptivus,
Drunella coloradensis, and Zapada Oregonensis Gr.) are intolerant to pollution. The HBI score was
2.47, which is lower than the recommended value of 3.5. It should also be noted that Bollman (2003b)
concluded that "in-stream habitats were diverse and available," and "the functional composition of the
assemblage included all expected groups in appropriate proportions."
Periphyton
Periphyton were collected at one site in Skyland Creek in August 2002. The siltation index (3.55) was
below the supplemental indicator of 20, and did not indicate impacts from sediment. Bahls (2003) noted
that "The dominant diatom at this site was Encyonema silesiacum, which is somewhat tolerant of organic
pollution. A large percentage of this species indicated moderate impairment here. The pollution index
also indicated minor impairment from organic loading. Diatom species richness, equitability, and
diversity were also low and indicated minor impairment. " Bahls concluded that a moderate impairment,
probably from organic enrichment, was present at this site. However, these results may be explained (and
somewhat expected) because of the 1998 fire. Increased organic loading from the 1998 fire may be the
source of moderate impairment of the periphyton communities in Skyland Creek. Soils this region also
have naturally high nutrient concentrations, and potentially explain the organic loading.
126
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Flathead River Headwaters TPA
Water Quality Impairment Status
Fish Population
No fish data have been collected.
Pfankuch Ratings
Pfankuch ratings were estimated at multiple locations along Skyland Creek in the 1980s and in 1998, and
the data are summarized in Table 3-33. In the absence of recent data, it is not possible to take full
advantage of this supplemental indicator.
Table 3-33. Pfankuch Ratings for Segments of Skyland Creek
Stream Segment
Year
Mass Wasting
Vegetative Bank
Protection
Cutting
Deposition
RM 1.95
1980
Fair
Fair
Good/Fair
Good/Fair
RM 2.11
1980
Good
Good
Good/Fair
Good
RM 2.39
1980
Good
Good
Good/Fair
Excellent
RM 2.59
1980
Excellent
Excellent
Fair
Fair
RM 2.69
1980
Excellent
Excellent
Fair
Good
RM 3.03
1980
Excellent
Excellent
Good/Fair
Fair
RM 3.83
1980
Fair
Excellent
Poor
Good
RM 4.26
1980
Excellent
Excellent
Good/Fair
Good
RM Unknown
1981
Poor
Good
Fair/Poor
Fair
RM 2.13
1987
Good
Good
Fair
Good/Fair
RM 2.36
1987
Excellent
Poor
Excellent
Excellent
RM 2.69
1987
Excellent
Good
Good
Excellent
RM 4.15
1987
Fair
Good
Good/Fair
Fair
RM 4.57
1987
Fair
Good
Good
Good
RM 4.04
1998
Good
Excellent
Good/Fair
Good
RM = river mile.
Suspended Sediment Concentration
Suspended sediment concentration (SSC) data were collected in Skyland Creek on nearly an annual basis
between 1980 and 1993 (n = 292). In general, samples were collected to capture spring runoff (in April,
May, and June) as well as base flow conditions (in July, August, September, October, and November).
However, the frequency of sampling varied from year to year.
The absence of current SSC data prohibits the use of the older data in making a current impairment
determination. However, the older data is useful in evaluating long-term trends and in making historical
comparisons with other streams in the TPA. The mean for the period of record, mean annual maximum,
and maximum reported values are presented in Table 3-34. In general, these values do not suggest water
quality impairment associated with sediment, since concentrations were below the supplemental indicator
values.
127
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Water Quality Impairment Status
Flathead River Headwaters TPA
Table 3-34. Comparison of Available SSC Data for Skyland Creek with the Supplemental Indicator
Values
SSC Metric
Observed Value
(mg/L)
Indicator Value for Comparison (mg/L)
Mean (mg/L)
2.21
3.15 ฑ 5.83
Mean Annual Maximum (mg/L)
7.87
14.56
Maximum (mg/L)
14.00
61.60
Turbidity
Turbidity data were collected in Skyland Creek for approximately the same period of record as for the
SSC data (1980-1993, n = 296). As with the SSC data, a lack of current data prohibits the use of for the
older data in making a current impairment determination, but the older data are useful in evaluating long-
term and historical trends.
The mean turbidity for the period of record is 1.47 NTU and the median is 0.91 NTU. The maximum
recorded value was 48 NTU in May 1987. Although the data are old, they do not exceed the
supplemental indictor values.
Riparian Assessment
A Natural Resources Conservation Service (NRCS) Visual Riparian Assessment was completed in 2002
(MDEQ, 2002). The overall score was 85.5 percent, indicative of good riparian condition. The only
disturbance found in the watershed was a lack of large riparian trees, which was attributed to flooding and
fire.
Sources
More than 75 percent of the Skyland Creek watershed burned in the 1998 Challenge Fire (4,038 acres).
Almost the entire headwaters region of Skyland Creek burned in this fire, from the confluence of the West
Fork Skyland Creek upstream. The large burned area has most likely contributed increased sediment
loads to Skyland Creek, as well as increased nutrient loads and unstable channel conditions. NRCS and
EPA field assessments noted that much of the riparian area was burned, and there is currently a lack of
shade and large woody debris around the channel. All field data collected since 1998 may reflect the
impacts of this fire.
Since 1960, 879 acres of land have been clear-cut (16 percent). This occurred during two time periods -
1970 to 1972 and 1984 to 1986. No clear-cuts have occurred since 1986. The calculated ECA for 2004 is
9.2 percent. Because there are no recent clear-cuts and the ECA is below the supplemental indicator,
clear-cut land does not appear to be a significant source of sediment.
The FNF found that roads are not a significant source of sediment in Skyland Creek (FNF, 2003). More
than half of the roads are closed yearlong, and the remaining roads are only open seasonally. No road-
stream crossings are at risk of failure, and all roads have had full BMPs implemented. Only 2.3 miles of
roads are within 125 feet of a stream.
128
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Flathead River Headwaters TPA
Water Quality Impairment Status
Skyland Creek Water Quality Impairment Summary
The cold-water fishery and aquatic life beneficial uses in Skyland Creek were listed on the 1996 303(d)
list as impaired because of habitat alteration, siltation, and suspended solids. The basis for the 1996 listing
is unknown. MDEQ lacked sufficient credible data to include this water body on the 2002 303(d) list. As
a result, reassessment sampling was completed for Skyland Creek in August 2002. The data for Skyland
Creek are summarized below and in Table 3-35.
It appears that siltation and suspended solids are not impairing beneficial uses in Skyland Creek. No
siltation was evident in the surface fines data. Although the number of dinger taxa was slightly lower
than the target value, Bollman (2003) noted that taxa richness was good and did not indicate a sediment
impairment. Information for the other targets (McNeil cores and substrate scores) was not available.
Supplemental indicators generally suggested good conditions relative to sediment and siltation. The
periphyton siltation index was low, which indicates that the algae community is not impacted by
excessive sediment. Bollman (2003) reported that the macroinvertebrate community was "excellent" and
Skyland Creek had "unpolluted water" with no indication of sediment deposition. IBI scores, dinger
taxa, and EPT taxa were all slightly lower than recommended values. However, the cause may simply be
due to watershed conditions (high elevation, low flow, drought) or the effects of the 1998 fire (increased
water yield, sediment loads, nutrient loads; watershed disturbance). This theory is supported by the
periphyton data, which suggested that excessive nutrient loading is present, most likely due to the 1998
fire.
Because of the 1998 Challenge fire, it is difficult to differentiate fire-related sediment impairments from
those associated with other potential anthropogenic sources. However, the FNF and MDEQ found no
major anthropogenic sediment sources during the 2002 and 2003 surveys. Historically, a small
percentage of the watershed has been clear-cut, but no land has been clear-cut for the past 18 years. All
roads have full BMP measures implemented, and the Forest Service found no indication of failing road-
stream crossings. The lack of sources in the Skyland Creek watershed suggests that any impacts found in
the stream are due to natural sources. This, in combination with the good percent surface fines, dinger
richness, Pfankuch ratings, and low periphyton siltation index, indicates that Skyland Creek is not
impaired because of siltation or sediment.
However, the macroinvertebrate and periphyton data do suggest that a slight aquatic life impairment is
present, most likely due to nutrients. This is explained and somewhat expected because of the 1998 fire
and subsequent increased nutrient loading. The impairment is most likely due to natural sources (fire)
and not anthropogenic sediment loading.
129
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Water Quality Impairment Status
Flathead River Headwaters TPA
Table 3-35. Comparison of Available Data with the Proposed Targets and Supplemental Indicators
for Skyland Creek
Targets
Threshold
Available Data
5-year Mean McNeil Core Percent Subsurface
Fines < 6.35 mm
35%
NA
5-year Mean Substrate Scores
> 10
NA
Percent Surface Fines < 2 mm
< 20%
5.7%
Clinger Richness
> 14
13
Supplemental Indicators
Recommended Value
Available Data
Juvenile Bull Trout and Westslope Cutthroat
Trout Density
Documented increasing or stable trend
NA
Bull Trout Redd Counts
Documented increasing or stable trend
NA
SSC Mean
SSC Mean Annual Maximum
SSC Maximum
ฑ 5.2 mg/L
14.6 mg/L
61.6 mg/L
NA
Turbidity
High flow - 50 NTU instantaneous maximum
Summer base flow - 10 NTU
NA
Pfankuch Mass Wasting Score
"good"
Good
Pfankuch Bank Vegetation Score
"good"
Excellent
Pfankuch Cutting Score
"good"
Good/Fair
Pfankuch Deposition Score
"good"
Good
Montana Mountain Macroinvertebrate Index of
Biological Integrity
> 75%
71%
Percentage of Clinger Taxa
"high"
39%
EPT Richness
>22
18
Periphyton Siltation Index
<20
3.6
Fire
Evaluated on a case-by-case basis
Year: 1998
Acres: 4038
% Burned: 76
Equivalent Clear-Cut Acres
< 25%
9.2%
Water Yield
< 10%
NA
Roads
Evaluated on a case-by-case basis
No significant
road sources
Riparian Assessment
> 75%
86%
130
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Flathead River Headwaters TPA
Water Quality Impairment Status
3.4.2.4 Morrison Creek
Morrison Creek is a third-order tributary flowing approximately 14.8 miles from its origin to the
confluence with the Middle Fork of the Flathead River (Figure 3-24). The total watershed area is 32,324
acres (50.5 square miles), the lower half of which is in the Great Bear Wilderness Area. All of the land
in the watershed is federally owned (the Wilderness Area and FNF). Because of access constraints and
the lack of potential anthropogenic sources in the Wilderness Area, sampling efforts have focused on
Morrison Creek upstream of the confluence of Lodgepole Creek in the FNF.
The cold-water fishery and aquatic life beneficial uses in Morrison Creek were listed on both the 1996
and 2002 303(d) lists as impaired because of habitat alteration and siltation. The basis for the 1996 listing
is unknown. According to MDEQ's Assessment Record Sheet, the 2002 listing was based primarily on
the results of a 1989 MDEQ stream assessment (MDEQ, 2002).
A review of the available data is provided below. The available data include substrate scores, McNeil
cores, Pfankuch ratings, pebble counts, sources (fires, harvest, roads), macroinvertebrates, and fish
population estimates.
131
-------
Water Quality Impairment Status
Flathead River Headwaters TPA
McNeil Core
MFWP collected McNeil core samples in 1990 and the mean value was 39.2 percent (Weaver et al.,
2003). This individual value exceeds the proposed maximum target value of 35 percent. However, no
recent data are available.
Substrate Scores
Substrate scores were calculated based on MFWP stream surveys conducted between 1986 and 2002
(Deleray et al., 1999). The mean substrate score for 1998 through 2002 was 13.4, indicating good
juvenile bull trout rearing habitat quality. The mean score for the period of record was 12.7.
Pebble Counts
Pebble counts were collected at two reaches in Morrison Creek in 2003. At the upstream reach, percent
surface fines smaller than 2 millimeters were 11.8 percent and 12.2 percent. Downstream, percent surface
fines smaller than 2 millimeters were 14.7 percent and 9.8 percent. None of the samples exceed the
supplemental indicator and there is no indication of a siltation impairment.
Macroin vertebrates
Macroinvertebrates were collected at one site on Morrison Creek in August 2003. Clinger data (15 taxa,
76 percent of the sample) indicate that sediment was not a cause of impairment at this site. The Mountain
IBI was 86, which is above the 75 percent value necessary to be considered fully supporting aquatic life
beneficial uses. There was a high number of EPT taxa (19).
Other supporting metrics also suggested that no water quality impairments were present. The HBI score
was 2.40, which is lower than the recommended value of 3.5. One tolerant taxon found at this site
comprised 0.3 percent of the sample. The dominant taxa (Cricotopus Nostococladius, Rhithrogena,
Baetis tricaudatus, Epeorus deceptivus, and Epeorus grandis) are sensitive to pollution. Overall, the
macroinvertebrate data suggest that the aquatic life beneficial use in Morrison Creek are not impaired
because of siltation.
Fish Population
MFWP estimated juvenile bull trout populations from 1980 through 2002 (with the exception of 1981 and
1984) (Deleray et al., 1999). The population declined in the early 1990s from a maximum count of 17.54
bull trout 100 square meters in 1986 to a minimum count of 1.46 bull trout per 100 square meters in 1994
(Figure 3-25). Declines in the bull trout population were partially related to an upstream migration barrier
that was removed by the Forest Service in 1992 (Deleray et al., 1999). Drought and impacts from trophic
dynamic changes in Flathead Lake are other possible contributing factors to fluctuations in bull trout
densities (Deleray et al., 1999). Bull trout densities have generally been increasing since 1997. MFWP
conducted surveys of redd counts from 1980 through 2002 (Deleray et al., 1999) (Figure 3-26). There
appears to be a slight decreasing trend over time. However, it is difficult to determine trends with any
accuracy due to the large variation in the data (a minimum of 9 redds to a maximum of 99 redds). No
data on westslope cutthroat populations have been collected on this stream.
132
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Flathead River Headwaters TPA
Water Quality Impairment Status
20
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S 16
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6 -
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0^(NO^lf)(DNCOO)0^(N(0^lO(DN(00)O^CN
000000000000000000000)0)0)0)0)0)0)0)0)0)000
CDCDCDCDCDCDCDCDCDCDCDCDCDCDCDCDO)0)0)0)000
Figure 3-25. Bull trout densities in Morrison Creek.
100 1
90 -
80 -
c 70 "II
= n
o n
0 60 -
1 , nnn
|2 40 - I
m 30 - n n n
20 ฆ n
10 ฆ
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0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)0)000
Figure 3-26. Bull trout redd counts in Morrison Creek.
133
-------
Water Quality Impairment Status
Flathead River Headwaters TPA
Pfankuch Ratings
No recent Pfankuch surveys were performed in the Morrison Creek watershed. The most recent survey
was completed in 1980, and is not considered useful in determining a current beneficial use.
Suspended Sediment Concentration
No SSC data have been collected.
Turbidity
No turbidity data have been collected.
Sources
No recent fires have occurred in the upper Morrison Creek watershed (upstream of the confluence with
Lodgepole Creek). The last fire occurred in 1910, and impacts on the current stream condition are
negligible. Two separate fires occurred in the Lodgepole Creek watershed in 1988, burning a total of 630
acres.
Since 1960, land was clear-cut during two years: 1972 and 1974. A total of 399 acres were cut during
those years (1 percent of the total watershed). The ECA for 2004 is 0.49 percent, which is well below the
supplemental indicator of 25 percent. Overall, a small percentage of the watershed was cut more than 30
years ago, and most likely has little effect on current conditions in Morrison Creek.
There are few roads in the Morrison Creek watershed (density = 0.12 miles per square mile), and most of
those are permanently closed. A seasonally closed gate restricts road access within the Morrison Creek
drainage (FNF, 2003). No high-risk culverts or road sediment sources were found, and all roads have
appropriate BMPs. There is no indication that roads are contributing excessive sediment to Morrison
Creek.
Morrison Creek Water Quality Impairment Summary
The cold-water fishery and aquatic life beneficial uses in Morrison Creek were listed on both the 1996
and 2002 303(d) lists as impaired because of habitat alteration and siltation. The basis for the 1996 listing
is unknown. According to MDEQ's Assessment Record Sheet, the 2002 listing was based primarily on
the results of a 1989 MDEQ stream assessment (MDEQ, 2002). A summary of the available data is
presented below and in Table 3-36.
Overall, it appears that siltation is not currently impairing beneficial uses in Morrison Creek. Pebble
count and substrate scores indicated good substrate conditions with no signs of siltation. There was a
high number of dinger taxa in the macroinvertebrate sample, and sediment does not appear to be
impairing that community. Only one McNeil core sample was collected in 1990, and it was not
considered in this analysis given the fact that it is only a single reading and is 14 years old.
Other supplemental indicators generally support this conclusion. Macroinvertebrate data suggest that
healthy, complex systems were present and there is no indication of impairment from any pollutants (high
IBI score). There is no indication that anthropogenic sources are contributing sediment to Morrison
Creek. There have been no recent fires, harvests, or major road activity. The ECA was only 0.49, roads
have BMPs, and no failing road-stream crossings were found. More than half of the watershed is part of
the Great Bear Wilderness Area (a roadless, non-harvested area). Although bull trout populations have
declined from 1980s levels, this trend is similar to the trend in other streams in the North Fork and Middle
Fork Flathead River watersheds, and is potentially due to changes in the Flathead Lake and Flathead
134
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Flathead River Headwaters TPA
Water Quality Impairment Status
River ecosystem. Together, the collected data and lack of sources suggest that aquatic life and fishery
beneficial uses are not impaired because of sediment in Morrison Creek.
Table 3-36. Comparison of Available Data with the Proposed Targets and Supplemental Indicators
for Morrison Creek
Targets
Threshold
Available Data
5-year Mean McNeil Core Percent Subsurface
Fines < 6.35 mm
35%
39.2 (One Sample
Collected in 1990)
5-year Mean Substrate Scores
> 10
12.7
Percent Surface Fines < 2 mm
< 20%
12.0%/12.3%
Clinger Richness
> 14
15
Supplemental Indicators
Recommended Value
Available Data
Juvenile Bull Trout and Westslope Cutthroat
Trout Density
Documented increasing or stable trend
Bull: Increasing Since
1997
Cutthroat: NA
Bull Trout Redd Counts
Documented increasing or stable trend
Possible Decline
SSC Mean
SSC Mean Annual Maximum
SSC Maximum
3.2 + 5.2 mg/L
14.6 mg/L
61.6 mg/L
NA
Turbidity
High flow-50 NTU instantaneous
maximum
Summer base flow - 10 NTU
NA
Pfankuch Mass Wasting Score
"good"
NA
Pfankuch Bank Vegetation Score
"good"
NA
Pfankuch Cutting Score
"good"
NA
Pfankuch Deposition Score
"good"
NA
Montana Mountain Macroinvertebrate Index of
Biological Integrity
> 75%
86%
Percentage of Clinger Taxa
"high"
76%
EPT Richness
>22
19
Periphyton Siltation Index
< 20
NA
Fire
Evaluated on a case-by-case basis
No Recent Fires
Equivalent Clear-Cut Acres
< 25%
0.49%
Water Yield
< 10%
NA
Evaluated on a case-by-case basis
Evaluated on a case-by-case basis
No significant road
sources
135
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Water Quality Impairment Status
Flathead River Headwaters TPA
3.4.3 South Fork Flathead River Watershed
The South Fork Flathead River watershed encompasses 1,075,951 acres or 1,681 square miles of land
(Figure 3-27). It flows 50 miles from the headwaters in the Bob Marshall Wilderness to the Hungry Horse
Reservoir. From the reservoir, the river flows 5.1 miles to the confluence with the Flathead River. More
than half the watershed (1,082 square miles) is designated as Wilderness Area (Bob Marshall Wilderness
and Great Bear Wilderness Area), and the Forest Service manages 560 square miles outside the
wilderness. The upper South Fork (upstream of Hungry Horse Dam) is not hydrologically connected to
the Flathead River, Flathead Lake, Middle Fork Flathead River, or North Fork Flathead River because of
the Hungry Horse Reservoir and Dam.
The water bodies listed as impaired on the Montana's 303(d) lists in the South Fork Flathead River
watershed are Sullivan Creek, South Fork Flathead River, and the Hungry Horse Reservoir.
3.4.3.1 Hungry Horse Reservoir
The cold-water fishery and aquatic life beneficial uses in the Hungry Horse Reservoir were listed on the
1996 303(d) list as impaired because of flow alteration, siltation, and suspended solids. In 2000, MDEQ
found the Hungry Horse Reservoir to be fully supporting its beneficial uses based primarily on the results
of a 1999 MFWP study, indicating that
the reservoir appears to be supporting a healthy, viable native salmonidfishery. Bull
trout may have even increased in recent years. There was no significant changes in the
size distribution of bull trout and cutthroat trout. Populations appear to have stabilized.
The reservoir has a low chlorophyll a concentration (oli go trophic) and high DO levels,
high transparency and low conductivity, and alkaline pH. These are in part a result of
basin geology. Drawdowns impact the fishery (cutthroat particularly) to some degree,
although the overall fishery has been stable over time.
Since it has been demonstrated that the Hungry Horse Reservoir is fully supporting its beneficial uses, no
TMDL is necessary. As a result, Hungry Horse Reservoir is not discussed further herein.
3.4.3.2 South Fork Flathead River
The South Fork Flathead River was listed on the 1996 303(d) list for water quality impairments
associated with habitat and flow alterations, and for flow alteration on the 2002 303(d) list. Since no
"pollutants" are cited as probable causes of impairment on either the 1996 or 2002 303(d) list, no TMDLs
are necessary. As a result, the South Fork Flathead River is not discussed further herein.
136
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Flathead River Headwaters TPA
Water Quality Impairment Status
15 Miles
LEWIS AND CLARK
COUNTY
O
Hungry H
Columbia Fallso
Columbia H
Swan La
o
LAKE
COUNTY
/\/303(d) Listed Segments
o Cities
Counties
Major Streams
Wilderness Area
I I South Fork Flathead
River Watershed
Ferndale
MISSOULA
COUNTY
oEssex
FLATHEAD
COUNTY
Figure 3-27. South Fork Flathead River watershed.
137
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Water Quality Impairment Status
Flathead River Headwaters TPA
3.4.3.3 Sullivan Creek
Sullivan Creek is a third-order tributary flowing approximately 15.3 miles from its origin to its
confluence with the Hungry Horse Reservoir (Figure 3-28). The watershed encompasses 73 square miles
with tributaries including Quintonkon, Connor, Slide, Branch, and Ball creeks. The cold-water fishery
and aquatic life beneficial uses in Sullivan Creek were listed on the 1996 303(d) list as impaired because
of habitat alterations. MDEQ lacked sufficient credible data to include this water body on the 2002
303(d) list. The basis for the 1996 listing is unknown. As a result, reassessment sampling was completed
for Sullivan Creek in August 2002.
A review of the available data is provided below. The available data include pebble counts,
macroinvertebrates, periphyton, sources (harvest, fires, roads), an NRCS Visual Riparian Assessments,
Pfankuch ratings, bull trout redd counts; and long-term, historical suspended sediment concentration and
turbidity data.
/\f 3D3(cf) Listed Streams
A JWQZ Sampling Site*
~ fawns
Lakes
Road*
Stream*
Sullivan Creek Watershed
Swan Lake
O
Figure 3-28. Sullivan Creek watershed.
138
-------
Flathead River Headwaters TPA
Water Quality Impairment Status
McNeil Core
No samples have been collected.
Substrate Scores
No samples have been collected.
Pebble Counts
Wolman pebble counts were conducted at two sites on Sullivan Creek in 2002 (Figure 3-28). The percent
fines smaller than 2 millimeters were 13.1 percent at the upper site and 5.0 percent at the lower site
(average of 9.1 percent for the entire reach). The data do not suggest that sediment is impairing beneficial
uses.
Macroinvertebrates
Macroinvertebrates were collected at two sites on Sullivan Creek in August 2002: just upstream of
Connor Creek (upper) and downstream of Quintonkon Creek (lower).
Clinger data (14 taxa, 72 percent of the sample) indicate that sediment was not a cause of impairment at
the upper site on Sullivan Creek. However, both the Mountain IBI score (71 percent) and the number of
EPT taxa (17) were slightly lower than the proposed supplemental indicators values. Bollman (2003)
noted that "clean, cold water" most likely existed at the time of sampling and "fine sediment deposition
did not substantially limit hard substrate habitats." Overall, it does not appear that siltation is impairing
the macroinvertebrate community at this site. Other metrics from the macroinvertebrate data show mixed
results. The HBI score was 1.27, which is lower than the recommended supplemental indicator of 3.5
(i.e., no apparent nutrient or sediment influences). None of the five most dominant taxa (Epeorus
deceptivus, Cinygmulci sp., Baetis tricaudatus, Drunella coloradensis, and Apatania sp.) are sensitive to
pollution.
There was no evidence of sediment impairment at the lower site either. There was a high number of
clinger taxa (16; 79 percent) and the Mountain IBI score was 76 (i.e., fully supporting beneficial uses).
Bollman (2003) noted that "cold water and excellent water quality" existed with no evidence of sediment
deposition. Only the number of EPT taxa (19) was slightly lower than the recommended value. The HBI
score (1.32) suggests that no sediment or nutrient impairments exist. None of the five most dominant taxa
(Cinygmula sp., Epeorus deceptivus, Baetis tricaudatus, Serratella tibialis, and Apatania sp.) are
sensitive to pollution. Overall, sediment does not appear to be impairing beneficial uses at the lower
Sullivan Creek site.
Periphyton
Periphyton data were collected at two sites on Sullivan Creek in August 2002: just upstream of Connor
Creek (upper site) and downstream of Quintonkon Creek (lower site). The siltation indices at both sites
was low (0.0 - upper; 0.23 - lower) and do not suggest impairment from sediment. Furthermore, Bahls
(2003) concluded that there were no overall impairments detected at the upper site and excellent water
quality was present. Slight impairments due to organic loading, which may be natural, were noted at the
lower site.
139
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Water Quality Impairment Status
Flathead River Headwaters TPA
Fish Population
MFWP conducted redd counts from 1993 through 2002 in Sullivan Creek and Quintonkon Creek (a major
tributary to Sullivan Creek). Counts for Sullivan Creek averaged 39.8 with a minimum number of 8 in
1994 and a maximum of 55 in 1999 (Figure 3-29) (Weaver et al., 2003). The data fluctuated over the 10-
year period, and there was no apparent trend over the period of record.
Quintonkon Creek redd counts averaged 9.8, and showed an increasing trend over time. Bull trout
populations were rated as "functioning acceptable" by the FNF (Van Eimeren, 2002).
(A
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10 -
n Sullivan
~ Quintonkin
EL
i i i i i i r
1993 1994 1995 1996 1997 1998 1999 2000 2001 2002
Figure 3-29. Bull trout redd counts in Sullivan Creek and Quintonkon Creek.
Pfankuch Ratings
Pfankuch ratings were completed in 1974, 1987, and 2002 at various locations in Sullivan Creek (Table 3-
37). The age of most of this information makes it of limited utility in evaluating current conditions. Data
collected in 2002 suggests that mass wasting, vegetative bank protection, and streambank cutting were
good at the upstream site. Almost no sediment deposition was observed at this site (excellent deposition
score). The Pfankuch ratings at the downstream site indicated worse conditions - large areas of mass
wasting were observed. Few riparian plants were observed and streambank cuts were significant. There
was also some sediment deposition (fair rating). However, the sampling site was located in an area of
unconsolidated sediments and glacial till, and some sediment erosion and deposition is to be expected.
This area has also historically been an area of high erosion and steep cutbanks, with the effects of the
1964 flood still evident (Stevens, personal communication, July 12, 2004).
140
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Flathead River Headwaters TPA
Water Quality Impairment Status
Table 3-37. Pfankuch Ratings for Segments of Sullivan Creek
Stream Segment
Year
Mass Wasting
Vegetative Bank
Protection
Cutting
Deposition
RM 1.96
1974
Excellent
Excellent
Fair
Fair
RM 3.85
1974
Excellent
Excellent
Fair
Fair
RM 4.69
1974
Good
Good
Excellent
Excellent
RM 6.87
1974
Good
Excellent
Good/Fair
Good
RM 9.85
1974
Poor
Fair
Poor
Fair
RM 3.65
1987
Poor
Fair
Fair/Poor
Fair/Poor
RM 3.96
1987
Poor
Fair
Fair/Poor
Fair/Poor
RM 6.90
1987
Fair
Good
Fair
Fair/Poor
RM 9.69
1987
Fair
Fair
Good/Fair
Fair
Upper Bridge
2002
Good
Good
Good/Fair
Excellent
Below
Quintonkon
2002
Poor
Fair
Fair
Fair
RM = river mile.
Suspended Sediment Concentrations
Suspended sediment concentration (SSC) data were collected in Sullivan Creek from 1978 to 1983 and
from 1985 to 1989 (n = 97). In general, samples were collected to capture spring runoff (in April, May,
and June) as well as base flow conditions (in July, August, September, October, and November).
However, the frequency of sampling varied from year to year. A lack of current data prohibits the use of
the older data for making a current impairment determination, but the data are useful in evaluating long-
term and historical trends. The mean for the period of record, mean annual maximum, and maximum
reported values are presented in Table 3-38. The values slightly exceed the proposed targets; however, it
should be noted that the targets are conservative since they were derived from a stream draining a 1,112
acre watershed compared with Sullivan Creek's 46,652 acres. For this reason, these data do not appear to
suggest sediment impairment, prior to 1989, associated with excessive suspended sediment loads.
Table 3-38. Comparison of Available SSC Data for Sullivan Creek with the Supplemental Indicator
Values
SSC Metric
Observed Value
(mg/L)
Indicator Value for Comparison (mg/L)
Mean (mg/L)
4.54
3.15 ฑ 5.83
Mean Annual Maximum (mg/L)
20.59
14.56
Maximum (mg/L)
63.57
61.60
Turbidity
Turbidity data were collected in Sullivan Creek for approximately the same period of record as for the
SSC data (1978-1989, n = 78). As with the SSC data, a lack of current data prohibits the use of the older
data for making a current impairment determination, but the data useful in evaluating long-term and
historical trends.
The mean turbidity for the period of record is 1.31 NTU and the median is 0.82 NTU. The maximum-
recorded value was 12 NTU in May 1986. No impairments are evident from the turbidity data.
141
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Water Quality Impairment Status
Flathead River Headwaters TPA
Riparian Assessment
An NRCS Visual Riparian Assessment was completed in 2002 (MDEQ, 2002). The overall stream reach
score was 95.5 percent, indicative of excellent riparian condition
Sources
Between 1929 and 2002, only 38 acres burned in the Sullivan Creek watershed. The most recent fire
occurred in 2003, burning 7,520 acres of land (16 percent). Effects of the fire are not evident in most of
the Sullivan Creek data because the data were collected before 2003 (and during a long period of time
with minimal fire). Natural sediment contributions will most likely increase in the future because of the
severity of the 2003 fire.
Since 1960, approximately 6 percent of the watershed has been clear-cut (FNF, 2003). Since 1984, only
60 acres of land have been clear-cut. The ECA for 2004 is 15.7 percent, which is below the supplemental
indicator of 25 percent and influenced by the 2003 fire. Because few acres have been recently clear-cut,
and only a small portion of the total watershed has been historically cut, it appears that clear-cutting
should have minimal impacts on stream water quality.
The FNF identified active upland erosion areas during the 2003 source assessment survey. Road density
in the watershed is 0.96 miles per square mile, which is rated "properly functioning" by Forest Service
criteria. A total of 103 road/stream crossings were identified, and 17 were at risk of failure. Only 7.5 of
69.8 road miles were located within 125 feet of a stream (25.7 miles within 300 feet). Portions of 33
miles of historical roads need to be evaluated for drainage problems that input sediment directly into
stream networks.
In summary, it appears that forest fires and logging have had minimal impacts on water quality in
Sullivan Creek (1984 through 2002). Several road issues were identified regarding poor road-stream
crossings and historical roads that may need BMPs. However, the extent of water quality impacts from
roads is unknown.
Sullivan Creek Water Quality Impairment Summary
The cold-water fishery and aquatic life beneficial uses in Sullivan Creek were listed on the 1996 303(d)
list as impaired because of habitat alterations. MDEQ lacked sufficient credible data to include this water
body on the 2002 303(d) list. The basis for the 1996 listing is unknown. As a result, reassessment
sampling was completed for Sullivan Creek in August 2002. A summary of the available sediment data is
presented below and in Table 3-39.
Overall, it appears that siltation is not currently impairing beneficial uses in Sullivan Creek. No siltation
was evident in the pebble counts, and the number of dinger taxa were higher than the target at two sites.
Information for the other targets (McNeil cores and substrate scores) was not available.
Supplemental indicators generally suggest good conditions in Sullivan Creek as well. Bull trout redd
counts fluctuated over a 10-year period of sampling, but showed no apparent trends. The periphyton
siltation index was very low (good) at two sites. SSC and turbidity values, although old, were low and
similar to reference conditions. Clear-cut land is most likely not a major source of sediment because only
a small percentage of the watershed has historically been clear-cut, and very little since 1984. At the
upstream site, macroinvertebrate data indicate that aquatic life uses may be slightly impaired. However,
Bollman (2003) noted that the data did not suggest that sediment was the cause of the impairment, and
that "clean, cool water" was most likely present at the time of sampling. The Mountain IBI indicated full
support at the downstream site. Good or excellent conditions were noted in the Pfankuch data at the
upstream site, although not the downstream site. The fair ratings at the downstream site are thought to be
142
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Flathead River Headwaters TPA
Water Quality Impairment Status
due to natural conditions. A recent NRCS survey found excellent conditions in Sullivan Creek. Overall,
the aquatic life and fishery beneficial uses do not appear to be impaired because of sediment in Sullivan
Creek.
Table 3-39. Comparison of Available Data with the Proposed Targets and Supplemental Indicators
for Sullivan Creek
Targets
Threshold
Upper
Lower
5-year Mean McNeil Core Percent
Subsurface Fines < 6.35 mm
35%
NA
5-year Mean Substrate Scores
> 10
NA
Percent Surface Fines < 2 mm
< 20%
13.1%
5.0%
Clinger Richness
> 14
14
16
Supplemental Indicators
Recommended Value
Upper
Lower
Juvenile Bull Trout and Westslope
Cutthroat Trout Density
Documented increasing or stable
trend
Bull: NA
Cutthroat: NA
Bull Trout Redd Counts
Documented increasing or stable
trend
Stable
SSC Mean
SSC Mean Annual Maximum
SSC Maximum
ฑ 5.2 mg/L
14.6 mg/L
61.6 mg/L
4.5 mg/L
20.6 mg/L
63.6 mg/L
Turbidity
High flow-50 NTU
instantaneous max
Summer base flow - 10 NTU
Mean: 1.31 NTU
Median: 0.82 NTU
Maximum: 12.0 NTU
Pfankuch Mass Wasting Score
"good"
Good
Poor
Pfankuch Bank Vegetation Score
"good"
Good
Fair
Pfankuch Cutting Score
"good"
Good/Fair
Fair
Pfankuch Deposition Score
"good"
Excellent
Fair
Montana Mountain Macroinvertebrate Index
of Biological Integrity
> 75%
71%
76%
Percentage of Clinger Taxa
"high"
72%
79%
EPT Richness
>22
17
19
HBI Score
3.5
1.27
1.32
Periphyton Siltation Index
< 20
0.0
0.23
Fire
Evaluated on a case-by-case
basis
Year: 2003
Acres: 7520
% Burned: 16
Equivalent Clear-Cut Acres
< 25%
15.7%
Water Yield
< 10%
NA
Roads
Evaluated on a case-by-case
basis
Some roads in need of BMPs
NRCS Riparian Assessment
> 75%
95% (Excellent)
143
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Water Quality Impairment Status
Flathead River Headwaters TPA
3.5 Water Quality Impairment Status Summary
The previous sections presented summaries of all available water quality data for waters appearing on
Montana's 1996 and 2002 303(d) lists. The weight-of-evidence approach described in Section 3.3 was
applied to the listed water bodies to address beneficial use impairments. Using this approach, aquatic life
and fishery beneficial use determinations were updated for each water body. A summary is presented in
Table 3-40. The South Fork Flathead River, Hungry Horse Reservoir, Big Creek, and Challenge Creek
have been addressed in other TMDLs or through MDEQ's 303(d) reassessment process and were
therefore not considered in this analysis.
As shown in Table 3-40, none of the evaluated stream segments except Lower Coal Creek are impaired as
a result of excessive levels of sediment. In Lower Coal Creek, the fishery beneficial use is impaired
because of habitat alterations and an unknown cause, possibly sediment. Due to the uncertainty in this
analysis, and to be proactive and protective of beneficial uses, a sediment TMDL will be developed for
Lower Coal Creek. Although it does not appear that nutrients are impairing beneficial uses in North Fork
Coal Creek, insufficient data are available at this time to make a final determination.
In summary, since no pollutants are currently causing impairments in Red Meadow Creek, Whale Creek,
South Fork Coal Creek, Granite Creek, Skyland Creek, Morrison Creek, and Sullivan Creek, no TMDLs
are necessary. However, implementation of a Voluntary Water Quality Improvement Strategy is
proposed to address all identified anthropogenic sources of sediment in those watersheds where human-
caused sources were identified (i.e., Red Meadow Creek, Granite Creek, Whale Creek, Sullivan Creek).
Necessary follow-up monitoring and a conceptual strategy to improve overall watershed health for these
water bodies is presented in Section 5.0. Because the fishery beneficial use in Lower Coal Creek is
impaired as a result of habitat alterations and an unknown cause (possibly sediment), a sediment TMDL
has been prepared and is presented in Section 4.0, along with load allocations, a restoration plan, and a
sediment monitoring plan. A study is also proposed to address the uncertainties in the Lower Coal Creek
beneficial use analysis, including a detailed habitat assessment in conjunction with a sediment source
assessment, and temperature monitoring to evaluate possible temperature impairments. Section 4.0 also
includes a monitoring plan to address the collection of supplemental nutrient data in North Fork Coal
Creek.
144
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Flathead River Headwaters TPA
Water Quality Impairment Status
Table 3-40. Current Water Quality Impairment Status for the Flathead River Headwaters TPA.
Water body
Name and
Number
Year
Listed
Listed Probable
Causes
Current Impairment
Status
Proposed Action
Red Meadow
Creek
MT76Q002-020
1996
Habitat alterations/Siltation
Not impaired
ฆ Implement Water Quality
Improvement Strategy to
address identified sources.
ฆ Conduct follow-up McNeil
core monitoring.
2002
Habitat alterations/Siltation
Whale Creek
MT76Q002-030
1996
Habitat alterations/Siltation
Not impaired
ฆ Implement Water Quality
Improvement Strategy to
address identified sources.
2002
Habitat alterations/Siltation
South Fork Coal
Creek
MT76Q002-040
1996
Habitat alterations/Siltation
Not impaired
ฆ Implement TMDL to
address identified sources
and habitat alterations.
ฆ Conduct habitat and
source assessment to
address uncertainties
ฆ Conduct follow-up nutrient
monitoring in North Fork
Coal Creek.
2002
Habitat alterations/Siltation
Lower Coal
Creek, SF to
confluence with
NF River
MT76Q002-080
1996
Siltation
Impaired for Habitat
Alterations and
Sediment
2002
Siltation
North Fork Coal
Creek
MT76Q002-070
1996
Nutrients/Siltation
Not impaired for
siltation. Unknown
for nutrients.
2002
Siltation
Granite Creek
MT76I002-010
1996
Habitat
alterations/Siltation/Suspended
Solids
Not impaired
ฆ No action
2002
Siltation/Bank Erosion
Skyland Creek
MT76I002-020
1996
Habitat alterations/
Siltation/Suspended Solids
Not impaired
ฆ No action
2002
Insufficient credible data
Morrison Creek
MT76I002-050
1996
Habitat alterations/Siltation
Not impaired
ฆ No action
2002
Habitat alterations/Siltation
Challenge Creek
MT76I002-040
1996
Habitat alter/Siltation
Not impaired
ฆ No action
2002
Not Listed
South Fork
Flathead River
MT76J001-010
1996
Habitat alterations
Flow alterations
Flow alteration
ฆ No action
2002
Flow alterations
Sullivan Creek
MT76J003-010
1996
Habitat alterations
Not impaired
ฆ Implement Water Quality
Improvement Strategy to
address identified sources.
ฆ Conduct follow-up McNeil
core monitoring.
2002
Insufficient credible data
Hungry Horse
Reservoir
MT76J002-1
1996
Flow alteration
Siltation
Suspended Solids
Not Impaired
ฆ No action
145
-------
-------
Flathead River Headwaters TPA
Coal Creek Sediment TMDL
4.0 COAL CREEK SEDIMENT TMDL
As discussed in Section 3.4.1.7, the cold-water fishery in Lower Coal Creek is impaired. The bull trout
population has failed to rebound in Lower Coal Creek unlike many of the other North Fork Flathead
River tributaries. The cause of this impairment is unknown. The fact that the substrate conditions are
slightly less than optimal when compared with the proposed threshold values may or may not explain this
impairment. Other factorssuch as physical habitat condition (e.g., large woody debris, number of pools,
barriers, stream temperature), high loads of sediment delivered to the stream from natural sources, or
historical anthropogenic sourcesmay be the cause. Or, perhaps, the impairment is caused by a
combination of factors. Given the uncertainty and to be protective of beneficial uses, a TMDL focusing
on addressing all known anthropogenic sediment sources and further study to identify the cause(s) of the
bull trout population decline are proposed. The required TMDL elements (i.e., identification of all
significant sources, water quality goals or targets, a TMDL, allocation, and margin of safety) are
presented in this section.
Although it appears that only Lower Coal Creek is impaired, this section of the document and all the
TMDL elements pertain to the entire Coal Creek watershed, from Coal Creek's confluence with the North
Fork Flathead River upstream to the watershed divide.
4.1 Significant Sources of Sediment in the Coal Creek Watershed
Potentially significant natural and anthropogenic sources of sediment loading to streams in the Flathead
River Headwaters TPA include fire, timber harvest activities, the forest road network including stream
crossings, bank erosion, mass wasting from avalanche chutes, natural soil creep, and stream down-cutting.
Each of these are discussed in the following subsections.
The FNF and MFWP conducted the most recent and comprehensive source assessments in the Coal Creek
watershed, looking at in-stream sediment conditions and potential upland sources of sediment. This
information, as well as information from additional analyses (GIS, and other reports), and personal
communications is summarized in the following subsections. The full MFWP and FNF reports are given
in Appendix B.
The conclusions presented herein have been developed from the best data available at the time this report
was prepared. Measured sediment loads from all sediment sources are not available; therefore, estimates
were made based on values in the scientific literature or were developed using various modeling
techniques. Further, detailed, on-the-ground assessments have not been conducted in the entire
watershed. As a result, interpolation was required and assumptions were made regarding conditions that
were not directly observed. However, it is felt that the information contained in the following subsections
allows reasonable comparisons to be made regarding the relative contributions of sediment from each of
the various source categories. Uncertainties are discussed in greater detail in Section 4.1.8, and a strategy
to address them is presented in Section 4.4.
147
-------
Coal Creek Sediment TMDL
Flathead River Headwaters TPA
4.1.1 Roads
Over the years, 125.3 miles of roads have been built in the Coal Creek watershed with a maximum road
density of 1.52 miles per square mile. Since 1995, 29 miles have been fully decommissioned following
FNF protocols, leaving a total of 96.3 road miles in 2004 (1.2 miles per square mile) (Figure 4-1). As
shown in Table 4-1, the majority of these roads (38.7 miles) are closed yearlong (i.e., not open to
motorized traffic that may cause increased erosion). Approximately 34 miles of roads are up to full
Forest Sendee BMP standards (Figure 4-2).
Table 4-1. Road Characteristics in the Coal Creek Watershed
Current Roads (mi)
Watershed
Closed
Seasonal
Open
Yearlong
Other
Total
Road
Miles
Number of
Road-Stream
Crossings
Watershed
Size (mi2)
Road
Density
(mi/mi )
De-
commissioned
(Since 1995)
Coal Creek
38.7
12.8
20.7
24.1
96.3
132
82.1
1.17
29.0
n
Streams
I i Coal Creek Watershed
a Road/Sediment Sources
Roads
/\/Closed Yearlong
/\/Decommission Since 1995
/V Historic Prior to 1995
Open Seasonally
/\J Open Yearlong
/\/ Other Roads
Streams
Figure 4-1. Location of roads in the Coal Creek watershed.
148
-------
Flathead River Headwaters TPA
Coal Creek Sediment TMDL
/\/Roads Up To BMP standards
Roads
Streams
I Coal Creek Watershed
i 9 \ %
Figure 4-2. Roads up to full BMP standards in the Coal Creek watershed.
In 2002 and 2003 the FNF evaluated all roads and road/stream crossings in the Coal Creek watershed to
determine whether they are currently contributing sediment to streams (see Appendix B for more detail).
If it appeared that a road segment was delivering sediment to a stream, loads were quantified using the
Forest Service's Water Erosion Prediction Model (WEPP-Roads). The WEPP-Roads model is described
in more detail online at http://forest.moscowfsl.wsu.edu/fswepp/.
According to the FNF survey, a total of 10 road sites deliver sediment to the stream network (Figure 4-1).
Average yearly loads are presented in Table 4-2. On average, approximately 1,000 pounds (0.5 ton) of
sediment are directly delivered to the stream network per year. Examples of road sediment sources
observed during the survey were plugged culverts at risk of failure, sediment slumps, and active streams
eroding the road prism (Figures 4-3 through 4-5).
It should be noted that road conditions have greatly improved in the FNF over the past several years.
Roads have been decommissioned or upgraded, and many road BMPs have been added (Figure 4-6).
With funding made available after the Moose Fire in 2001, upgrading to BMP standards on
approximately 26 miles of existing roadways was accomplished in 2002 and 2003. The reduction of
sediment and road runoff delivery to the stream channel network will decrease water and sediment yield
to streams by virtue of improved drainage from existing roads in the upper reaches of the watershed. The
BMP standards include the following:
149
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Coal Creek Sediment TMDL
Flathead River Headwaters TPA
The installation of drive-through dips (four to six per mile)
The installation of ditch relief structures as needed to prevent scour and divert ditch flow
away from stream channels and through adequate filtration zones
The placement of slash filter windows below roads where needed
The installation of sediment traps/basins above and below culverts as needed
The addition of flared inlet sections to culverts where needed
The replacement of 10 or more existing stream culverts with larger units designed to
accommodate a 100-year flood event and promote fish passage where applicable. This
also greatly reduces the risk of future culvert failure.
The FNF, in coordination with the Montana DNRC and MFWP, has overseen the road improvements to
ensure proper design of fish passage structures. The road improvement work will result in decreased
suspended sediment, decreased peak flow levels, and a decreased risk of sedimentation associated with
culvert failure.
Although there are relatively few road sources of sediment today, it is acknowledged that sediment
contributions from roads and road building activities were much higher in the past, and possibly have
contributed to the elevated in-stream sediment noted in Coal Creek.
Table 4-2. Sediment Loads from Roads in the Coal Creek Watershed3
Affected Stream
Map ID
Road #
Avg Sediment Leaving Buffer (lbs/year)
North Fork Coal
1
5278
304.31
South Fork Coal
9
1604
267.28
Tributary of Deadhorse Creek
7
1691
22.7
Tributary of Deadhorse Creek
8
1693
176.9
Tributary to North Fork Coal
2
5278
42.68
Tributary to North Fork Coal
3
5278
69.75
Tributary to North Fork Coal
4
5270
47.3
Tributary to North Fork Coal
5
5270
24.32
Tributary to North Fork Coal
6
5270
43.16
Tributary to North Fork Coal
10
317
0.64
Total
999.04
150
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Flathead River Headwaters TPA Coal Creek Sediment TMDL
Figure 4-4. Active stream eroding road prism on Figure 4-6. Example of BMP to divert water
Road 5278. from the road surface.
Figure 4-5. Plugged culvert on Road 1604.
-------
Coal Creek Sediment TMDL
Flathead River Headwaters TPA
4.1.2 Bank Erosion
Bank erosion is a natural process in streams, and can contribute a significant natural load of sediment.
However, anthropogenic sourcessuch as grazing, roads, riparian harvests, or flow modificationscan
lead to increased bank erosion. MFWP identified areas with significant bank erosion during the 2002-
2003 survey of the Coal Creek watershed, and the location of these sites is shown in Figure 4-7. Length
and height of the bank erosion were recorded in North Fork Coal Creek, South Fork Coal Creek, Mathias
Creek, and Lower Coal Creek upstream of the confluence with Deadhorse Creek. Examples of bank
erosion sites are shown in Figures 4-8 through 4-10. Most of the bank erosion noted during the survey
appears to be natural, although at one site (Site ID 1), bank erosion was due to an old road culvert that
was improperly removed.
Rates of bank erosion were calculated using estimates of near bank stress and stream bank erodibility in
conjunction with published literature values (Rosgen, 1996). Higher near bank stress or stream bank
erodibility results in higher rates of erosion. Overall, estimated rates of erosion ranged from 0.18 feet to
0.5 foot per year. The rate of erosion was then multiplied by the area of eroding bank (in square feet) to
obtain a volume of sediment per year, and then multiplied by the sediment density (i.e., average bulk
density of 1.3 grams per cubic centimeter; USDA, 1998) to obtain a mass of sediment per year.
Table 4-3 shows the results of this analysis. It is estimated that approximately 700 tons of sediment are
delivered to the stream network due to bank erosion per year. Approximately 0.1 ton per year appears to
be attributable to human activity. The remainder is thought to be largely a natural phenomenon.
It should be noted that not all streams in the watershed were assessed for bank erosion, and the survey
was conducted only on major streams upstream of the confluence with Deadhorse Creek. Therefore,
there may be more bank erosion than reported by MFWP. Further study is recommended to better
identify and quantify bank erosion in the Coal Creel watershed, and to address uncertainty in the current
analysis and a margin of safety (MOS).
152
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Flathead River Headwaters TPA
Coal Creek Sediment TMDL
Table 4-3. Estimates of Bank Erosion and Sediment Loads
Map ID
Height (ft)
Length(ft)
Area (ft*)
Near Bank
Stress
Erodibility
Bank
Erosion
Rate
(ft/year)
Sediment
Volume (ft3)
Sediment
Load
(tons/year)
1
1
20
20
moderate
moderate
0.18
4
0.1
2
16.4
33
541
moderate
high
0.3
162
6.6
3
6.6
65.5
432
moderate
high
0.3
130
5.3
4
3
30
90
moderate
high
0.3
27
1.1
5
32.8
50
1,640
moderate
high
0.3
492
20.0
6
197
98
19,306
moderate
high
0.3
5,792
235.0
7
66
66
4,356
moderate
high
0.3
1,307
53.0
8
7
10
70
moderate
high
0.3
21
0.9
9
10
50
500
moderate
high
0.3
150
6.1
10
20
66
1,320
moderate
high
0.3
396
16.1
11
33
82
2,706
moderate
high
0.3
812
32.9
12
33
50
1,650
moderate
high
0.3
495
20.1
13
8
33
264
moderate
high
0.3
79
3.2
14
60
164
9,840
high
high
0.5
4,920
199.7
15
33
115
3,795
high
high
0.5
1,898
77.0
16
20
82
1,640
moderate
high
0.3
492
20.0
Total
697.0
/\ Streams
[ ] Coal Creek Watershed i
Figure 4-7. Location of bank erosion sites in Coal Creek as identified by MFWP.
153
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Coal Creek Sediment TMDL
Flathead River Headwaters TPA
Figure 4-8. Bank erosion at Old Road culvert Figure 4-10. Bank erosion on North Fork Coal
(Map ID #1). Creek (Map ID #15).
Figure 4-9. Bank erosion on North Fork Coal
Creek (Map ID #13).
154
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Flathead River Headwaters TPA
Coal Creek Sediment TMDL
4.1.3 Fire
Fire can contribute to increased erosion because of increased surface water runoff and the removal of
vegetation, forest litter, and root masses. In 2001, the Moose Fire burned 14,938 acres (30 percent) of the
Lower Coal Creek watershed (See Figure 2-26). The FNF modeled the effects of the fire using the Water
Erosion Prediction Model (WEPP-Disturbed) and soil map units (Sirucek, personal communication,
August 3, 2004). A delivery ratio was then applied to the erosion value, because not all eroded soil makes
it to the stream. The model estimated an annual sediment load of 53,000 tons for 2003, or an average of
3.55 tons of sediment per acre per year. However, the WEPP model assumed that average rainfall fell in
the Coal Creek watershed in 2002 and 2003. This was not the case, as both 2002 and 2003 were
extremely dry years. Because of the low rainfall and low intensity storms, sediment loads from the
Moose Fire are most likely much less than predicted. Forest service personnel estimated that less than
one ton of sediment per acre of land was actually delivered to streams in 2003, or approximately 10,000
total tons of sediment (Sirucek, personal communication, September 20, 2004). The amount of erosion
due to the Moose Fire will continue to decrease in the future as the forest revegetates, and soils and water
yield stabilize (Figure 4-11).
Figure 4-11. Effects of the Moose Fire and vegetative regrowth since 2001 (Note the shrub and
herbaceous vegetation that has already resulted in excellent ground cover).
155
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Coal Creek Sediment TMDL
Flathead River Headwaters TPA
4.1.4 Harvest Activities
Harvest activities can also contribute to increased erosion because of increased water yields, ground
disturbances, and removal of binding vegetation. Since 1960, 18 percent of the Coal Creek watershed has
been harvested (9 percent intensive harvests), with 1 percent harvested since 1995 (See Figure 2-23).
Examples of harvested sites are shown in Figures 4-12 and 4-13.
Land harvested between 1995 and 2003 was modeled using the WEPP-Disturbed model. This period was
selected because land harvested 10 or more years ago most likely has little to no erosion today following
revegetation and decreased water yields. Parameters required by the WEPP model, such as slope gradient
and slope shape, were obtained from the FNF Soil Survey (USDA, 1998). Slope lengths were estimated
using Digital Elevation Models (DEMs) in a GIS. Ground cover was assumed to be 50 to 75 percent,
depending on the type of soil and slope. This range of values was chosen to represent the "worst case,"
recognizing that percent ground cover may be much higher in many areas. This conservative approach
was also chosen to represent a Margin of Safety (MOS), as required by the TMDL process. A delivery
ratio was then applied to the WEPP results to take into account the fact that not all eroded soil makes it to
a stream. Overall, the WEPP model estimated that 34 tons of sediment are contributed from harvest
activities per year, as calculated in 2003. This load will continue to decrease in the future as the forest
revegetates and water yields decrease.
It should be noted that past harvest activities may have contributed much more sediment than is being
contributed today. This "historical" sediment input may have contributed to the elevated bedload
sediment documented by the McNeil core and substrate scores.
Figure 4-13. Historical (1980s) clear-cut land
in the Coal Creek watershed.
Figure 4-12. Clear-cut land in the Coal Creek
watershed (Year 2000).
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Flathead River Headwaters TPA
Coal Creek Sediment TMDL
4.1.5 Other Potential Anthropogenic Sediment Sources
At the same time that roads were surveyed, FNF personnel verified previously mapped potential upland
sediment sources. Two previously compiled sediment source maps were available. In July 2002, the FNF
conducted a low-level helicopter reconnaissance flight over the Coal Creek watershed to transfer erosion
sites spotted from the air to orthoquads. During the 2002 field season, the sites from the orthoquad were
verified in the field to determine whether or not sediment was directly introduced into the stream network
Most of the previously identified sites were well vegetated and appeared to be stable. Overall, less than 2
acres of upland sediment sources were discovered that directly introduced sediment into stream networks.
The results from this study suggest that there are very few upland sources of sediment in the Coal Creek
watershed.
The MFWP survey found that an old skid trail resulted in the formation of a new stream channel in the
Mathias Creek watershed (Figure 4-14; Appendix B). MFWP estimates that approximately 4,950 tons of
sediment have been eroded over approximately a 45-year period. Equipment operation in this area also
has resulted in erosion (Figure 4-15). The extent to which these sources are actively contributing
sediment to the stream network is unknown at this time. Further study is recommended to determine the
extent to which these sources are currently eroding and to develop a restoration strategy, if necessary.
Several other upland sources of sediment exist in the Coal Creek watershed. Avalanche chutes, stream
down-cutting, and mass slumping are three natural sources of sediment. Sediment loads from these
sources have not been quantified. Given the results of the FNF source assessment surveys, it is assumed
that the loads from these sources are largely natural in origin.
Figure 4-14. Old skid trail with stream
formation in the Mathias Creek watershed.
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Coal Creek Sediment TMDL
Flathead River Headwaters TPA
4.1.6 Large Woody Debris
It is important to understand the condition of large woody debris (LWD) because of its relationship to
aquatic life, channel formation, and sediment transport. LWD helps to create pools and trap sediment, and
provides essential fish and aquatic life habitat. LWD also has the potential to drastically alter flows and
shift stream channels. Too much or not enough LWD can lead to altered sediment transport/deposition
and poor aquatic life habitat.
MFWP evaluated the condition of LWD in several stream segments in Coal Creek. Three general
classifications of LWD were derived from the MFWP study and are described below.
Normal - normal or expected amounts of LWD in the stream, resulting from natural
processes (wind blown trees, beaver activity, fire, normal forest processes). This
classification represents reference conditions.
High - excessive amounts of LWD in the stream due to human activities (e.g., harvest,
roads), causing an excessive number of LWD dams and sediment traps. Large amounts of
LWD due to fire are considered "normal."
Low - low or less than expected amounts of LWD in the stream. This recognizes that some
streams may have a LWD deficit due to harvest or other activities that may remove LWD
from the stream channel.
The results from the MFWP assessment are shown in Table 4-4. There were a variety of conditions noted
in the Coal Creek watershed, some of which warrant further investigation and possible restoration.
Segments with "high" or "low" amounts of LWD should be considered for future restoration. Detailed
field notes from the MFWP survey, including source locations, are shown in Appendix B. Feature
locations are plotted in Figure 4-16, and the corresponding numbers refer to the reference Map IDs in the
MFWP report. Figures 4-17 through 4-19 provide examples.
In contrast to the MFWP study, Hauer et al. (1999) found that there was no relationship between the
frequency of LWD in reference watersheds and managed watersheds in northwestern Montana, including
Coal Creek. This points out that there is some uncertainty over the extent to which LWD is, or is not,
influencing water quality and the cold-water fishery in Coal Creek. It should be noted that it is difficult to
assess the condition of LWD in a stream and its implications for water quality, since the quantity and
distribution of LWD is a function of both natural and human phenomena that often occur over very long
periods of time. Nevertheless, the potential implications of LWD should be considered relative to the
current bull trout situation in Coal Creek.
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Coal Creek Sediment TMDL
Table 4-4. Large Woody Debris Conditions in Selected Tributaries in the Coal Creek Watershed
Segment
LWD Condition
Unnamed Trib to Mathias Creek
Low, harvest-related (upper): High (lower)
Mathias Creek
Upper: Normal; Lower: High
South Fork Coal Creek to Confluence with Mathias Creek
Normal
South Fork Coal Creek, confluence w/ Mathias to Electrofishing section
Low, riparian harvest-related
South Fork Coal Creek, Electrofishing section to main Coal Creek
Low, riparian harvest-related and channel
straightening
North Fork of North Fork Coal Creek
High
North Fork Coal Creek (to the confluence with North Fork of N. Fork
Coal Creek
Normal
North Fork Coal Creek from confluence of N. Fork N. Fork to coring site
Normal
North Fork Coal Creek, coring site to 2 miles upstream of S. Fork Rd
Bridge
Normal
North Fork Coal Creek, 2 miles upstream of S. Fork Rd Bridge to the
Bridge
Low, riparian harvest-related, possible
channel straightening
North Fork Coal Creek, S. Fork Rd Bridge to just past the confluence
with the South Fork
Normal
Just below confluence with South Fork to Deadhorse Creek
High, partially due to fire
O
O
LWD Braidingi'Ac cumulating deposit*
LWD Deposit site, FdneiJGravels
New LWD recruitment
Mo new LWD reefultmerat
Riparian toflglnfl
Likes
Streams
Coal Creek Watershed
Figure 4-16. Location of LWD sites.
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Flathead River Headwaters TPA
Figure 4-19. Accumulation of LWD with
accumulating deposits.
Figure 4-17. Portion of Coal Creek artificially
straightened; lack of LWD.
Figure 4-18. Accumulation of LWD with
accumulating deposits.
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Coal Creek Sediment TMDL
4.1.7 Summary of Sources
Currently, the major sources of sediment in the Coal Creek watershed are bank erosion and overland
erosion caused by the Moose Fire. Relative to these two sources, anthropogenic sediment loading (i.e.,
from timber harvests, roads, and the one site of bank erosion caused by human activity) is very small.
Table 4-5 and Figure 4-20 summarize these sediment sources and present a relative comparison between
the evaluated source categories. Fire-related sediment is currently 92 percent of the sediment load in
Coal Creek, while harvests and roads are less than 0.1 percent of the total load. Bank erosion accounts for
approximately 6 percent of the total load. However, it is recognized that not all sources have been
documented, and future assessments are needed (See Section 4.5).
Sediment loading is a dynamic process that changes with harvest activities, fire, forest growth, and
precipitation/stream discharge. For example, Figure 4-21 shows that anthropogenic sources of sediment
would be a much larger percentage of the sediment load if there had been no fire in 2001. Also, current
sources of sediment are not always correlated with current in-stream sediment. In the past, sediment
loads may have been high because of harvests, roads, or floods. At that time, a high sediment load may
have been delivered to the stream, and still remains in the stream today. In-stream sediment loads (or
bedloads) take many years to flush out of the system. Therefore, a direct correlation does not always exist
between the current sediment load or current sources of sediment and the measured substrate condition in
a stream. The McNeil core and substrate fines data suggest that fine sediment in the bottom substrate
may be higher in Coal Creek than in other North Fork watersheds. However, there does not appear to be
a link between current anthropogenic sources of sediment and the in-stream sediment load, because
current anthropogenic sources of sediment are very low relative to natural sources.
Table 4-5. Summary of Sediment Sources in the Coal Creek Watershed
Sediment Source
Sediment Load
(tons/year)
Sediment Load (%)
Harvest
34
0%
Road
0.5
0%
Fire'1
10,000
92%
Bank Erosion2
697
6%
Mathias Creek Skid Trail/Historical Equipment Operation
194
2%
Total
10,926
100%
Based on Flathead National Forest estimates.
2 Not all eroding banks have been documented. The actual contribution from bank erosion is most likely higher than
reported.
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Flathead River Headwaters TPA
Mathias Creek Harvest Sediment
Skid Trail/Historic 0%
Figure 4-20. Distribution of sediment sources.
Harvest Sediment
Figure 4-21. Distribution of sediment sources (Without Moose Fire).
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Coal Creek Sediment TMDL
4.1.8 Source Assessment Uncertainty
As described above and in Appendix B, a substantial effort was made to identify all significant
anthropogenic sources of sediment loading in the Coal Creek watershed. Where possible, estimates of
sediment loads from each of the sources were also made. Although it is felt that this has resulted in
sufficient information to reach the conclusions presented in this report, there are still some uncertainties
regarding whether or not all of the significant sources have been identified, and regarding the
quantification of sediment loads. The primary uncertainties are as follows:
Bank erosion has not been thoroughly assessed in Coal Creek below Deadhorse Creek or in all
major tributaries.
The extent to which the old skid trail and eroded bank (shown in Figures 4-15 and 4-16) are
actively contributing sediment to the stream network is unknown.
The cause and effect relationship between large woody debris and bull trout in Coal Creek is
unknown and the extent to which human actions have altered the quantity and distribution of
large woody debris is unknown.
The extent to which past activities such as harvest and road building have affected Lower Coal
Creek is unknown.
These uncertainties will be addressed by the proposed activities described in Sections 4.3.6, 4.4, and 4.5.
4.2 Targets
As noted in Section 3.3, MDEQ is required to assess the waters for which TMDLs have been completed
to determine whether compliance with water quality standards has been attained. The process by which
this will be accomplished is discussed in Section 3.3 (Targets and Supplemental Indicators Applied as
Water Quality Goals) and is shown in Figure 3-3. The sediment targets listed in Table 3-6, and restated
below in Table 4-6, are proposed as the thresholds against which compliance with water quality standards
will be measured in Lower Coal Creek. If all the target threshold values are met, it will be assumed that
beneficial uses are fully supported and water quality standards have been achieved. Alternatively, if one
or more of the target threshold values are exceeded, it will be assumed that beneficial uses are not fully
supported and water quality standards have not been achieved. However, it will not be automatically
assumed that implementation of this TMDL was unsuccessful just because one or more of the target
threshold values have been exceeded. The circumstances around the exceedance will be investigated. For
example, the exceedance might be a result of natural causes such as floods, drought, fire or the physical
character of the watershed. In addition, in accordance with MCA 75-5-703(9), an evaluation will be
conducted to determine whether:
the implementation of a new or improved suite of control measures is necessary;
more time is needed to achieve water quality standards;
revisions to components of the TMDL are necessary, or;
changes in land management practices occur
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Table 4-6. Coal Creek Water Quality Goals
Water Quality Goal
Threshold
5-year Mean McNeil Core Percent Subsurface Fines < 6.35 mm
35%
5-year Mean Substrate Score
> 10
Percent Surface Fines < 2 mm
< 20%
Clinger Richness
> 14
4.3 TMDL and Allocations
A TMDL is composed of the sum of individual waste load allocations (WLAs) for point sources and load
allocations (LAs) for nonpoint sources and natural background levels. In addition, the TMDL must
include a margin of safety (MOS), either implicitly or explicitly, that accounts for the uncertainty in the
relationship between pollutant loads and the quality of the receiving water body. This definition is
denoted by the following equation:
TMDL = WLAs + LAs + MOS
There are no point sources of sediment in the Coal Creek watershed; therefore, the waste load allocation
for point sources can be removed from the equation. Furthermore, since people have no control over
natural sediment loading (e.g., most of the eroding banks, fire-related loading, natural avalanche chutes),
there is no practical purpose for considering natural loading in the TMDL equation. Therefore, the Coal
Creek TMDL is expressed merely as the sum of the allocations to the known anthropogenic nonpoint
sources. The hypothesis is that there is no more that can be accomplished to solve the problem if all the
current anthropogenic sediment sources are addressed. However, given that the estimated loads from
anthropogenic sources are very small in comparison with the estimated loads from natural sources, it is
not known whether reducing anthropogenic sources will result in significant improvements to the bull
trout fishery. Given the uncertainty of the link between current anthropogenic sediment loading and the
current health of the bull trout population, an unconventional "Phase II" allocation is also proposed. The
purpose of the Phase II allocation is to facilitate future study to (1) ensure that all of the anthropogenic
sources are appropriately addressed, and (2) better understand the non-pollutant issues that may be having
an impact on bull trout (e.g., large woody debris, physical habitat issues, channel morphology, barriers).
The TMDL and allocations are further summarized in Table 4-7 and are described in more detail in the
following paragraphs. The proposed restoration and adaptive management strategy is presented in
Section 4.5.
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Coal Creek Sediment TMDL
Table 4-7. Load Allocations for Sediment in Coal Creek
Sources
Current Load (tons/year)
Reduction
Allocation (tons/year)
or Approach
Point Sources
(WLA)
0
NA
0
Anthropogenic
Nonpoint Sources
(LA)
Existing Roads
0.5
75%
0.375 tons/year
0.125
Historical/Current
Harvest
34
100%
(34 tons/year)
0
Bank Erosion
0.1
90%
0.09 tons/year
0.01
Other3
Unknown
To be determined
To be determined
Future Roads and
Harvest
Not specified
Not specified
No sediment loading
increases other than
potential minor
predicted short-term
increases associated
with 100% compliance
with applicable BMP
standards.
Phase II -
Uncertainty and
Non-Pollutant
Issues
To be determined
To be determined
To be determined
aSee Sections 4.1.5 and 4.3.4 for a description of "other."
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4.3.1 Existing Road Allocation
As described in Section 4.1.1, 10 forest road-related sediment sources have been identified. This
allocation assumes that each of these affected road segments will be brought up to the Forest Service's
Road BMP Standards per Forest Service Handbook 2509.22, Soil and Water Conservation Handbook.
Based on best professional judgment, it is estimated that this will result in approximately a 75 percent
reduction in sediment loading from these sources.
4.3.2 Historical/Current Harvest Allocation
This source category is described in Section 4.1.4. The 100 percent load reduction assumes that the
anthropogenic increases in sediment loading from these harvest activities will decline over time with
forest regeneration and will eventually yield sediment at natural levels.
4.3.3 Bank Erosion Allocation
As described in Section 4.1.2, bank erosion appears to be one of the most significant sources of sediment
loading to Coal Creek. With the exception of one eroding bank that was obviously caused by human
activities (see Figure 4-8), the majority of the bank erosion is thought to be of natural origin. This
allocation, therefore, focuses on elimination/reduction of the anthropogenic source. This eroding bank is
a relatively small and localized phenomenon that appears to have resulted from the removal of an old
culvert. It is felt that the sediment load from this source can be virtually eliminated using conventional
engineering techniques; therefore, a 90 percent load reduction is proposed.
Although no other load reductions are currently sought from eroding banks, further study is proposed (see
Section 4.3.6) to ensure that there are no other bank erosion sites caused by human actions that need to be
addressed.
4.3.4 Other Allocation
As discussed in Section 4.1.5, MFWP identified two areas (shown in Figures 4-15 and 4-16) that appear
to have contributed a significant load of sediment to Coal Creek in the past. At this time, it is not known
whether sediment loading from these two areas is still significant. Further study is necessary to assess the
current situation and determine whether or not sediment loading from these sites is significant. These
sources will be addressed as part of the Phase II studies described in Section 4.3.6.
4.3.5 Future Roads and Harvest Allocation
It is not reasonable to assume that there will be no future silviculture activities in the Coal Creek
watershed. An allocation is therefore required to account for potential future sediment loading. This
allocation proposes no future sediment loading increases associated with harvest and/or forest roads other
than potential minor, short-term increases that may be predicted and associated with 100 percent
compliance with the applicable best management practice (BMP) standards.
4.3.6 Phase II Allocation Strategy
The Phase II Allocation Strategy is primarily intended to address the uncertainty associated with the
hypothesis that treating all known anthropogenic sediment sources will result in an improvement to the
bull trout fishery. This will be accomplished by implementing the Monitoring and Restoration Strategies
described in Sections 4.4 and 4.5, below.
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Coal Creek Sediment TMDL
4.4 Monitoring and Assessment Strategy
The purpose of the monitoring strategy is to provide answers to the following questions:
1. Has implementation of this plan resulted in attainment of water quality standards and full
support of the cold-water fishery beneficial use? (i.e., trend and compliance monitoring)
2. Have all the significant anthropogenic sediment sources been identified? (supplemental
monitoring)
3. Are other factors such as physical habitat limitations, stream channel morphology, and fish
barriers having a significant negative impact on bull trout in Coal Creek? (supplemental
monitoring)
4. Is North Fork Coal Creek impaired because of excessive anthropogenic nutrient loading?
(North Fork Nutrient Assessment)
It is envisioned that the first step in the implementation of this monitoring and assessment strategy will be
the development of a detailed work plan and sampling and analysis plan.
4.4.1 Trend Monitoring
MFWP has collected McNeil core, substrate score, bull trout population, and redd count data annually in
North Fork Coal Creek, South Fork Coal Creek, and Lower Coal Creek since the early 1980s. Continued
annual monitoring for these parameters within these water bodies is recommended. In addition, surface
fines and macroinvertebrate data should be collected on roughly a 5-year basis to facilitate application of
all the targets described in Section 4.2.
4.4.2 Supplemental Monitoring
Additional monitoring is also suggested to better assess channel, bank, and habitat conditions and to
collect supplemental information regarding potential sources of sediment within the watershed. The
following activities are recommended:
Conduct a complete Rosgen Level II survey of the entire Lower, North Fork, and South Fork
Coal Creek segments and suitable reference streams or segments.
Conduct a quantitative large woody debris inventory of Lower, North Fork, and South Fork Coal
Creek segments and suitable reference streams or segments.
Conduct additional supplemental source assessment surveys to address the uncertainties identified
in Section 4.1.8.
Install temperature data loggers to assess the potential effect of temperature on bull trout
populations.
Evaluate the condition of permanent cross sections and longitudinal profiles established in 2003.
4.4.3 North Fork Nutrient Assessment
EPA conducted additional monitoring in August 2004 to provide supplemental data regarding the
potential nutrient impairment in North Fork Coal Creek discussed in Section 3.4.1.6. Samples were
collected following MDEQ field protocols (MDEQ, 2004) and analyzed for the following parameters:
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Field Parameters - Temperature, flow, dissolved oxygen, pH, turbidity, conductivity
Laboratory Parameters - total phosphorus (TP), nitrate plus nitrite (N02 + N03), total Kjeldhal
nitrogen (TKN), total nitrogen (calculated), ammonia, chlorophyll- a (benthic)
Biological Parameters - Periphyton, macroinvertebrates
When the laboratory results become available in 2005, they will be evaluated to make a final
determination regarding the water quality impairment status of North Fork Coal Creek relative to
nutrients. If it is found that anthropogenic sources of nutrients are not causing an impairment,
documentation will be provided to the MDEQ such that the 303(d) list status of this water body can be
changed in 2006 (i.e., the next 303(d) list to be prepared by MDEQ). If, on the other hand, it is
determined that anthropogenic sources of nutrients are causing impairment, a TMDL will be prepared.
4.5 Restoration Strategy
A phased restoration strategy is proposed. Phase I will involve implementation of the monitoring and
assessment strategy described above in Section 4.4. A parallel Phase I effort should involve developing
and implementing a detailed plan to obtain the sediment load reductions from the known anthropogenic
sediment sources for which allocations have been assigned in Section 4.3 (i.e., the existing roads and the
one anthropogenic bank erosion site).
Phase II will be defined through implementation of the Monitoring and Assessment Strategy. It may be
determined that large woody debris and physical habitat issues are the primary problem and passive
management (i.e., allowing the bed load and channel form to reach equilibrium naturally overtime) is the
best solution. On the other hand, it may be that a combination of active and passive management may be
necessary to solve the problem.
It is envisioned that implementation of Phase I and II will be a joint effort among MFWP, the FNF, and
Montana DNRC with some assistance from MDEQ and EPA. It is also likely that outside sources of
funding (e.g., Clean Water Act Section 319 grants, EPA Consolidated Funding Grants) will be sought for
implementation. Although the three primary agencies have agreed to apply for Phase I funding in 2004,
the schedule for implementation will be dictated by the availability of funding and resources.
4.6 Dealing with Uncertainty and Margin of Safety
Based on the available data evaluated in Section 3.4.1.7 and consideration of the fact that the majority of
the sediment load delivered to Coal Creek appears to be largely of natural origin, one could argue that no
TMDL is necessary for Lower Coal Creek. However, interpretation of the state's narrative water quality
criteria is not a "black-and-white" exercise. The relevant narrative standards prohibit harmful or other
undesirable conditions related to pollutant increases above "naturally" occurring levels. The beneficial
uses listed as impaired in Lower Coal Creek (cold-water fishery and aquatic life) experience a high degree
of "natural" variability as do many of the chemical and physical parameters used as targets or
supplemental indicators. Are we certain that anthropogenic sediment loads are or are not significantly
contributing to the bull trout declines? To be conservative and err on the side of water quality protection,
a TMDL has been prepared. In the case of Lower Coal Creek, this fact alone provides a substantial
margin of safety.
The phased allocation approach also provides a margin of safety by addressing the uncertainties regarding
the identification/quantification of sediment sources outlined in Section 4.1 and by providing for
additional study to better understand the potential causes of the bull trout decline.
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Voluntary Water Quality Improvement Strategy
5.0 VOLUNTARY WATER QUALITY IMPROVEMENT STRATEGY FOR RED
MEADOW, WHALE, AND SULLIVAN CREEKS
As discussed in Section 3.0, the aquatic life and fisheries beneficial uses in Red Meadow, Whale, Granite,
Skyland, Morrison, and Sullivan creeks are not impaired. As a result, no TMDLs are required.
Nonetheless, minor sources of excess sediment from anthropogenic activities were identified in the
watersheds of Red Meadow, Whale, and Sullivan creeks. No significant sources were found during the
survey in the Granite Creek, Skyland Creek, and Morrison Creek watersheds (see Appendix B). Coal
Creek was discussed in Section 4.0. The Voluntary Water Quality Improvement Strategy presented in this
section is the first step in addressing these sources and improving overall watershed health in Red
Meadow, Whale, and Sullivan creeks. This strategy is conceptual, focusing on accurate identification and
prioritization of the sources, specifying any follow-up water quality monitoring that may have been
identified as a need in Section 3.0, and providing a conceptual implementation strategy. Site-specific
designs or plans are not presented herein. It should be noted that, relative to Section 303(d) of the Clean
Water Act or the Montana Water Quality Act, implementation of this strategy is not required.
Implementation is voluntary. It is envisioned that the Forest Service will address these sources when
funding and resources are available following standard Forest Service protocols on a case-by-case basis
for the purpose of improving watershed and aquatic health.
5.1 Identified Potential Sediment Sources
The FNF completed a comprehensive source assessment for Red Meadow Creek, Coal Creek, Whale
Creek, Skyland Creek, Granite Creek, Morrison Creek, and Sullivan Creek in 2002 and 2003 (FNF,
2003). GIS, aerial photos, aerial verification, and field verification were used to locate and describe
potential sources of sediment. The FNF fish passage team also completed field surveys at all road/stream
crossings on perennial streams. Additional potential sources of sediment are addressed in Section 2.0 of
this document (Section 2.1.9, Harvest History; Section 2.1.10, Fires; Section 2.1.11, Roads).
Table 5-1 summarizes sediment sources in the evaluated watersheds. Sources are summarized into five
major categories: fire, clear-cuts/equivalent clear-cut acreage (ECA), roads, other natural sources of
sediment (e.g., naturally eroding banks, avalanche chutes), and other anthropogenic sources of sediment.
Overall, minor sources were found in almost all of the watersheds. Fire, timber harvest, and roads were
the major sources of sediment, to varying degrees, in each watershed. Figures 5-1 through 5-3 show
examples of the sediment sources and their locations as found in the FNF survey.
5.2 Monitoring Strategy
Continued annual McNeil core, substrate score, bull trout population, and redd count monitoring is
proposed in the streams currently monitored by MFWP (Red Meadow Creek, Whale Creek, Granite
Creek). The intent is to continue tracking trends in these important bull trout habitats. As noted in
Section 3.0, no McNeil core data have been collected in Skyland or Sullivan creeks and no recent data is
available for either Red Meadow or Morrison Creeks. Periodic (once every five-years) McNeil core
monitoring is proposed for these three water bodies to complete the data set for the FTPA and provide
additional data to further support the impairment decisions that were presented earlier in this document.
5.3 Conceptual Implementation Strategy
As shown in Table 5-1, roads are the primary anthropogenic sources of sediment in need of mitigation in
the subject watersheds. Approximately 9, 21, and 33 miles of roads in the watersheds of Red Meadow
Creek, Whale Creek, and Sullivan Creek, respectively, need further evaluation to identify specific source
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areas and restoration strategies. In addition, a number of issues regarding culverts and stream crossings
need further evaluation to develop specific restoration strategies (Table 5-1 and Figures 5-1 through 5-3)
Implementation will first involve additional investigation to compile sufficient information to prioritize
restoration activities and to develop site-specific designs. Since all of the identified source areas are on
lands managed by the FNF, FNF will be responsible for the actual implementation of restoration
measures. The schedule for implementation will depend upon the availability of funding and resources.
Table 5-1. Potential Sources of Sediment in Selected Watersheds
Segment
Name
Type
Description
Fire
1988 Red Bench Fire (24% burned in lower part of watershed)
Harvests
13% clear-cut since 1960, last cut in 1990
ECA
12%
Red Meadow
Creek
Roads
Road 115-8 miles of road and crossings contributing sediment
Road 115A- 1 mile of road contributing sediment
Other Natural
Unknown
Other Non-
natural
Unknown
Fire
2003 Wedge Fire (12% burned in lower half of watershed)
Harvests
16% Clear-cut since 1960, last major cuts 1999/2000 (72 acres)
"Active upland sediment sources induced by timber harvest activities is not a
significant source of sediment in the Whale Creek drainage" (FNF, 2003).
ECA
14%
Whale Creek
Roads
Road 589 - five improperly removed culvert tank traps, sediment slumps,
and active streams eroding the road prism
11 (closed) road miles require work to reduce sediment (unspecified
locations)
10 (open) road miles contribute sediment at stream crossings or from relief
culverts that handle too much surface drainage (unspecified)
4 culverts need to be removed and channels restored (unspecified)
8 perennial stream culverts contribute sediment directly into streams
(unspecified)
Other Natural
Unknown
Other Non
Natural
Unknown
Fire
2003 Ball Fire (16% of watershed burned)
Harvests
6% clear-cut since 1960, last major cuts 1997 (24 acres)
ECA
15.7%
Sullivan
Creek
Roads
17 road/perennial stream crossings at risk
33 miles of old roads need to be evaluated for drainage problems
Other Natural
Unknown
Other Non-
natural
Unknown
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Voluntary Water Quality Improvement Strategy
Figure 5-1. Examples of sources of sediment in the Whale Creek watershed.
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Flathead River Headwaters TPA
Figure 5-2. Examples of sources of sediment in the Red Meadow Creek watershed.
172
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Flathead River Headwaters TPA Voluntary Water Quality Improvement Strategy
Figure 5-3. Examples of sources of sediment in the Sullivan Creek watershed
173
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Flathead River Headwaters TPA
Public Involvement
6.0 PUBLIC INVOLVEMENT
As described in Section 2.3.3, the FTPA is largely under federal ownership with the U.S. Forest Service
(Flathead National Forest) and National Park Service (Glacier National Park) as the primary land
owners/managers. Although only a minor landowner within the entire FTPA, the Montana Department of
Natural Resources and Conservation (DNRC) owns a significant portion of the land area within the Coal
Creek Watershed. Private land ownership comprises only a small portion of the total area. As such, the
primary land managers within the watershed include the Flathead National Forest, Glacier National Park,
and DNRC. Other significant stakeholders within the watershed include the Flathead Basin Commission,
due to their role in water quality throughout the entire Flathead Basin, and Montana Fish, Wildlife, and
Parks (MFWP), due to their active role in bull trout protection in the basin. This document was prepared
in close coordination with these primary stakeholders, with the exception of Glacier National Park. None
of the subject water bodies were located with the boundaries of the park.
A series of project level meetings were held with the Flathead National Forest, DNRC, and MFWP
including a meeting on July 14 and 15, 2004 at the Flathead National Forest office in Kalispell, Montana
to present and discuss a pre-public release draft of the document. Additionally, at this meeting,
conceptual plans were discussed regarding the development of a Section 319-grant application to
implement this TMDL. The draft document was also on the agenda and discussed at the July Flathead
Basin Commission meeting held in Lakeside, Montana. At that meeting, the FBC agreed to sponsor a
319-grant application for implementation of this TMDL. It was decided at that time that the "project
partners" for the implementation project would include the Flathead Basin Commission, Flathead
National Forest, DNRC, and MFWP.
The draft Water Quality Assessment and TMDLs for the Flathead River Headwaters Planning Area
document was formally released for public review on October 20, 2004 (Appendix F). The notice of
availability was made through a press release to the following media sources:
Associated Press
Bigfork Eagle
Daily Interlake
Hungry Horse News
Independent Record
KAJ TV-CBS
KALS FM
KCFW TV-NBC
KGEZ-FM
KOFI - AM/FM
Whitefish Pilot
Yellowstone Public Radio
Additionally, the notice was posted on the Montana Watershed Coordination Council's "list-serve" for
watershed issues ("WASHED@,listserv.montana.eduV The document was made available for review on
MDEQ's website (http://www.deq. state ,mt.us/index.asp).
The formal public comment period extended from October 20, 2004 to November 20, 2004, and a public
informational meeting was held on November 8, 2004. Formal written comments were submitted by five
individuals. A summary of the public comments and the EPA/DEQ responses are presented in
Appendix E.
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Flathead River Headwaters TPA
References
7.0 REFERENCES
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Barbour, M.T., J. Gerritsen, B.D. Snyder, and J.B. Stribling. 1999. Rapid Bioassessment Protocols for
Use in Streams and Wadeable Rivers: Periphyton, Benthic Macroinvertebrates and Fis. Second edition.
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Beschta, R.L., and W.S. Platts. 1986. Morphological features of small streams: Significance and
function. American Water Resources Association, Water Resources Bulletin 22(3): 369-379.
Bollman. W. 1998. Improving Stream Bioassessment Methods for the Montana Valley and Foothill
Prairies Ecoregion. Master's Thesis, University of Montana, Missoula, MT.
Bollman. W. 2003a. A Biological Assessment of Sites on Sullivan and Skyland Creeks: Flathead County
Montana. Project #TMDL-C08. Montana Department of Environmental Quality, Helena, MT.
Bollman. W. 2003b. A Biological Assessment of Sites on the North and Middle Forks of the Flathead
River Drainage, Flathead County, Montana. Montana Department of Environmental Quality, Helena,
MT.
Bukantis, R. 1998. Rapid Bioassessment Macroinvertebrate Protocols: Sampling and Sample Analysis
SOP's. Working draft, April 22, 1997. Montana Department of Environmental Quality, Planning
Prevention and Assistance Division, Helena, MT.
Chesnut, J. 1999a. Data Assessment Record for the 2002 303(d) List - Red Meadow Creek. Montana
Department of Environmental Quality, Planning, Prevention, and Assistance Division. Available at
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Department of Environmental Quality, Planning, Prevention, and Assistance Division. Available at
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Chesnut, J. 1999c. Data Assessment Record for the 2002 303(d) List - Morrison Creek. Montana
Department of Environmental Quality, Planning, Prevention, and Assistance Division. Available at
http://nris.state.mt.us/wis/environet/2002_303dhome.html. Accessed June 22, 2004.
Chesnut, J. 2000. Data Assessment Record for the 2002 303(d) List - Granite Creek. Montana
Department of Environmental Quality, Planning, Prevention, and Assistance Division. Available at
http://nris.state.mt.us/wis/environet/2002_303dhome.html. Accessed June 22, 2004.
Cilimburg, A.C., and K.C. Short. 2003. Forest Fire in the U.S. Northern Rockies: A Primer. Available at
http://www.northernrockiesfire.org/default.htm. Accessed June 29, 2004.
Constenius, Kurt N. 1996. Late paleogene extensional collapse of the Cordilleran Foreland Fold and
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Deleray, M., L. Knotek, S. Rumsey, and T. Weaver. 1999. Flathead Lake and River System Fisheries
Status Report. Montana Fish, Wildlife, and Parks, Kalispell, MT.
Dodson, M. H., 2001. Letter dated July 23, 2001 from Max H. Dodson, U.S. Environmental Protection
Agency, to Art Compton, Montana Department of Environmental Quality.
FBC (Flathead Basin Commission). 1991. Flathead Basin Forest Practices Water Quality and Fisheries
Cooperative Program: Final Report. Flathead Basin Commission, Kalispell, MT.
FNF (Flathead National Forest). 2003. Source Assessment Summary Conducted by the Flathead
National Forest in 2002 and 2003. Flathead National Forest, Kalispell, MT.
Ford, G.L., C.L. Maynard, J.A. Nesser, and D.S. Page-Dunroese. Landtype Associations of the
Northern Region: A First Approximation. USDA Forest Service. Available at
http://nris.state.mt.us/nrcs/soils/ltapage.html. Accessed June 16, 2004.
Galbraith, Alan F. 1973. A Water Yield and Channel Stability Analysis Procedure, Kootenai National
Forest, U.S. Forest Servic. In Forest Hydrology, Hydrologic Effects of Vegetation Manipulation, Part II.
December 1973.
Gray, J.R., G. Douglas Glysson, L.M. Turrios, and G.E. Schwartz. 2000. Comparability of Suspended-
Sediment Concentration and Total Suspended Solids Data. Water Resources Investigations Report 00-
4191. U.S. Geological Survey, Reston, VA.
Harrison, J.E., A.B. Griggs, and J.D. Wells. 2000. Geologic and Structure Maps of the Wallace lฐx 2ฐ
Quadrangle, Montana and Idaho: A Digital Database. USGS Miscellaneous Investigations Series Map I-
1509-A. U.S. Geological Survey.
Harrison, J.E., J.W. Whipple, and D.J.Lidke. 2002. Spatial Digital Database of Selected Data from the
Geologic Map of the Western Part of the Cut Bank 1ฐ x 2ฐ Quadrangle, Northwestern Montana. USGS
Geologic Investigations Series Map 1-2593. U.S. Geological Survey.
Hauer, F.R., and C.O. Blum. 1991. The Effect of Timber Management on Stream Water Quality.
Flathead Basin Commission, Kalispell, MT.
Hauer, F.R., and E. Hill. 1997. Analysis of1994-1996 Headwaters Monitoring Data: A Contribution to
the Master Plan for Monitoring Water Quality in the Flathead Basin. Flathead Lake Biological Station
Open File Report #140-97. Poison, MT.
Hauer, F.R., G.C. Poole, J.T. Gangemi, and C.V. Baxter. 1999. Large Woody Debris in Bull Trout
Spawning Streams of Logged and Wilderness Watersheds in Northwest Montana. Canadian Journal of
Fisheries and Aquatic Science 56: 915-924.
Hilsenhoff, W.L. 1987. An Improved Biotic Index of Organic Stream Pollution. Great Lakes Entomol.
20: 31-39.
Jones, J.A., and G.E. Grant. 1996. Peak Flow Responses to Clear-Cutting and Roads in Small and Large
Basins, Western Cascades, Oregon. Water Resources Research 32(4): 959-974.
King, J., and L.C. Tennyson. 1984. alteration of streamflow characteristics following road construction
in North Central Idaho. Water Resources Research 20(8): 1159-1163.
178
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References
King, J. 1989. Stream/low Response to Road Building and Harvesting: A Comparison with Equivelent
Clearcut Area Procedure. USDA Forest Service, Intermountain Research Station. INT-401.
Lundeen, L.J., and J.L. Hall. 1964. Flood Damage Report. Flathead National Forest, USDA Forest
Service.
Martinson, A., W.J. Basko. 1998. Soil Survey of Flathead National Forest Area, Montana. USDA Forest
Service in cooperation with Montana Agricultural Experiment Station.
MDEQ (Montana Department of Environmental Quality). 1996. Montana List ofWaterbodies in Need of
Total Maximum Daily Load Development. Montana Department of Environmental Quality, Helena, MT.
MDEQ (Montana Department of Environmental Quality). 2002. 2002 Montana 303(d) List-A
Compilation of Impaired and Threatened Waterbodies in Need of Water Quality Restoration. Montana
Department of Environmental Quality, Planning, Prevention, and Assistance Division. Helena, MT.
MDEQ (Montana Department of Environmental Quality). 2004. Montana Numeric Water Quality
Standards. Circular WQB-7 Montana Department of Environmental Quality, Planning, Prevention, and
Assistance Division Water Quality Standards Section, Helena, MT. Available online at
http: //www .deq. state .mt.us/wqinfo/Standards/Index. asp.
MFWP (Montana Fish, Wildlife, and Parks). 2004. Coal Creek Channel Survey - Preliminary Overview
2003. Montana Fish, Wildlife, and Parks. Kalispell, MT.
Mudge, M.R., R.L. Earhart, J.W. Whipple, and J.E. Harrison. 2001. Geologic and Structure Map of the
Choteau 1ฐ x 2ฐ Quadrangle, Western Montana: A Digital Database. USGS Miscellaneous
Investigations Series Map 1-1300. U.S. Geological Survey.
NMED (New Mexico Environmental Department). 2002. Protocol for the Assessment of Stream Bottom
Deposits on Wadable Streams. New Mexico Environmental Department, Surface Water Quality Bureau.
Santa Fe, New Mexico. Available at http: //www .nmenv. state ,nm .us/swqb/TMDL Library .html.
Accessed June 20, 2004.
Ott. 1993. An Introduction to Statistical Methods and Data Analysis - Fourth Edition. Duxbury Press.
Belmont, California.
Pfankuch, D.J. 1975. Stream Inventory and Channel Stability Evaluation: A Watershed Management
Procedure. USDA-FS. Northern Region. Rl-75-002. Government Printing Office, Washington, DC.
Pfankuch, D.J. 1978. Stream Reach Inventory and Channel Stability Evaluation. U.S. Department of
Agriculture, Forest Service, Northern Region.
Phillips. P. 2000. Data Assessment Record for the 2002 303(d) List - Coal Creek [Online]. Montana
Department of Environmental Quality, Planning, Prevention, and Assistance Division. Available at
http://nris.state.mt.us/wis/environet/2002 303dhome.html. Accessed June 22, 2004.
Rober, B.B., J.L. Kershner, E. Archer, R. Henderson, and N. Bouwes, 2002. An evaluation of physical
stream habitat attributes used to monitor streams. Journal of the American Water Resources Association.
December 2002.
Rosgen, D. 1996. Applied River Morphology. Wildland Hydrology. Pagosa Springs, CO.
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Rothrock, J.A., P.K. Barten, and G.L. Ingman. 1998. Land Use and Aquatic Biointegrity in the Blackfoot
River Watershed, Montana. Journal of the American Water Resources Association 34(3): 565-581.
Smith, Larry N. 2002. Surficial Geologic Map of the Upper Flathead River Valley (Kalispell Valley)
Area, Flathead County, Northwestern Montana. Ground-Water Assessment Atlas No. 2, Part B, Map 6.
Open-File Version January 2002. Montana Bureau of Mines and Geology.
Suplee. M. 1999a. Data Assessment Record for the 2002 303(d) List-North Fork Coal Creek. Montana
Department of Environmental Quality, Planning, Prevention, and Assistance Division. Available at
http://nris.state.mt.us/wis/environet/2002 303dhome.html. Accessed June 22, 2004.
Suplee. M. 1999b. Data Assessment Record for the 2002 303(d) List - Coal Creek. Montana Department
of Environmental Quality, Planning, Prevention, and Assistance Division. Available at
http://nris.state.mt.us/wis/environet/2002 303dhome.html. Accessed June 22, 2004.
USDA (U.S. Department of Agriculture). 1995. State Soil Geographic (SIATSGO) Data Base. U.S.
Department of Agriculture, Natural Resources Conservation Service. Available at
http://w ww.ncgc.nrcs.usda.gov/branch/ssb/products/statsgo/indcx.html. Accessed May 11, 2004.
USDA (U.S. Department of Agriculture). 1998. Soil Survey of Flathead National Forest Area, Montana,
Prepared in cooperation with Montana Agricultural Experiment Station, Natural Resources Conservation
Service, and U.S. Forest Service.
USEPA (U.S. Environmental Protection Agency). 1997. Revision to Rapid Bioassessment Protocols for
Use in Streams and Rivers: Periphyton, Benthic Macroinvertebrates, and Fish. U.S. Environmental
Protection Agency, Washington, DC.
USEPA (U.S. Environmental Protection Agency). 2000. Ambient Water Quality Criteria
Recommendations - Information Supporting The Development Of State And Tribal Nutrient Criteria For
Rivers And Streams In Nutrient Ecoregion II. U.S. Environmental Protection Agency - Office of Water.
EPA - 822-B-00-015.
Weaver, T., M. Deleray, S. Rumsey, G. Grisak, and C. Muhlfeld. 2003. Flathead lake and River System
Fisheries Status Report. DJ Report No. F-78-R-1 through 5, Element 1, Project 1 and 2, SBAS Project
No. 3130. Montana Fish, Wildlife, and Parks, Kalispell, MT.
Weaver, T, and J. Fraley. 1991. Fisheries Habitat and Fish Populations. Flathead Basin Forest
Practices Water Quality and Fisheries Cooperative Program. Flathead Basin Commission, Kalispell, MT.
Wolman, M.G. 1954. A method of sampling coarse river-bed material. Transactions of the American
Geophysical Union (EOS) 35: 951-956.
Woods, Alan J., James Omernik, M. John, A. Nesser, J. Shelden, and Sandra H. Azevedo. 1999.
Ecoregions of Montana (color poster with map, descriptive text, summary tables, and photographs); (map
scale 1:1,500,000). U.S. Geological Survey, Reston, VA.
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Appendix A
APPENDIX A: LANDFORM GROUPS IN THE FLATHEAD TMDL PLANNING
AREA
Valley Bottoms (VA)
Valley bottoms are low in the landscape and are composed of stream terraces, floodplains, glacial
outwash plains and outwash terraces. Parent materials are sands, silts, or gravels underlain by siltstones,
or glacial deposits. The dominant slopes have gradients of 2% to 20%. Fossil terraces have very steep
slopes on the front edge. The primary soils are deep with extremely gravelly sand and loam textures. The
vegetation is a mosaic of deciduous forest, coniferous forest, and wet meadows or shrubland. The riparian
vegetation is dominantly Abies lasiocarpa / Streptopus amplexifolius, Abies lasiocarpa / Calamagrostis
canadensis and Picea / Cornus stolonifera habitat types. Sensitive soils occur on the wet, poorly drained
flood plains and lacustrine deposits.
Breaklands (BK)
Breaklands occur in both upland and alpine landscape settings and are typically composed of structural
breaklands and stream breaklands. The dominant slopes have gradients of 55% to 70%. Parent materials
are volcanic ash overlying bedrock composed of argillites, siltstone, quartzite, dolomites, and limestone.
Structural breaklands are formed in colluvial materials from weakly weathered meta-sedimentary Belt
bedrock. Stream breaklands are formed in glaciofluvial material deposited during the last glacial epoch.
The dominant soils are shallow to moderately deep with very gravelly loam textures. The vegetation is a
mosaic of coniferous forest, and mountain shrub/grass lands.
The landform group is slight to moderately dissected by streams with sub-parallel and parallel stream
patterns dominant. Streams are ephemeral at higher elevations and perennial at lower elevations and are
typically classified as A or Aa+ types with gradients from 4% to greater than 10%. Straight (non sinuous)
cascading reaches, with frequently spaced pools are characteristic. Streams are very stable when flowing
through bedrock and boulders (A1 and A2) with low sensitivity to increases in water yields, peak flows or
sediment. When flowing through finer materials - cobbles, gravels, or sands (A3 or A4), disturbed stream
reaches can yield significant sediment.
The riparian vegetation is dominantly Abies lasiocarpa / Streptopus amplexifolius habitat type on poorly
drained sites. Small pockets of Abies lasiocarpa / Oplopanax horridum habitat type is dominant on poorly
drained soils. Sensitive soils occur on dissected breaklands that receive more than 50 inches of
precipitation per year.
Steep Alpine Glaciated Lands (STGLMS)
Steep alpine glaciated lands occur in upland and alpine landscape settings and are primarily composed of
glacial troughwall, cirque headwall, and cirque basin landforms. Parent materials are alpine glacial debris
and colluviums derived from and underlain by argillite, siltstone, quartzite, limestone, and dolomite
bedrocks. The landforms are typically high elevation and high precipitation areas. The vegetation is a
mosaic of coniferous forest, alpine meadows, and shrubland associated with avalanche chutes.
Glacial troughwalls are formed in glacial tills on lower elevation slopes with volcanic ash influenced
colluvium on the higher elevation slopes. Slope gradients range from 50% to 90%. Soils on the lower
slopes are moderately shallow to deep, are moderate to highly developed, and have cobbly medium
textures. The troughwall landforms are moderately to highly dissected by streams with parallel stream
pattern dominant. Streams are either 1st or 2nd order, intermittent or ephemeral at the higher elevations
and perennial at the lower elevations. Troughwall streams are characterized by moderate to high
entrenchment, moderate to high confinement, and low sinuosity and are classified as Aa+ or A types with
A-1
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Appendix A
Flathead River Headwaters TPA
gradients from 4% to greater than 10%. Straight cascading reaches with frequent pools characterize
streams within this landform. Streambeds of bedrock and boulders are typed as Al/Aa+1 or A2/Aa+2 and
are normally very stable. Large flows produced from either rain on snow events, or large spring runoffs
after wildfire events periodically erode the steep channels
Cirque headwalls and cirque basins are formed in glacial till on lower elevation slopes with volcanic ash
influenced colluvium on the higher elevation slopes. Slope gradients range from 5% to 90%. Soils are
shallow to moderately deep and weakly developed with very gravelly medium textures. The cirque basin
landform generates flatter gradient streams through finer materials (small boulder to clay size deposits)
than the troughwall landform. The streams are pre-dominantly B types with moderately steep gradients of
2% to 4% in narrow valleys with gently sloping sides. Riffles with frequently spaced pools are the
dominant characteristic. Under normal flow conditions, streams are very stable. Increased peak flows
through finer soil particles create streams moderately sensitive to channel erosion. Cirque lakes and
associated wetlands are a minor component of the cirque basin map unit.
The riparian vegetation is dominantly Abies lasiocarpa / Streptopus amplexifolius habitat type on poorly
drained sites. Small pockets of Abies lasiocarpa / Oplopanax horridum dominant habitat type occurs in
poorly drained soils. All cirque basins have sensitive soils. Glacial troughwalls have sensitive soils where
precipitation exceeds 50 inches per year.
Glaciated Mountainsides (GLMS)
Glaciated lands occur in both valley bottom and upland landscape settings and are primarily composed of
glacial moraine landforms. Parent materials are continental or alpine glacial debris with or without
volcanic ash surface layers. The soils are underlain by bedrock composed of argillites, siltstone,
limestone, dolomites, and quartzite. The dominant slopes range from 5% to 50%. In the valley bottoms
the glacial moraines create rolling hummocky topography with slopes ranging from 5% to 30%. On the
uplands the glacial moraines create straight to slightly concave slopes that range from 20% to 55%.
Glacial moraines typically occur at the base of glacial troughwalls. The primary soils are moderate to very
deep with very gravelly, coarse and medium textures. The major vegetative cover is a dense coniferous
forest with occasional meadow openings.
2nd to 4th order perennial streams have dissected the landform into a moderate to highly dendritic stream
pattern. Streams occupy narrow valleys with gently sloping sides, are characterized by low to moderate
entrenchment, low to moderate confinement, low to moderate sinuosity, and are typically classified either
A or B stream types. The A types have gradients from 4% to 10% with straight (non sinuous) cascading
reaches and frequently spaced pools. When flowing through boulders (A2) streams are very stable with
low sensitivity to increases in water yields, peak flows or sediment. The lower elevation flatter streams
are B types with gradients from 2% to 4%. Riffles are the dominant characteristic, with frequently spaced
pools. The streambed materials typically range from fine sand to small boulder in size, with gravel to
cobble size materials predominant. Large woody debris is the primary gradient control, unless stream
flow is through finer soil particles, leading to greater sensitivity to channel erosion from increased peak
flows.
The riparian vegetation is dominantly Abies lasiocarpa / Streptopus amplexifolius, Abies lasiocarpa /
Oplopanax horridium, Abies lasiocarpa / Calamagrostis canadensis, and Picea/Cornus stolonifera riparian
habitat types. Sensitive soils occur where this landform receives more than 50 inches of precipitation per
year.
Mountain Slopes and Ridges (MSRI)
Mountain slopes and ridges occur in both the upland and alpine landscape settings and are typically
composed of dissected mountain slopes, glaciated mountain slopes, and glacially scoured ridge tops. The
A-2
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Flathead River Headwaters TPA
Appendix A
geomorphic processes that occur on these areas include colluvial, fluvial and glacial, erosion or
deposition. Parent materials are volcanic ash overlying bedrock composed of argillites, siltstone,
quartzite, and limestone. The vegetation is a mosaic of coniferous forest, mountain shrub lands, and
mountain grasslands.
The landform group is a combination of glacially scoured ridge tops and dissected mountain slopes
(fluvial). Glacially scoured ridge tops have been strongly modified by continental ice. The prominent
features are ridge tops and ridge noses with exposed bedrock. These areas have slopes that range from
10% to 45%. Soils are shallow to moderately deep, and are weak to moderately developed with medium
textures. Slopes range from 30% to 60%.
The mountain slopes landform is moderately to strongly dissected by ephemeral and perennial streams
that occupy narrow "v" shaped valleys, with the dominant stream pattern either dendritic or sub-parallel.
Streams are typically classified as A or Aa+ types with gradients from 4% to 10% and are characterized
by straight (non sinuous) cascading reaches and frequently spaced pools. When flowing on bedrock and
boulders (A1 and A2) streams are very stable with low sensitivity to increases in water yields, peak flows
or sediment. The streams in the ridge top landform position occur at the heads of drainages and are
typically ephemeral or intermittent streams associated with seeps and springs.
The riparian vegetation is dominantly Abies lasiocarpa / Streptopus amplexifolius, Abies lasiocarpa /
Oplopanax horridium and Picea / Cornus stolonifera riparian habitat types. There are no sensitive soils in
this landform group.
Mass Wasted Slopes (MWSL)
This land type is a complex mixture of colluvial soils of various textures and residual soils on rolling to
steep mass failure lands. Soil permeability is rapid due to rock fracturing. Drainages are usually short and
dry with pattern defined by dominant rock fracturing or bedding. Seeps, springs and small ponds occur at
slope breaks. Slopes are complex and result from debris slides and rotational slumps. Topography is
subdued by secondary mass wasting on dipping bedrock associated with block gliding. Elevation ranges
from 4,000 to 6,000 feet above mean sea level. The parent material is predominantly residuum derived
from the underlying bedrock and colluvium deposited by mass failure. The parent material has a wide
variety of physical and chemical properties depending on the degree of weathering and the bedrock
source. The soils formed in colluvium occur on benches deposited by mass failure and are pale brown, silt
loam volcanic ash influenced loess. Slopes on benches of colluvium are 30%. Soils formed in residuum
occur on the steep scarps above the colluvial deposits and slopes are 50%. Residuum soils are brown,
very gravelly loam glacial till that is neutral to medium acidic. The residuum soils have 45% to 80%
angular coarse rock fragments.
The major habitat types on the benches with colluvium are Abies lasiocarpa / Clintonia uniflora, Abies
grandis / Clintonia uniflora, and Thuja plicata / Clintonia uniflora. The major habitat types on the scarps
that have residuum soils are Abies lasiocarpa / Xerophyllum tenax, and Abies lasiocarpa / Meniesia
ferruginea.
Frost Shattered Mountain Ridges (FSMR)
Oversteepened cirque headwalls and narrow alpine ridges formed of dipping glacial scoured slab bedrock
are the dominant characteristics of this landform group. The landform group usually surrounds
amphitheater shaped basins at the head of glaciated valleys, some containing tarns, with elevations
ranging between 4,000 to 8,000 feet above mean sea level. Slopes are convex and range from 40% to
60%.
A-3
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Appendix A
Flathead River Headwaters TPA
The sub parallel, first-order drainages within the landform group are controlled by the jointing and
fracture patterns of bedrock. Parent material consists of Precambrian quartzite, limestone, argillite and
siltite. 50% to 70% of these land types are composed of rock land covered by lichen. Talus slopes are
common. The remaining 30% to 50% of the ridges have thin, rocky soils that support trees, shrubs and
grasses. Shallow soils are formed in pockets of volcanic ash influenced loess mixed by colluvial drift and
frost churning.
The major habitat types found on soil pockets within the landform group are Abies lasiocarpa /
Xerophyllum tenax, Abies lasiocarpa / Vaccinium scoparium, Pinus albicaulis / Abies lasiocarpa, and
Larix lyalii / Abies lasiocarpa. The shallow pockets of soil that exist are sensitive.
A-4
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Flathead River Headwaters TPA Appendix B
APPENDIX B: FLATHEAD NATIONAL FOREST AND
MONTANA FISH, WILDLIFE, AND PARKS SOURCE
ASSESSMENTS
Flathead TMDL Planning Area
Source Assessment Summary
Conducted by the Flathead
National Forest in 2002 and 2003
B-1
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Appendix B
Flathead River Headwaters TPA
1.0 Introduction
Under an interagency agreement with the U.S. Environmental Protection Agency (EPA), the Flathead
National Forest (FNF) conducted a sediment source assessment survey in support of the development of
all necessary total maximum daily loads (TMDL) for the Flathead River Headwaters TMDL Planning
Area (FTP A). A summary of the methods and results of the survey are presented below.
2.0 Source Assessment
The 303(d) listed stream segments in the FTPA are listed as impaired for sediment. This document
describes the source assessment work completed by the FNF in 2002-2003 to evaluate potential sediment
sources in the TMDL watersheds. Three possible sediment sources were considered in the FTPA.
Potential sources include possible contributions from:
upland sources (e.g. soil loss resulting from forest harvest practices and timber management,
mass wasting);
localized influences and impacts to riparian areas (e.g. erosion from roads, road crossings,
riparian harvests).
instream sediment sources ( a survey was conducted for Coal Creek from headwaters to
confluence with Deadhorse by MFWP).
2.1 Upland Source Assessment
The FNF employed several techniques to determine possible sediment sources in the 303(d) listed
watersheds. The process consisted of the following steps:
To assess timber management impacts, GIS analysis of the harvest activity per watershed was
completed and acreage with high erosion potential was summarized.
Historical aerial photographs were reviewed to target both natural and timber-related sediment
sources and to prioritize field verification efforts.
A portion of the sediment sources identified in Steps 1 and 2 were field verified.
2.1.1 GIS Analysis
To determine the contribution of sediment attributed to harvest activity, areas with soil disturbance caused
by past management activities and with low vegetation recovery were identified using GIS. Data sources
used for analyzing the effects of timber management included the sediment hazard rating index (landtype
information such as landslide prone areas, steep slopes, eroable soils and soil types, sensitivity to
compaction, distance to stream network), and timber stand management history (extent of harvests, types
of harvest, dates of harvest) from the Timber Stand Management Records System (TSMRS) database.
The sediment hazard layer was overlain with the historic harvest layer and summarizations for each
harvest type within high sediment hazard zones were identified. The GIS analysis identified historically
managed areas with high potential to contribute sediment from previously harvested areas. The acreage
considered as potential soil erosion areas due to soil disturbance are provided in Table 2-1.
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Flathead River Headwaters TPA
Appendix B
Table 2-1. Summary of the Acreage Examined for Possible Sediment Contributions
Stream Segment
Historic TSMRS acres
Final acreage amended to
Percent of Final
with soil disturbance
TSMRS acres after historic
Acreage Field
identified with GIS
aerial photo review
Verified
Red Meadow
977
1028
72%
Whale Creek
1900
245
9%l
FNF Coal Creek
1270
1978
75%
Granite Creek
226
318
24%
Skyland Creek
136
73
17%
Morrison Creek
80
217
83%
Sullivan Creek
1524
NA2
NA
A higher percentage of final acreage was not assessed for Whale Creek because of the 2003 fires.
Sullivan Creek was considered fully supporting beneficial uses based on macroinvertebrate results from 2002
therefore; no sediment source analysis was completed.
2.1.2 Aerial Photographs
Historical aerial photographs were also evaluated for all 303(d) watersheds (with the exception of
Sullivan Creek) to identify potential sediment source sites left after timber management activities. The
photographs were at scale 1:16,000 and were taken in 1979, 1989, and 1999. The photos were examined
for changes in texture, color and pattern to detect potential sediment sources within old harvest sites,
especially skid trails and landings. Potential sediment sources from landslides, road cut banks and fill
slopes, or avalanche fans were also targeted for field verification. The potential sediment sites were
transcribed to orthoquads for the 303(d) drainages to facilitate finding them during field verification. The
total acreage values for the potential sediment sources increased in some drainages due to non-timber
management related sediment sources such as avalanche fans and road cut slopes. Other watersheds
showed a decrease in potential erosion acres estimates based on vegetation recovery after historic harvest
practices. Final numbers for potential erosion areas are provided in Table 2-1.
In July 2002, a low-level helicopter reconnaissance flight was conducted over 303(d) drainages within the
North Fork watershed. The Three Forks Zone (TFZ) hydrologist (Dean Sirucek), TFZ fisheries biologist
(Rick Stevens), and the FNF soil scientist (Bill Basko) identified potential sediment sources and
transcribed them to orthoquads for Whale, Red Meadow, and Coal Creek watersheds. The orthoquads
were used as guidance for field verification. The TMDL field crew visited each site to assess the
potential for sediment to be input to the stream network.
All topographic maps, aerial photo stereographic pairs, highlighted orthoquads, and field notebooks are
archived at the FNF Supervisors Office, Resources division.
2.1.3 Field Verification
The final step was to conduct a field visit to as many areas as possible to identify possible sediment
sources. The FNF field crew conducted a visual survey of each site during 2002 and 2003, assessing soil
and vegetation stability. Photographs were taken at sites with sparse vegetation recovery, particularly in
riparian zones. Based on field observations, the crew determined whether or not the site remained an
active sediment source.
2.1.4 Results
The majority of potential sediment sources on uplands were located on ephemeral and first-order streams
that had been crossed with roads. The FNF looked at areas of potential erosion with one major filter:
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Appendix B
Flathead River Headwaters TPA
Is sediment introduced directly into the active stream network? Active streams were defined as
channels with flowing water.
Based on the GIS analysis, estimation of current condition of historic timber management areas, aerial
photograph review, and field verification, active upland sediment sources induced by timber harvest
activities is not a significant source of sediment in the 303(d) listed watersheds.
2.2 Localized Sediment Contributions from Roads and Road/ Stream Crossings
Road surfaces and cut slopes are the primary sources of sediment in the FNF. Closing roads to vehicle
use reduces erosion by eliminating the formation of ruts and by reestablishment of vegetation on the
road surface. Road cuts on sensitive landtypes may continue to contribute sediment into ditches and first-
order drainage systems.
Sensitive landtypes have the potential to be sources of sediment. The determinant characteristic of
sensitive landtypes is an excess of water within the soil profile, usually on a seasonal basis, but in some
landtypes, year around. Sensitive landtypes in a natural undisturbed condition act as a temporary storage
site for water, allowing moisture to slowly move down slope until emerging as springs, wetlands, streams,
or percolating into groundwater. Disruption of this hydrologic function by management activities such as
road building or timber harvest can cause water held by sensitive landtypes to seep out and onto the road,
skid trail or landing, moving quickly down slope into streams. Additional water yield increases the risk
of sediment delivery to streams by the efficient routing of water over roads, skid trails and landings.
Sensitive landtypes are priority places to search for sources of sediment to streams caused from plugged
culverts, rutted roads, road ditches that concentrate large quantities of water, or old cutting units with
water running down skid trails, known as "skid streams". The big concern for sensitive land types is the
increase in water yield associated with disturbance. The increased drainage efficiency is the lasting
problem although increases in sediment are also a risk. Stream crossings per square mile indicate avenues
for road sediment to enter the drainage network (Van Eimeren, 1998). Potential sediment contributions
from roads were evaluated for all drainages. In 2002 and 2003, the FNF field crew completed driving and
walking surveys on all open, closed, decommissioned, and maintained roads in the 303(d) listed
watersheds (except Sullivan) to identify active sediment sources. Pictures and GPS locations were taken
at each site for compilation in the restoration plan and to forward to road managers for inclusion in road
maintenance plans. Table 2-2 provides summary information on stream crossings and roads located in
each watershed.
In 2002, the FNF fish passage team completed field surveys at all road /stream crossings on perennial
streams. Data compiled in 2002 by the fish passage field crews were reviewed to prioritize 2003 field
efforts. Field surveys in 2003 were completed at all road/stream crossings for intermittent streams to
determine culvert condition and sediment potential. The road/stream crossing survey evaluated the
culvert's risk of failure, erosion potential, and size. Culverts deemed to have a great risk of failing have
been targeted for replacement by the FNF, based on availability of funding.
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Flathead River Headwaters TPA
Appendix B
Table 2-2. Road / Stream Crossing Summary
Number of
Number of
Road/Stream
Road miles
Number of
Road/Stream
Crossings at
in need of
Road miles
Road miles
Stream
Road/Stream
Crossings
Failure Risk in
BMP's or
within 125'
within 300'
Segment
Crossings
Evaluated
the Watershed
upgrading
of stream
of stream
Red
Meadow
76
76
0
9
14.6
16.9
Creek
Whale
Creek
84
84
8
21
26.8
30.2
FNF Coal
Creek
142
135
16
40
13.8
34.9
Granite
Creek
16
16
2
18
1.7
5.5
Skyland
Creek
13
13
0
0
2.3
2.5
Morrison
Creek
5
5
0
0
6.9
1.7
Sullivan
Creek
103
55
Partially
completed
2003 with
BAER
Fire funds
Partially
completed
2003 with
BAER
Fire funds
7.1
25.7
3.0 Results
The results of the source assessment done for the 303(d) drainages are presented below in a series of maps
with photos. The 303(d) drainages are presented in order of priority for restoration based on assumed
impairment status, expectation of funding availability and projected improvement to conditions (reduction
of fine sediment in active stream network) for enhanced support of aquatic life and cold-water fisheries.
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Appendix B
Flathead River Headwaters TPA
3.1 Coal Creek
3.1.1 Road Survey results
Active upland sediment sources induced by timber harvest activities is not a significant source of
sediment in the Coal Creek drainage. The five pictures above illustrate the typical sediment source
problems found in the Coal Creek drainage. Eleven road / stream crossing sediment sources occur
throughout the drainage. The major sediment sources occur on Roads 5270 and 5278 in the North Fork
Coal, with three plugged culverts at risk of failure, sediment slumps, and active streams eroding the road
prism. North Fork Coal Creek drainage contains 8 perennial stream culverts that input sediment directly
into the stream network, 2 of which have partially failed and need to be removed and the stream channel
restored. Portions of 17 miles of bermed, closed roads contribute sediment into the stream network and
require work to reduce road sediment. There are 5 miles of heavily traveled road that require ditch
drainage improvements, water bars, drain dip installation, culvert inlet armoring, and relief culvert
installation to reduce sediment.
3.1.2 Stream Channel Survey Results
In the winter of 2002-2003 an interagency group convened to discuss stream habitat conditions in Coal
Creek, a tributary to the North Fork of the Flathead River. The group consisted of representatives, mostly
hydrologists or fisheries biologists, from the U.S. Forest Service, U.S. Fish and Wildlife Service,
Montana Department of Natural Resources and Conservation, and Montana Fish Wildlife and Parks
(MFWP). The group convened for several reasons, including declines in bull trout spawning, TMDL
planning, and observed in-channel erosion and sedimentation. The group met a number of times
including a fieldtrip to Coal Creek where we looked at active bank erosion. The outcome of these
meetings was concurrence that the group needed to work towards improving habitat conditions in the
stream. To do this, it was decided that we needed better information of existing channel conditions to
take a holistic approach to restoration. Prior to working on isolated locations within the drainage, the
group decided to do preliminary surveys of the forest road system, in-channel conditions, and water yields
within the drainage. The Coal Creek Working Group felt this baseline information was important in order
to proceed with a better likelihood of success. The report (Cavigili, 2004) completed by MFWP
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Flathead River Headwaters TPA
Appendix B
addresses the in-channel stream habitat conditions in Coal Creek and its tributaries upstream of the
confluence with Dead Horse Creek.
From the information collected during that survey, MFWP were able to produce an overview of channel
conditions in the drainage and provide information in a format that allows others to view channel
conditions and assess the current status. This will allow members of the interagency working group and
others to direct future restoration efforts. The MFWP report consists of six parts. These paragraphs are
the introduction to that document summarizing the preliminary channel survey and containing
methodology, and summaries of general channel conditions for four stream reaches.
Prior to this survey, a very similar survey was conducted in 1988 (Weaver, Tom. 1989. Coal Creek
Fisheries Monitoring Study NO. VII and Forest-Wide Fisheries Monitoring-1988. Montana Fish,
Wildlife and Parks, Kalispell, MT). The FNF and Montana Fish Wildlife and Parks conducted this earlier
study through a cooperative effort. This report provided a narrative description of stream features
beginning in the headwaters and working downstream identifying sediment sources, bank instability
concerns, and restoration measures. This report stated that there were highly unstable channel areas in
each of the three major forks in the Coal Creek drainage. The vast majority of the problems were related
to land-management, logging and road building activities of the 1950's and 1960's. It noted that
sediment generated decades ago continued to cause channel instability and erosion in the late 1980's.
Since the 1980's, there had been a number of road improvement projects on federal and state lands to
improve stream crossings and road drainage. However, a number of the problems observed in the 1988
report had not been addressed. The 2003 survey aimed to repeat the 1988 survey and determine current
status of and if there were major changes in channel condition. MFWP personnel (Jon Cavigli, Tom
Weaver, and Mark Deleray) split the roughly 28 miles of stream between the three recorders, which took
15 person-days. For reporting purposes, MFWP broke the river miles into four reaches. One reach was
Mathias Creek and its tributaries down to its confluence with the South Fork of Coal Creek. The second
was the South Fork of Coal Creek from the headwaters down to the confluence with main Coal Creek.
The third was the upper two forks of main Coal Creek. And the forth reach was main Coal Creek from
the confluence of the upper two forks down to the confluence with Dead Horse Creek. Starting at the
headwaters or upstream end of a reach, observers walked downstream noting in-channel sediment
deposits, eroding banks or other sediment sources. Major features were noted in narrative field notes,
digital photographs, and GPS coordinates. Digital photos and GPS coordinates may not be available for
some reaches due to availability of equipment. This survey provides a qualitative overview of channel
conditions that can be compared to similar information from the 1988 report and provide a holistic view
of the drainage to direct future surveys and restoration needs (Cavigili, 2004).
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Appendix B
Flathead River Headwaters TPA
3.2 Whale Creek
3.2.2 Road Survey results
Active upland sediment sources induced by timber harvest activities is not a significant source of
sediment in the Whale Creek drainage. The five pictures above illustrate the typical sediment source
problems found in the Whale Creek drainage. Eight road / stream crossing sediment sources occur
throughout the drainage. The major sediment sources occur on historic road 589 in the Shorty Creek
tributary, with five improperly removed culvert tank traps, sediment slumps, and active streams eroding
the road prism. Whale drainage contains 8 perennial stream culverts that were installed in a manner that
contributes sediment directly into the stream network. The road system within the drainage contains
approximately 11 road miles that are closed to traffic and require work to reduce sediment. There are 10
road miles that are open to traffic that contribute sediment at stream crossings or from relief culverts that
handle too much surface drainage. Four culverts need to be removed and channels restored.
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Flathead River Headwaters TPA
Appendix B
3.3.3 Road Survey results
Active upland sediment sources induced by timber harvest activities are unknown in the
Sullivan/Quintonkin drainage. The five pictures above illustrate the typical sediment sources found by
the fish passage crew in the Sullivan/Quintonkin drainage in 2002. There are 17 road/perennial stream
crossings at risk in the Sullivan/Quintonkin drainage. Portions of 33 miles of historic roads need to be
evaluated for drainage problems that input sediment directly into stream networks. In 2003, the Ball Fire
burned approximately 7520 acres in the Sullivan/Quintonkin drainage. Bum Area Emergency Restoration
(BAER) addressed immediate sediment sources within the burn area and independent fire suppression
rehabilitation was conducted on reopened roads and fire lines to address risks to watershed health directly
because of fire suppression efforts.
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Appendix B
Flathead River Headwaters TPA
3.4 Red Meadow Creek
3.4.1 Road Survey results
Red Meadow drainage contains approximately 15 acres of historic harvest within high altitude, NE
aspect, steeply sloping riparian zones that have not yet attained full vegetative recovery. Planting native
trees, shrubs, and grasses would restore riparian zone health and reduce potential for mass failures and
sediment input into first order tributaries. The main access road (Road 115) has 8 miles of road currently
contributing sediment into Red Meadow Creek. This road needs improved drainage at first-order stream
crossings and more ditch relief culverts to reduce sediment. Approximately 1 mile on Road 115A needs
grading, ditch relief, water bars, and culverts unplugged to reduce sediment and provide access across the
Whitefish divide for a popular driving loop and access for hikers and horses to trailheads into upper lakes.
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Flathead River Headwaters TPA
Appendix B
3.5 Granite Creek
3.5.1 Road Survey Results
Active upland sediment sources induced by timber harvest activities are not significant sources of
sediment in the Granite drainage. Roads to Granite are accessed through the Skyland drainage. The
TMDL road survey did not find any sediment source problems at road/' stream crossings outside normal
road maintenance parameters. Granite Creek is formed by the confluence of Challenge and Dodge
Creeks. The main problem for aquatic life support and cold-water fisheries in the Granite Creek drainage
is channel dewatering. The stream channel occupies a wide alluvial valley that has experienced historic
riparian harvests. The historic timber management units are well vegetated and the historic haul roads are
bermed or gated to prevent traffic.
3.5.2 Stream Channel Survey Results
A walk-down stream survey was conducted from the confluence of Dodge and Challenge to the
wilderness trailhead in an attempt to obtain a macroinvertebrate sample for Granite Creek. The discharge
from Dodge Creek was dry and the discharge from Challenge Creek continued downstream from the
confluence approximately 50 meters before plunging below the surface. The channel intercepted
groundwater again at the confluence with Sign Creek, but inchannel flow plunged below surface again at
Tumbler Creek. The channel was filled with large, woody debns (LWD) and pocket pools harboring
stranded Westslope Cutthroat trout. Historic beaver activity was pervasive with recent evidence of new
colonization in the lower portion of the survey. Old mid-channel bars, point bars and slumping banks
indicated past flooding caused by peak flows in 1997 and 1964.
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Appendix B
Flathead River Headwaters TPA
3.6 Morrison Creek
3.6.1 Road Survey results
Active upland sediment sources induced by timber harvest activities are not significant sources of
sediment in the Morrison drainage. A gate closed seasonally restricts road access within the Morrison
Creek drainage. The major use comes from horse packers during hunting season and from snowmobiles
during winter months. No high-risk culverts or road sediment sources were found. The initial construction
of roads during timber harvest m the late 1970"s created springs that now have established wetlands on
the old, unused roadbeds. As long as traffic does not impact wetlands with rut formation and vegetation
disturbance, the wet areas act as a reservoir for runoff and as habitat for terrestrial aquatic and amphibian
species. The historic roadbeds are well vegetated past the bridge at the confluence of Morrison with
Puzzle Creek and are well traveled by deer, elk, moose and bear.
The pictures above illustrate the bedrock dominated channel type in the upper reaches of Morrison Creek.
Morrison Creek flows south by southeast into the Bob Marshall Wilderness Area and 011 to confluence
with the Middle Fork of the Flathead River system. No reference site was installed due to the assumption
of non-impairment status.
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Flathead River Headwaters TPA
Appendix B
3.7 Skyland Creek
3.7.1 Road Survey results
Active upland sediment sources induced by timber harvest activities are not significant sources of
sediment in the Skyland drainage. All 14 miles of roads within the Skyland drainage have been brought
up to current Best Management Standards. The pictures above illustrate proper function of drain dips,
water bars, and ditch relief culverts. Routine maintenance is conducted on the roads that are open
seasonally for recreational use.
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Appendix B
Flathead River Headwaters TPA
REFERENCES
Cavigili, Jon, Tom Weaver, Mark Deleray, Coal Creek Channel Survey Preliminary Overview 2003.
Montana Fish Wildlife and Parks, February 2004.
Harrelson, C.C., C.L. Rawlings, J.P. Potyondy, Stream Channel Reference Sites: An Illustrated Guide to
Field Technique. USDA Forest Service, Rocky Mountain Forest and Range Experiment Station, General
Technical Report RM-245, 1994.
Montana Department of Environmental Quality (MDEQ), Protocols and Stream Reach Assessments.
2003.
Pfankuch, Dale, J., Stream Reach Inventory and Channel Stability Evaluation. A Watershed Management
Procedure. USDA Forest Service, Northern Region, 1978.
Rosgen, Dave, River Morphology . December 1996.
Van Eimeren, Pat, Biological Assessment for Forest Service Activities within the North. Middle, and
South Forks of the Flathead River Drainage on Bull Trout (Salvclinus conflucntus). 1998.
Wolman, M.G. 1954, A method of sampling coarse riverbed material. Transactions of American
Geophysical Union 35: 951-956.
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Flathead River Headwaters TPA
Appendix B
Coal Creek Channel Survey
Preliminary Overview 2003
Conducted and Prepared By:
Jon Cavigli
Tom Weaver
And
Mark Deleray
Montana Fish Wildlife and Parks
490 N. Meridian Rd.
Kalispell, MT
59901
February 2004
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Appendix B
Flathead River Headwaters TPA
Introduction and Methods
In the winter of 2002-2003 an interagency group convened to discuss stream habitat conditions in Coal
Creek, a tributary to the North Fork of the Flathead River. The group consisted of representatives, mostly
hydrologists or fisheries biologists, from the U.S. Forest Service, U.S. Fish and Wildlife Service,
Montana Department of Natural Resources and Conservation, and Montana Fish Wildlife and Parks
(MFWP). The group convened for a number of reasons, including declines in bull trout spawning, TMDL
planning, and observed in-channel erosion and sedimentation. The group met a number of times
including a fieldtrip to Coal Creek where we looked at active bank erosion. The outcome of these
meetings was concurrence that the group needed to work towards improving habitat conditions in the
stream. To do this, it was decided that we needed better information of existing channel conditions to
take a holistic approach to restoration. Prior to working on isolated locations within the drainage, the
group decided to do preliminary surveys of the forest road system, in-channel conditions, and water yields
within the drainage. We felt this baseline information was important in order to proceed with a better
likelihood of success. This report addresses the in-channel stream habitat conditions in Coal Creek and
its tributaries upstream of the confluence with Dead Horse Creek.
From the information collected during this survey, we were able to produce an overview of channel
conditions in the drainage and provide information in a format that allows others to view channel
conditions and assess the current status. This will allow members of the interagency working group and
others to direct future restoration efforts. This report consists of six parts. The first is this document
summarizing the preliminary channel survey and containing a brief introduction, methodology, and
summaries of general channel conditions for four stream reaches. Also included are four GIS maps (one
for each reach) with GPS locations and photographs of channel features. Some digital photographs are
embedded in the maps. The maps were built by MFWP (Jeff Hutten) in the Information Services Unit
located in the MFWP Region 1 headquarters. The third part of this report is a copy of our field notes with
an appendix that contains a table relating numbered locations on the maps to field observations and
photographs. The fourth portion is an Access database, which provides this information in a format that
may be useful in future assessments. The fifth part is a file containing all photographs taken during the
survey. The last part of this report is a copy of the narrative summary from the 1988 survey (see below).
By referring to the maps, field notes, appendix table, or the Access database a reader can electronically
view the information collected in this survey.
Prior to this survey, a very similar survey was conducted in 1988 (Weaver, Tom. 1989. Coal Creek
Fisheries Monitoring Study NO. VII and Forest-Wide Fisheries Monitoring-1988. Montana Fish,
Wildlife and Parks, Kalispell, MT). The FNF and Montana Fish Wildlife and Parks conducted this earlier
study through a cooperative effort. This report provided a narrative description of stream features
beginning in the headwaters and working downstream identifying sediment sources, bank instability
concerns, and restoration measures. This report stated that there were highly unstable channel areas in
each of the three major forks in the Coal Creek drainage. The vast majority of the problems were related
to land-management, logging and road building activities of the 1950's and 1960's. It noted that
sediment generated decades ago continued to cause channel instability and erosion in the late 1980's.
Since the 1980's, there had been a number of road improvement projects on federal and state lands to
improve stream crossings and road drainage. However, a number of the problems observed in the 1988
report had not been addressed. The 2003 survey aimed to repeat the 1988 survey and determine current
status of and if there were major changes in channel condition.
MFWP personnel (Jon Cavigli, Tom Weaver, and Mark Deleray) split the roughly 28 miles of stream
between the three recorders, which took 15 person-days. For reporting purposes, we broke the river miles
into four reaches. One reach was Mathias Creek and its tributaries down to its confluence with the South
Fork of Coal Creek. The second was the South Fork of Coal Creek from the headwaters down to the
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Flathead River Headwaters TPA
Appendix B
confluence with main Coal Creek. The third was the upper two forks of main Coal Creek. And the forth
reach was main Coal Creek from the confluence of the upper two forks down to the confluence with Dead
Horse Creek. Starting at the headwaters or upstream end of a reach, observers walked downstream noting
in-channel sediment deposits, eroding banks or other sediment sources. Major features were noted in
narrative field notes, digital photographs, and GPS coordinates. Digital photos and GPS coordinates may
not be available for some reaches due to availability of equipment. This survey provides a qualitative
overview of channel conditions that can be compared to similar information from the 1988 report and
provide a holistic view of the drainage to direct future surveys and restoration needs.
Summaries of Stream Habitat Conditions in Four Reaches
Mathias Creek - Map 1
The headwaters reach of Mathias Creek is steep with step pools formed by bedrock slabs and large woody
debris. Upstream from the Road 317 crossing the channel appears relatively stable with the exception of
a reach through the old cutting unit near the upper fork. No Streamside Management Zone (SMZ) was
provided here and the channel has migrated through areas of deposition on large woody debris. Several
low cut banks are present. Frequent avalanches from the steep slopes north of the channel compound the
erosion problem. Surveyors noted 20 sites where large woody debris held gravels and fine sediments,
two depositional plugs where the channel braided (This feature is a plug of sediment often associated with
large woody debris that will be referred to as Plug Deposition Braiding (PDB)) and eleven wind-thrown
trees in the channel area between the old cutting unit and the 317 crossing.
Most of the fill has been removed from the upper crossing of Road 317; the pipe is still in place.
Downstream from this crossing extensive deposition is evident on old logging debris. Several old
machine crossings are present and wind-thrown trees are common along the channel throughout an old
logging unit. Bull trout spawning occurred throughout this general area during past years.
Approximately 1.3 km below the crossing of Road 317 a small tributary flows into Mathias Creek from
the South. This drainage has been highly impacted by past land management activities. The survey team
accessed this area by continuing past the upper Mathias Creek crossing on Road 317 approximately 1.2
km to where this drainage is crossed by Road 317 in Section 4. This drainage has been a major sediment
contributing area. Portions of Sections 4 and 5 above Road 317 north of the Mathias-Hallowatt saddle
were logged approximately 45 years ago. Poor skid trail location and equipment operation in the channel
area resulted in an estimated 6100 m3 of material delivered and transported downstream. Water yield and
transport has been enhanced by a "new" channel system and channel stability problems are evident
throughout the drainage downstream. The culverts where these channels cross Road 317 were removed in
1999, but banks were left too steep and erosion of road fill is ongoing. Downstream from these crossings,
channels are very steep and sediment traps are full of stored fine material. This small tributary to Mathias
should be evaluated for future restoration potential.
Lower Mathias Creek remains relatively steep downstream from the confluence with this small tributary.
The large woody debris storing major deposits of fine sediment is old and some of it is failing, allowing
sediment movement that created new channels. As the gradient decreases, this situation becomes more
common. Lower Mathias Creek passes through logging units and potential for new recruitment of large
woody debris is generally limited or nonexistent. In some areas, lateral deposition is being colonized by
vegetation and appears to be stabilizing. Surveyors noted approximately six major plugs of deposition
causing braiding (PDB) through this reach.
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Appendix B
Flathead River Headwaters TPA
Main Coal Creek Headwaters - Map 2
The fork of main Coal Creek flowing out of Haines Pass covers a distance of 4.8 km from the headwaters
(Section 36) to the junction with the north fork of Coal Creek in Section 19. The upper 1.0 km drains an
undeveloped area; however, slopes north of the pass appear highly erosive and natural slumping has
occurred in several areas. The channel here is steep but stable. Deposited materials are generally larger
than 2.0 mm. The area in the vicinity of the trailhead (#26) has contributed a substantial amount of fine
sediment, largely from management-related activities. Deposition on stable channel debris is evident and
streambed substrate in low gradient areas is highly embedded. Large woody debris is generally lacking
throughout this reach but where jams occur a large amount of sediment is stored. Surveyors noted four
PDBs in the reach. Bull trout spawning has been documented just upstream from the junction with the
north fork of Coal during past surveys.
The fork flowing out of the unnamed lake in Section 23 is characterized as steep and stable. We call this
headwater reach the north fork of Coal Creek. Bedrock step pools with large amounts of large woody
debris are common. As the gradient decreases debris jams cause deposition and gradient checks. Cut
stumps and logging debris are present in the channel through old cutting units and a short reach (300 m)
appears to have been straightened and channelized by machinery. A gradient break is present as the
channel flows out into the Haines Fork valley. Active cutting and depositional areas occur approaching
the junction with Haines Fork. The survey team identified four large depositional areas, six PDBs and 22
lateral deposits all associated with large woody debris in the north fork of Coal Creek. This reach should
be evaluated for future restoration potential.
South Fork Coal Creek - Map 3
The headwaters of South Coal Creek are undeveloped from the Whitefish Divide down to just above the
1686 crossing in Section 31. Sediment sources are natural and materials deposited are generally >2.0
mm. The fill has been removed from the tops of each end of the 72" open arch culvert where 1686
crosses; the pipe is still in place. Below this crossing the channel is steep with bedrock and boulders
forming cascades and falls. Large old debris, both natural and logging related is storing sediment. Old
cutting units occur on both sides. A 2.5 m falls is formed by large woody debris on bedrock 1.4 km
downstream from the 1686 crossing. This barrier is located at the upstream end of the bull trout redd
count section. Stream gradient lessens from here down. Many depositional areas due to old debris
accumulations create braiding (PDBs). Cutting units exist on both banks with inadequate SMZs. Cut
stumps occur in the channel and there is evidence of logging debris being cut out of the channel during
past years (-15 years ago). Proceeding downstream, these debris accumulations causing deposition and
braiding become more common as gradient decreases. Wind-thrown trees are common along old cutting
units with inadequate SMZs on South Coal Creek and adjacent wetlands. Intercepted groundwater forms
small channels, which are full of fine sediments. South Coal joins with Mathias Creek approximately 3.8
km downstream from the 1686 crossing.
The lower portion of South Coal Creek runs through old cutting units with no SMZs. Cut stumps are
visible in the channel area, which has been artificially straightened. Large woody debris is lacking
through these old units and the potential for recruitment is limited or non-existent. This reach should be
evaluated for future restoration potential. Several slumping banks occur on the north side of the channel
through these old units. Once the stream leaves the logged area, gradient increases and it becomes more
confined. Five large logjams have caused major deposition and braiding (PDBs). Two large slumps are
present just upstream from the junction with main Coal Creek.
B-18
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Flathead River Headwaters TPA
Appendix B
Main Coal Creek - Map 4
Downstream from the confluence of the upper two forks of main Coal Creek, the channel ran through old
cutting units where inadequate SMZs and machine operation in the channel area and adjacent wetlands
caused instability. Logging debris and cut stumps in the channel were common. Seven PDBs were noted
along with several slumping banks upstream from the campsite crossing at the edge of Section 17. Bull
trout spawning has been documented throughout this reach. Below the crossing in Section 17 the channel
is similar. We noted several additional PDBs in the mile below this crossing. The bull trout redd count
section ends approximately 1.4 km below the Section 17 crossing. From here downstream to the junction
of South Coal Creek, main Coal Creek passes through a canyon-like area with large substrate, bedrock,
and higher gradient. Surveyors noted 15 PDBs and a lack of debris in the upstream section of this reach.
Several large slumping banks are present downstream from the 317 Bridge.
Downstream from the Coal-South Coal confluence deposition is extensive and generally finer material;
PDBs are practically continuous. Sand deposits occur in channel and on gravel bars. Substrate is highly
embedded with sand "wind rows" obvious behind mid-channel obstructions. Downstream from Dead
Horse Bridge large woody debris because of the Moose Fire became more evident. Many logs across the
channel and in jams have burned. Beaver activity became more common and is causing braiding in
several areas. All large debris jams have extensive deposits of sand and gravel and low velocity areas
have a thin layer of organic sediment. We ended this survey in the willow meadow area at the mouth of
Dead Horse Creek.
B-19
-------
Appendix B
Flathead River Headwaters TPA
MFWP Coal Creek Channel Survey - 2003
Field Comments
Note: Underlined photo numbers are the photos included on printed maps.
ID#'s are labeled on map.
Map One
Tributary to Mathias Creek approximately 1.4 km below upper crossing of Rd. 317
7/08/03 Weaver
Begin narrative 2100 paces downstream from the crossing of Forest Road #317 on Mathias Creek
(T33N R22W Sec5). Approximately 1.4 km (2100 paces) below the upper crossing of road 317 a
small tributary flows into Mathias Creek from the South. This drainage has been a major
sediment contributing area in Coal Creek. Increased water yields resulting from formation of
new channels in Sections 4 and 5 continue to exacerbate channel stability problems in
downstream areas of Mathias, South Coal and main Coal Creeks.
Portions of Sections 4 & 5 above road 317 North of the Mathias-Hallowat saddle were logged
(likely clearcut) approximately 40 years ago. It appears that a small draw draining the Southeast
corner of Section 5 was used as a skid trail (Photo P7080023).
Runoff concentrated in this draw, eroding the shallow soils down to bedrock in many places
(Photos P7080024. P7080027). This "new" channel is approximately 1450m in length and an
estimated 3450 cubic-meters of material has been delivered and transported downstream.
The culvert where this channel crosses road 317 was removed in 1999. This channel joins the
first order stream draining the western half of Section 4 approximately 250 m below road 317.
Equipment operation in the channel area of the first order stream has resulted in similar erosion
and water yield problems (Photos P7080016, P7080022). An estimated 1200 m of stream has
been impacted resulting in approximately 2650 cubic-meters of material delivered and
transported downstream.
The culvert at the crossing of road 317 was also removed in 1999 (Photos P7080013, P7080015).
In all, over 6100 cubic-meters of material resulted from this unit. Deposition is still evident
within these channels but most of this material has been transported downstream. Water yield has
been enhanced by the "new" channel system and channel stability problems are evident
throughout the entire Coal Creek drainage downstream.
Map One
Mathias Creek from barrier falls down to forest Rd. 317 uppermost crossing
7/09/03 Cavigli
Walked upstream from highest road crossing to barrier falls. (Photo P7090011).
Gradient steep from falls to highest old cutting unit. Step pools formed by bedrock slabs. Moss
covered banks with old, mature LWD holding back gravels here and there.
Top of highest cutting unit. Lots of LWD in stream through this unit, holding gravels and fine
sediments. Cut stumps prevalent in riparian area. Stream looks unraveled compared with reach
above (Three Photos P7090005, P7090006, P7090007).
(Two Photos P7090009, P7090008) One picture of avalanche chute coming down to stream, the
other picture is view looking in the opposite direction. Just downstream of ID97.
Approximately 200-300 meters below above photos high water channel with cobble substrate
(Photo P7090013).
(Photo P7090014) Gravels deposited on stream margin.
(Two Photos P7090015. P7090016) Two different PDB's ~ Plug. Deposition. Braiding.
(Woody debris plug, deposition of sediment, resulting braided channel). One has island of
grasses, non-woody plants, and Spruce growing on it.
B-20
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Flathead River Headwaters TPA
Appendix B
Lower reach all the way down to road crossing contains a good amount of old LWD (Photo
P7090017). Last photo is good example of LWD with some gravel storage.
Ending point. Culvert @ road crossing.
Summary: Upper reach is very steep with step pools formed by bedrock slabs. Some old LWD
holding back gravels. Stable looking channel. Through cutting unit there is lots of LWD holding
material and stream looks unraveled with braids and low cut banks. Rest of stream down to road
crossing has lots of LWD. Counted 20 sites associated with LWD holding gravel and sediment
deposits. Counted two PDB's and eleven tree wind-throws below the highest cutting unit.
Overall the stream looked pretty good.
Map One
Tributary south of Mathias Cr. to Mathias and down to confluence with South Coal
7/09/03 Deleray
This is the pulled culvert site on Rd. 317 that received water from manmade channel described by
Weaver on 7/08/03. There is up to six feet of eroding road fill on one side, up to three feet on the
other. The six-foot side is very steep, 1:1 and vertical in the six foot eroded area. Possible
project: Re-slope fill, and stabilize.
Upstream: 1) No recruitment of LWD in years and for years to come. 2) Fill and bed-load stored
behind deteriorating logs, some have already failed. Possible project: Add LWD
Downstream: Within the first 50 yards there are five logs with sediment trapped behind, forming
stair steps, plug, after plug, after plug. This steep area has numerous "step pools" but all the
"pools" are filled in with sediments, stored behind the LWD.
Halfway down, a new channel forms off side of sediment plug formed by LWD (just above
confluence with other channel to the northeast).
Below this confluence there's a lot of sediment stored in side-bars and behind LWD.
(Photo P7090031) Sediment plug is above a six-foot drop.
Steep reach: Less stored sediments, some stored on stream margin, some in LWD and large
rocks. It is too steep to store much.
Lower half of this steeper reach is less steep and once again has old LWD storing sediments.
There also appears to be fines stored on banks and are now being covered by moss and small
vegetation. Channel appears to be narrowing and healing (Photo P7090032).
Confluence with Mathias Cr.
Mathias Cr.: Boulder section, sediments on margins appear trapped behind LWD with some
vegetated, stable channel and bank. {(Photo P7090033) LWD plug stabilized}
Periodically, large deposits of sediment, gravel, etc. are behind LWD dams. There is still some
moderate gradient. (Photo P7090034)
As gradient drops, there are large deposits of sediment and increased occurrence of braiding,
leaving mid-stream gravel bars at times, and forming "new" side-channel through the woods with
dirt and gravel beds. **These are very similar to the one that we looked at last winter with the
interagency group. (Photo P7090035. of "new" side-channel)
Wide channel with high embeddedness
With exception noted above, most of this reach looks good, pools have returned and runs also.
There are still sediments behind LWD and on margins. (Photo P7090036) Still, there are some
mid-channel bars, but banks are stable.
(Photos P7090037, P7090038) Sediments on margin bars are being colonized by vegetation (i.e.
Recovery).
There is still a lot of small material being stored in mobile bars, mid-channel. Also, still periodic
large sediment plugs behind LWD in mid-channel with new small channel on edges going
around. Numerous lateral bars (small, some vegetated, some not and appear active) since the
confluence with Mathias. I have been in a large, harvested unit with low recruitment of LWD, no
new stuff with branches in channel (Photo P7090039). Where there is old LWD there is a
B-21
-------
Appendix B
Flathead River Headwaters TPA
sediment plug behind it.
(Photo P7090040) Note tree above channel. It's top is flat and notched for walking.
Lower in reach: Numerous lateral bars and mid-channel bars with increased incidence of
braiding around deposits. New channels appear fairly well established. Low incidence of raw,
actively eroding banks. Stream is in process of healing, but not yet healed. {(Photos P7090041.
P7090042) Braid and vegetated plug}
Extensive in-stream deposits are behind LWD. (Photo P7090043) Photo is of LWD plug with
water flowing under it and around it.
(Photos P7090044. P7090045) Same photo twice; this large plug is active and underwater in
high flows. Juvenile DV approximately 100 mm observed.
(Photo P7090046) In-stream sediment deposits are present mid-channel and numerous. Braiding
is occurring with gravel and sand deposits common, some active eroding topsoil.
Lower, there is more LWD with stored sediment. Channel is wide and relatively shallow with
lots of sediment in channel. Banks appear stable except in recently braided sections.
(Photo P7090047) Margin deposits, channel moved to right creating newer channel. High water
uses old channel.
This is a large depositional area with three braids. (Photo P7090048)
End at confluence with South Coal creek.
Map ID76 is where we parked our truck near Kelly hump on road 317 for this days survey.
* * * Probably six or so deposits and associated braids through this section like the one the winter
interagency group looked at.
Map Two
North Coal Cr. (Upper reach) down to confluence with Coal Creek (Haines)
7/11/03 Cavigli
(Photo P7110001) Beginning point above last cutting unit on North Coal. Took photo of starting
point, LWD with associated gravel plug and gradient drop.
This reach characterized by steep gradient, falling through bedrock steps.
Lots of LWD, big stuff, gravels are piled up on stream margin and behind LWD plugs.
(Photo P7110002) Barrier? Approximately a 4-meter drop.
(Photo P7110003) Gravels deposited below LWD jam, boulders, and on stream margin.
(Photo P7110004) Cut tree in riparian of stream channel.
(Photo P7110005) Large deposit of gravels, 30'x 15', with Willows established on stream
margin. Does not look real stable.
PDB, first one, log jam has forced out of channel movement, no fines left.
(Photo P7110006) More gravel deposits on stream margin.
(Photo P7110007) Another barrier looking bedrock formation.
(Photo P7110008) Smaller gravel and fines accumulation on stream margin below LWD.
(Photo P7110009) PDB #2, a result of LWD jam (logging debris). Out of channel stream
movement. Below this point are small cut banks with fines removed. What's left is moss
covered large cobble.
(Photo P7 110010) Cut stump in riparian, downed log parallel to stream has gravels deposited
behind it.
(Photos P7110011, P7 110012) Large PDB #3 has extended gravel bar associated with it and has
deposition into island of trees between migrated braid and low water channel. Second photo
shows LWD jam plugging this deposit. This is largest plug with fines that I've seen today.
(Photo P7110013) Immediately below PDB #3 are gradient checks made of LWD holding more
gravels and cobble. Stream turns at this point and begins dropping into Haines Fork valley,
straight section of about 300 meters.
PDB #4 caused by major LWD pile-up. Gravel deposited on stream margin.
B-22
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Flathead River Headwaters TPA
Appendix B
(Photo P7110014) Eroded bank sprigged and toe anchored, fix by Hank Dawson some years ago.
Looks like it is healing well.
(Photo P7 110015) PDB #4. Gradient change occurs here, slope lessens. Channel braids here at
LWD jam. Can easily see clearcut on other side of Haines Fork.
After a 300-400 paces the braided channels come back together.
(Photo P7 110016) Two cut stumps on stream margin with gravel deposits behind them.
(Photo P710017) Ending point at confluence with Coal Creek (Haines). North Coal at this time
was 56ฐF while Coal was 49ฐF.
Summary: Upper reach characterized by steep gradient with bedrock step pools. Lots of LWD
with, in my opinion, a fair amount of gravel deposits. Middle reach has a little less gradient with
lots of LWD causing jams and gradient checks, backing up a lot of deposited gravels and fine
sediments. Lower reach I'd say begins at ID62 where there is an obvious gradient reduction with
braiding beginning at initial depositional area. There is some active cutting into banks in this
braided section with associated gravel bars and gravel deposits on stream margin. Did observe
WCT today, whole length of stream. They were all juvenile sized fish. According to my notes I
identified 4 large plugs of sediment, 6 PDB's, and 22 stream margin depositional areas all
associated with LWD.
Map Two
Coal Creek (Haines) down to confluence with North Coal
7/11/03 Deleray
Start @ upper road crossing (Photo P7110061 Walking bridge)
Stream appears stable @ crossing. Moss on rocks, mid channel has old LWD storing bed load.
About 100 yards downstream in an old unit the bed load is stored behind old LWD. Counted
twenty through here, all approximately ten yards long (Photos P7110062, P7110063). Excessive
bed load stored in stream and on margins.
(Photos P7110064, P7110065) Old LWD retaining bed load and upstream bar becoming
vegetated.
Bridge and deck storing bed load, channel moved to right side of bridge. This was a low bridge
with approximately one foot of clearance. Gap was plugged and bed load filled in behind it
(Photo P7110066).
(Photo P7110067) Old LWD plug of sediment. LWD failed and now channel cut out and by
passes half of plug.
(Photo P7110068) Between LWD plugs, there are sections of stream without LWD.
Mini PDB - Plug, Deposition, Braiding. (Woody debris plug, deposition of sediment, resulting
braided channel) has island with established Alders on it. Channel is stable.
Adult WCT, 8-10 inches long. No other fish seen to this point.
(Photo P7110069) Failed LWD dam.
Tally for failed LWD dams to this point, four. These are the obvious ones, recent failures with
many others already likely failed.
Large deposit, 5'x 30'x 60', new channel has formed and is still forming around plug. PDB
situation (#1). This is 50' above ID52.
There must be some type of gradient change. This reach is wide, 30' or so and shallow, averages
6" deep (Photo P7110070). There are large bed load deposits, new channels going into the trees.
Another PDB (#2). Observed two WCT, 5-6" and 6-7".
Gradient increases, series of cascades present. Between ID52 and ID51 the channel looks really
good, narrower and deeper than above. It has nice pools, stable banks with no excessive bed load
deposits.
Just below ID51, large deposits present behind old LWD jam. Stopped adding to tally of plugs.
Where there are old LWD jams (2) there are sediment plugs stored behind. There is an obvious
B-23
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Appendix B
Flathead River Headwaters TPA
lack of newer LWD. All LWD is old and rotten. Sections without LWD have large substrate
with relatively straight channels.
These old log jams form mini PDB's with new channels on both edges of stream.
Cascade with 1-2 meter drops, a potential barrier to fish passage. *
(Photo P7110071) Approximately 3-meter drops, fish barrier made of bedrock.
Culvert (4' diameter) is not a barrier at this flow with an approximate one-foot jump into nice
drop pool. *
Following 100 meters below pipe is high gradient cascade with a 1-2 meter jump. No sediment
stored between ID50 to just below ID48. After 100 m gradient drops, LWD jams (2) store
sediments. Saw fish again here.
Ending place @ confluence with N. Coal Creek. ID48 to ID47, gradient is low to moderate.
Where LWD exists it holds bed load and forms pools. This reach looks pretty good. Sediments
stored on margins and behind LWD, but low frequency of pools that are present look good.***
Summary for today's reach: Looks relatively good. There are few actively eroding banks. LWD
lacking. There is no newer LWD. All LWD without branches, bark, and is deteriorating. Only
thing that could be done is to add LWD to reach. This reach is currently producing relatively low
amounts of sediment to the lower reaches.
Map Three
Upper reach South Coal Creek to confluence with Mathias Creek (No GPS unit)
7/09/03 Weaver
Begin survey 1000 paces upstream from crossing of Forest Road 1686 in Section 31. This is the
headwaters of South Coal Creek.
Upstream from starting point South Coal Drainage is undeveloped. Sediment sources are natural;
mostly from wind-thrown trees in the channel area; materials deposited in overflow channels and
on logs across stream are generally > 2.0 mm; mostly large gravel; lots of large, older naturally
recruited woody debris present. The main channel subs and resurfaces several times in the
headwaters reach.
A depositional area and related overflow channel is located 445 paces below he starting point.
Small stream joins the main channel 514 paces below the starting point. This small inflow drains
from an old cutting unit on the North side of the drainage; this is the uppermost development in
South Coal Creek.
A raw bank 10 m long by 1.0 m high contributes sediment 785 paces downstream from the
starting point.
At pace 900 an uprooted tree resulted in sediment input 6.0 m long by 2.0 m high.
Forest Road 1686 crosses at pace 1000. The pipe is still in place with fill on it, but most of the
fill material has been removed at each end of the 72-inch open bottom arch (Photos 0709000]_,
Q7090002). If this pipe plugged, the stream would pass through where fill has been removed.
Although sediment input resulting from a failure has been reduced, a substantial amount would
still occur.
Downstream from this crossing, bedrock, boulders and large debris form many cascades/falls.
Many are natural, but old logging debris is storing fine sediment in many locations. This
situation exists for approximately one-mile below the 1686 crossing. Old units occur on both
sides with adequate SMZ present.
An old bridge crossing is present 2200 paces below the 1686 crossing.
Just upstream a 5.0 m long by 3.0 m high cut bank on the North side contributes fine sediment.
At pace 2240 a bedrock falls with old debris creates a 2.5 m falls. This is the upstream end of the
bull trout spawning area in South Coal Creek. Basin-wide redd counts begin here.
Stream gradient lessens from here down and many depositional areas occur due to old debris
accumulations; channel has migrated in many areas forming sediment sources during active
period.
B-24
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Flathead River Headwaters TPA
Appendix B
At pace 3300 a 10.0 m long by 5.0 m high cut bank with downed trees forms a sediment source;
lots of deposition at the foot of this bank. Bull trout spawning has been documented from here
down.
Cutting units exist on both banks; stumps in channel area; NO SMZ; logging debris in channel
some of which has been cut out 15 or so years ago.
At pace 4000, debris accumulations causing braiding and deposition become more common; lots
of wind-throw in old cutting units; NO or inadequate SMZ on South Coal channel and adjacent
wetlands. Intercepted groundwater forms stream channels that are full of fine material and
contribute to main channel.
The Mathias Creek Road 317 crosses at pace 5615.
The junction with Mathias Creek is at pace 5650, today's ending point. Deposition and braiding
occur down to this point.
Map Three
South Fork Coal, confluence with Mathias down to electrofishing section
7/10/03 Deleray
First quarter mile or so, moderate gradient few deposits of sediment. Ones that were there
were small, six foot long associated with LWD on margins (looks good).
Large deposits of sediment, gradient break (lower) with stream braiding into three or so small
channels, some of deposition is vegetated with Willow, Alder, grasses, etc. (Photo
P7100049). This could be an Interagency type project.
LWD is relatively abundant at plug and below, storing sediment. Newer channels, one pretty
established channel with some actively eroding banks, but not much. Fines are moving
annually and show new deposits on margins.
LWD storing large deposits
Avalanche chute, small deposits, it is relatively stable. LWD holding sediments.
Channel to here is stable with exception of ID45 plug. Looks good.
Stream has healed in sections. Alder and Willow on large deposits, looks stable.
Bridge crossing, few LWD in last 300 yards, otherwise channel looks good and stable.
Braid (two channels). Large, mid-channel deposits of mostly cobble, five feet high, vegetated
with Cottonwood, Alder, Willow, and Spruce. It is teardrop shaped, approximately thirty feet
long with eroding bank (raw) at downstream end of teardrop island (Photos P7100050,
P7100051).
Just downstream, outside bank of meander is eroding. Large gravel bar deposited on inside
of meander with few LWD across channel. It is up on banks and sides.
I've been in an old unit. No LWD, somewhat incised channel.
Haven't climbed over LWD since bridge (Photo P7100052). Stream has long reaches of
boulder/cobble runs with no sediment storage. There is one meander present between bridge
and photo site. No LWD recruitment for years to come. This reach does not appear to be
contributing much sediment at this time, but it isn't storing any either.
Gravel bars and meander at end of long straight reach (Photos P7100053, P7100054) just
below ID43.
Channel began meandering after ID43. Short sections of banks are eroding on outside bends
in same areas.
Extensive riparian logging occurred in this unit, through reach, numerous stumps in channel
(Photo P7100055).
Cabled trees. (Photos P7100056, P7100057) Erosion at upper end, trees lay parallel to bank.
They are not storing sediment.
Braiding, large sediment deposits in riparian of harvested unit (Photos P7100058,
B-25
-------
Appendix B
Flathead River Headwaters TPA
P7100059). I counted DV redds in this braided section last year. Some bank erosion active
at this time, reach is somewhat unstable with numerous banks eroding for short reach (each
has small contribution)
End @ electrofishing section on South Coal. (Photo P7100060)
* * * Stream reach through unit was straightened by dozer therefore no LWD and channel has
incised nature. This would be potential project to re-establish natural stream configuration
and LWD.
Map Three
South Coal Creek, electrofishing section to confluence with Main Coal Creek
7/10/03 Weaver
Begin survey at the lower block net line in the South Coal electrofishing section. Mark did the
reach upstream.
Braiding occurred 340 paces below the starting point where an old jam caused deposition of fine
material.
A 20 m long by 2.0 m high cut bank was present on the North side at pace 400.
At pace 550 deposition in the channel resulted in braiding and a vegetative plug; cut stumps are in
the channel area; old unit with No SMZ.
Another plug occurred at pace 1400 with lots of deposition, braiding and wind-thrown trees.
An actively slumping bank on the North side contributed sediment (15 m long by 10 m high) at
pace 2060.
Channel artificially straightened (Photo P8130003)
An old debris jam at pace 2350 caused major deposition and channel braiding; jam span entire
channel and contains logging debris; this area extends several hundred paces downstream (Photo
P813000ฃ P8130005).
Another similar but more extensive plug is present at pace 2650. This one extends 300 paces
downstream; fish passage during low flow is questionable (No WP).
Another plug is located at pace 3975 extending downstream 200 paces (No WP).
A 60 m high by 30 m long cut bank is actively contributing fine sediment at pace 4300 (No WP).
Another plug with large wood, deposition and active braiding occurred at pace 4400. This jam is
3.0 m to 4.0 m high.
At pace 4500 lots of debris and a 20 m by 20 m slumping bank were present. A major
depositional area was located just downstream in mid-channel.
The South Fork of Coal joined main Coal Creek at pace 4850.
B-26
-------
Flathead River Headwaters TPA Appendix C
APPENDIX C: 2002 AND 2003 FIELD SAMPLING DATA (AVAILABLE UPON
REQUEST FROM MONTANA DEQ)
C-1
-------
-------
Flathead River Headwaters TPA Appendix D
APPENDIX D: MCNEIL CORE, SUBSTRATE SCORE, AND FISHERIES DATA
D-1
-------
-------
Flathead River Headwaters TPA
Appendix D
Table D-l. McNeil Core data for streams in the Flathead River Headwaters Planning Area.
Year
Lower
Coal
NF-Coal
SF-Coal
Whale
Granite
Big
Creek
Challenge
Trail
Red
Meadow
Morrison
Creek
1981
34.1
25.1
23.8
25.7
1982
40.2
31.8
44.6
32.6
36.1
1983
39.3
32.6
28.2
27.2
1984
32.8
29.5
27.8
28.1
1985
36.4
34.9
36
22.5
28.7
26.2
1986
34.8
29.4
31.8
26
49
21.6
25
1987
40.8
30.2
31.4
28.9
41.3
29.1
32.5
27.4
1988
39.2
39.8
32.1
37.2
45.5
40.4
40.9
30
1989
37.8
37.8
36.9
35.3
45.2
48.4
43.5
40.1
1990
42.1
32.8
33.6
33
53.4
33
34.6
39.2
1991
36.1
32.6
32.7
34.2
37.2
32.9
38.2
33.7
1992
35.8
33.5
34
32.2
41.4
37.4
41.9
29.5
1993
35.5
30
28.4
33.4
36
37.2
36.8
33.6
1994
32.6
25.5
26.2
29.5
33.5
34.5
34.6
24.8
1995
37.5
30.8
28.8
32.6
34.8
32.2
37.9
29.5
1996
38.2
29.6
30.1
31.4
33.6
30
38.1
34.5
1997
36.4
30.1
29.2
30.9
32.5
31.1
36.4
29.8
1998
37.4
30.9
30.2
31.3
32
32.2
35.9
30.2
1999
37.6
31.4
30.8
31.9
35.1
33.1
33.1
30
2000
36.5
31
30
30.8
34.7
31.4
35.1
29.7
2001
37.6
31.8
30.9
31.6
33.7
32.1
36
30.4
N
21
17
17
20
17
21
15
20
1
1
Average
37.1
31.9
31.4
30.9
37.8
33.2
36.9
29.8
40.1
39.2
Std Dev
2.4
3.3
2.7
3.4
5.5
7.3
3.3
3.3
NA
NA
Coefficient of
Variation
6.6%
10.4%
8.7%
11.1%
14.5%
21.9%
8.8%
11.1%
NA
NA
CI
1.0
1.6
1.3
1.5
2.6
3.1
1.6
1.5
NA
NA
Range
9.5
14.3
10.7
14.7
17
31.8
11
11.3
NA
NA
Median
37.4
31
30.9
31.5
35.1
32.2
36.4
29.75
40.1
39.2
Min
32.6
25.5
26.2
22.5
32
21.6
32.5
24.8
40.1
39.2
Max
42.1
39.8
36.9
37.2
49
53.4
43.5
36.1
40.1
39.2
5-yr Ave
37.1
31.04
30.22
31.3
33.6
31.98
35.3
30.02
NA
NA
5-yr Median
37.4
31
30.2
31.3
33.7
32.1
35.9
30
NA
NA
Source: Weaver et a!., 2003
D-1
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Appendix D
Flathead River Headwaters TPA
Table D-2. Substrate score data for streams in the Flathead River Headwaters Planning Area.
Year
Big
Creek
Cyclone
Coal
Creek
Granite
Morrison
North
Fork
Coal
Ole
Quintonkin
Red
Meadow
South
Fork
Coal
Whale
1984
10.2
12.2
1985
11.6
13.5
12.8
1986
12.2
12.3
12.3
14.2
12.5
12.0
1987
11.5
10.0
12.8
13.7
12.3
13.0
12.2
1988
11.2
9.8
12.8
13.0
12.5
12.7
12.0
11.7
1989
11.8
11.3
9.6
13.0
12.3
11.8
11.8
11.8
11.5
1990
11.3
11.6
10.4
11.1
13.2
10.9
11.5
11.3
1991
11.8
9.8
11.9
12.7
11.3
11.4
11.8
1992
11.1
11.2
12.1
12.5
11.5
11.9
11.2
1993
10.8
10.7
11.5
12.1
11.8
11.4
11.3
1994
10.6
10.5
13.1
13.1
12.0
12.4
12.1
1995
10.9
11.1
10.8
12.7
13.6
12.3
12.5
11.8
1996
11.1
11.3
10.7
12.5
13.7
13.2
12.1
12.3
12.0
1997
11.0
11.6
10.5
12.8
13.7
13.1
12.3
12.7
11.6
1998
11.3
11.4
10.4
13.1
13.9
12.9
12.8
12.2
12.6
11.9
1999
11.8
11.9
10.1
13.3
13.6
12.8
13.0
12.3
12.8
12.1
2000
11.7
11.4
9.8
13.6
13.8
12.9
12.8
11.9
12.8
12.5
2001
11.6
11.6
9.7
11.6
13.7
13.6
12.4
12.5
11.7
12.9
12.4
2002
12.0
11.1
9.4
11.4
13.2
13.4
12.1
12.3
11.4
12.6
12.2
Average
11.4
11.4
10.4
11.5
12.7
13.3
12.5
12.8
11.9
12.3
11.8
5-yr Ave
11.7
11.5
9.9
11.5
13.4
13.7
12.6
12.7
11.9
12.7
12.2
Std Dev
0.5
0.2
0.7
0.1
0.7
0.6
0.4
0.3
0.5
0.5
0.4
Coefficient
of
Variation
4.0%
2.2%
7.0%
1.2%
5.6%
4.7%
3.2%
2.4%
4.0%
4.1%
3.4%
Median
11.3
11.4
10.4
11.5
12.8
13.5
12.5
12.8
11.9
12.4
11.8
5-yr
Median
11.7
11.4
9.8
11.5
13.3
13.6
12.8
12.8
11.9
12.8
12.2
Min
10.6
11.1
9.4
11.4
11.1
12.1
11.8
12.3
10.9
11.4
11.2
Max
12.2
11.9
12.3
11.6
13.7
14.2
12.9
13.2
12.7
12.9
12.5
Range
1.6
0.8
2.9
0.2
2.6
2.1
1.1
0.9
1.8
1.5
1.3
Source: Weaver et a!., 2003
D-2
-------
Flathead River Headwaters TPA
Appendix D
Table D-3. Redd data for streams in the Flathead River Headwaters Planning Area.
Year
Big
Coal
Granite
Morrison
Quintonkin
Sullivan
Trail
Whale
1980
20
34
34
75
45
1981
18
23
14
32
78
98
1982
41
60
34
86
94
211
1983
22
61
31
67
56
141
1984
9
53
47
38
32
133
1985
9
40
24
99
25
94
1986
12
13
37
52
69
90
1987
22
48
34
49
64
143
1988
19
52
32
50
62
136
1989
24
50
31
63
51
119
1990
25
29
21
24
65
109
1991
24
34
20
45
27
61
1992
16
7
16
17
26
12
1993
2
10
9
14
5
25
13
46
1994
11
6
18
21
3
8
15
32
1995
14
13
25
28
7
28
28
1996
6
3
4
9
4
52
8
35
1997
13
5
12
39
0
50
9
17
1998
30
14
22
35
11
54
17
40
1999
34
7
37
30
15
55
21
49
2000
32
3
26
44
15
45
42
68
2001
22
0
18
40
17
51
27
77
2002
12
0
18
30
21
18
26
71
Average
19
25
25
43
10
40
39
81
5-yr Ave
26
5
24
36
16
45
27
61
Std Dev
10
21
10
23
7
18
25
50
Coefficient of
Variation
50.2%
86.1%
42.6%
53.2%
71.3%
44.8%
63.1%
62.0%
Median
19
14
24
39
9
50
28
71
5-yr Median
30
3
22
35
15
51
26
68
Min
2
0
4
9
0
8
8
12
Max
41
61
47
99
21
55
94
211
Range
39
61
43
90
21
47
86
199
Source: Weaver et a!., 2003
D-3
-------
Appendix D
Flathead River Headwaters TPA
Table D-4. Westslope cutthroat trout densities for streams in the Flathead River Headwaters
Planning Area.
Year
Challenge
Cyclone
North Coal
South Coal
Red Meadow
1981
13.26
1982
10.72
3.15
1983
9.57
18.33
2.36
9.22
1984
4.18
1985
4.66
6.01
1986
20.51
3.98
3.56
1987
31.19
5.43
3.77
3.62
1988
22.69
37.82
5.33
4.45
11.17
1989
21.41
18.41
5.67
6.56
5.82
1990
12.8
3.36
4.29
7.02
1991
11.71
2.76
1.28
1992
20.29
6.27
2.55
1993
10.42
6.53
2.73
1994
4.74
4.22
2.67
5.2
1995
3.68
3.29
1.59
8.72
1996
14.07
3.44
0.25
4.17
1997
16.14
6.32
5.53
1.64
1998
13.25
8.67
0.86
5.82
1999
18.62
2.53
8.71
1.4
6.53
2000
8.15
7.65
2.01
8.58
2001
8.34
11.11
9.94
3.87
12.34
2002
9.7
9.99
8.39
3.05
6.77
N
19
8
21
17
14
Average
14.1
14.7
5.4
2.9
7.0
Std Dev
6.9
10.8
2.2
1.8
2.7
Coefficient of
Variation
49.0%
73.4%
40.9%
61.0%
38.2%
CI
3.1
7.5
0.9
0.8
1.4
Range
27.5
35.3
7.6
6.3
00
CO
Median
12.8
12.2
5.3
2.7
6.7
Min
3.7
2.5
2.4
0.3
3.6
Max
31.2
37.8
9.9
6.6
12.3
5-yr Ave
11.2
9.2
8.7
2.2
8.0
5-yr Median
9.0
10.6
8.7
2.0
6.8
Source: Weaver et a!., 2003
D-4
-------
Flathead River Headwaters TPA
Appendix D
Table D-5. Bull trout densities for streams in the Flathead River Headwaters Planning Area.
Year
Coal
Granite
Creek
Morrison
Creek
North Fork
Coal
Ole Creek
Red
Meadow
South Fork
Coal
Whale
Creek
1980
13.52
1981
4.69
1982
4.87
15.50
1.34
2.10
1983
3.17
11.44
1.57
5.87
2.44
1984
4.28
4.18
1985
4.38
11.27
3.67
5.91
1986
6.57
17.54
2.96
2.91
5.72
2.15
1987
8.33
17.47
4.05
3.10
3.00
1.16
3.82
1988
4.92
13.23
4.08
1.93
2.48
1989
4.07
11.87
4.89
3.59
1.91
1.73
2.14
1990
2.99
2.22
2.84
4.05
4.38
2.30
1991
4.80
7.57
0.69
4.38
1992
3.26
3.21
1.50
5.38
6.19
1993
2.14
6.25
0.63
1.45
3.42
1994
2.27
1.46
0.22
0.40
0.75
5.10
1995
2.00
8.07
0.24
0.16
3.77
4.39
1996
0.26
2.66
0.10
0.34
0.41
2.13
1997
0.07
3.46
0.08
1.96
0.57
1998
0.36
3.89
0.10
3.85
1.04
0.16
8.52
1999
0.62
4.84
0.16
0.78
0.93
1.17
3.18
2000
0.32
5.74
0.43
2.88
0.44
1.04
3.03
2001
1.31
5.99
5.37
0.75
3.25
0.58
1.54
4.30
2002
0.58
4.13
5.90
0.53
2.51
0.63
2.60
6.32
N
21
2
21
21
9
14
17
17
Average
2.9
5.1
8.2
1.7
2.8
1.9
2.4
3.8
Std Dev
2.3
1.3
5.1
1.7
0.9
2.0
1.8
2.0
Coefficient
of
Variation
77.5%
26.0%
62.4%
99.4%
33.0%
102.8%
74.5%
51.5%
CI
1.0
1.8
2.2
0.7
0.6
1.0
0.8
0.9
Range
8.3
1.9
16.1
4.8
3.1
5.7
5.8
8.0
Median
3.0
5.1
6.3
0.8
2.9
1.0
1.7
3.4
Min
0.1
4.1
1.5
0.1
0.8
0.2
0.2
0.6
Max
8.3
6.0
17.5
4.9
3.9
5.9
5.9
8.5
5-yr Ave
0.6
5.1
5.1
0.4
2.7
0.7
1.3
5.1
5-yr
Median
0.6
5.1
5.4
0.4
2.9
0.6
1.2
4.3
Source: Weaver et a!., 2003
D-5
-------
-------
Flathead River Headwaters TPA Appendix E
APPENDIX E: RESPONSE TO PUBLIC COMMENTS
E-1
-------
-------
Flathead River Headwaters TPA
Appendix E
Response to Comments
As described in Section 6.0, the formal public comment period extended from October 20, 2004 to
November 20, 2004. Five individuals submitted formal written comments. Their comments have been
summarized/paraphrased below. Responses prepared by EPA and DEQ follow each of the individual
comments. The original comment letters are located in the project files at DEQ and may be reviewed
upon request.
1. Comment: The document is very difficult to read, due to a lack of organization, unity, and
coherence. One should not have to be an aquatic expert to understand the data presented and with
some reorganization, the EPA could make this document much easier for the public to
understand.
Response: By necessity, TMDL documents are generally very technical in nature with much of
the subject matter required by regulation or otherwise recommended by EPA and/or State
guidance. The TMDL documents, therefore, will generally be relatively lengthy and contain
considerable technical information that may or may not be commonly understood by the
layperson. The State of Montana has chosen to organize the documents such that the required
elements are apparent to the reader/reviewer of these documents and also include much of the
technical analysis within the body of the document. As we produce our TMDL documents, we
are walking a fine line between production of a document that the average layperson can
understand versus production of a document that can withstand the pressures of technical, peer
review and possibly litigation. It is difficult to meet the demands of both in a single document.
Therefore, we generally include a brief executive summary that presents the important points of
the document in an easily readable format.
Although we included an executive summary with the draft document, we have prepared a brief
"summary report" in response to this comment. The summary report is a stand-alone document
that will be made available with the Final TMDL document. On a case-by-case basis where future
TMDL documents become excessively lengthy and/or technical, DEQ will provide similar
"Summary Reports" to give the layperson an alternative to reading the entire TMDL document.
2. Comment: It seems the EPA jumped ahead into Phase III of the planning stage, making
conclusions without first collecting and analyzing data thoroughly.
Response: We disagree. This report was prepared following the same approach utilized for all
of the TMDLs prepared in Montana in 2004. The first step involved characterizing the watershed
in which the subject water bodies exist (Section 2.0). This was followed by the compilation and
review of all available water quality data, and identification of data gaps for all of the streams in
the TPA appearing on the 1996 or 2002 303(d) list. A sampling and analysis plan was then
developed and implemented to address data gaps associated with in-stream water quality as well
as watershed scale source assessment information (see Appendix C and our response to
Comment 9). An understanding of the current water quality condition of each of the subject
streams was then developed and has been articulated in Section 3.0. Lower Coal Creek was
determined to be the only water body in need of a TMDL. Targets, a total maximum daily load,
allocations, a monitoring strategy, and restoration strategy were then developed for the entire
Coal Creek Watershed (Section 4.0).
3. Comment: It appears that grant money will be used to fund implementation of the Coal Creek
TMDL and the Voluntary Water Quality Improvement Strategy for Red Meadow, Whale, and
Sullivan Creeks and the remaining money would be obtained from local sources. What are these
local sources?
E-3
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Appendix E
Flathead River Headwaters TPA
Response: The Flathead Basin Commission submitted a 319 Grant Application to the Montana
Department of Environmental Quality in December 2004 to implement the Coal Creek TMDL
and Voluntary Water Quality Improvement Strategy for Red Meadow, Whale, and Sullivan
Creeks. Since final funding decisions have not yet been made, it is not possible to provide an
answer to this question at this time.
4. Comment: We must question if the Coal Creek TMDL and Voluntary Water Quality
Improvement strategy will improve future water quality to the same degree that increased forest
restoration and stewardship efforts would do.
Response: Comment noted.
5. Comment: We urge DEQ to recognize and include substantial road reclamation in its Flathead
Headwaters TMDL restoration plan as a primary means to reduce the degree to which road
density and road location are impairing stream reaches in their ability to support bull trout and
other aquatic life.
Response: Road reclamation is included as part of the Coal Creek TMDL (Section 4.0) and the
Voluntary Water Quality Improvement Strategy for Red Meadow, Whale, and Sullivan Creeks
(Section 5.0). In 2003, the Flathead National Forest identified all road segments contributing
sediment to 303(d) listed streams (See Section 3.3.2.7, pg. 73). Ten road segments in Coal Creek
were identified for restoration activities (Section 4.1.1, page 146), and DEQ proposed road
restoration activities for these 10 segments in Section 4.5. Potential road sources of sediment are
discussed for Whale Creek, Red Meadow Creek, and Sullivan Creek in Section 5.0. Section 5.3
then discusses the implementation strategy for road restoration activities in these watersheds.
Furthermore, various road reclamation activities have been and continue to occur throughout the
Flathead National Forest and Coal Creek State Forest (See Section 4.1.1).
6. Comment: We have reviewed substantial data indicating many of these streams need on-the-
ground restoration work, especially in terms of reclaiming roads in order to reduce road densities
that have caused may of these streams to receive "functioning at risk" or "functioning at
unacceptable risk" ratings in Forest Service biological assessments for bull trout.
Response: As described in Sections 4.1 and 5.1, source assessment surveys were conducted
within the watersheds of all of the subject streams. As described in Sections 4.0 and 5.0, on-the-
ground restoration work is proposed for all identified sources of sediment (including, but not
limited to, roads). Further, in December 2004 the Flathead Basin Commission submitted a 319
Grant Application to implement many of these activities.
7. Comment: There is no mention of public involvement anywhere in this document. All
stakeholders should be provided a voice in this important clean up process.
Response: A public involvement summary is presented in Section 6.0 of the final document.
8. Comment: The fires have done far more to degrade the water quality and fisheries habitat in
Coal Creek than any established road or forestry activities ever have.
Response: The relative contribution of sediment from fire in Coal Creek is presented in Section
4.1.3 of the document.
9. Comment: The TMDL includes very little recent data for any of the streams.
E-4
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Flathead River Headwaters TPA
Appendix E
Response: Recent data were evaluated for all of the subject streams considered in this document
(see individual stream discussions in Section 3.4, Appendix B, Appendix C, and Appendix D).
The Sampling and Analysis Plan in Appendix C highlights an EPA/USFS sampling effort
conducted in 2002 and 2003 that included physical surveys (i.e., cross-sectional measurements,
longitudinal profiles, Pfankuchs, and Wolman pebble counts) and macroinvertebrates. These data
were all considered in this document. Additionally, McNeil Core data, Substrate Score results,
and bull trout redd count and/or population density information from as recently as 2001, 2002, or
2003 was reviewed for most of the streams (i.e., the most recent data from Montana Fish,
Wildlife and Parks available at the time this report was prepared). Recent McNeil Core data was
not available for Red Meadow, Skyland, Sullivan, and Morrison Creeks. Additional McNeil Core
data collection efforts are proposed for these streams in Section 5.2. Finally, the Flathead
National Forest conducted a sediment source assessment survey in 2002 and 2003 of the entire
TMDL Planning Area (see Appendix B) and Montana Fish, Wildlife, and Parks conducted a
source assessment survey in the Coal Creek Watershed in 2002 and 2003 (see Appendix B).
Although older data was evaluated and considered in this document, it was generally only
considered as supplemental information to assist us in the development of an overall
understanding of the current water quality condition of the subject streams (see Section 3.3.2).
10. Comment: The TMDL should have evaluated temperature as a pollutant
Response: None of the subject water bodies ever appeared on any of Montana's 303(d) lists for
impairment associated with temperature. As a result, there was no requirement to address
temperature as part of this process at this time. Nonetheless, it was recognized that temperature
could be one of the causal factors in the bull trout declines in the Coal Creek Watershed. That is
why the installation of temperature data loggers was included in the proposed supplemental
monitoring program presented in Section 4.4.2.
11. Comment: The road density threshold value of 1.5 miles/mile2 is too high. For example, a road
density less than 1.5 miles (Table 2-10) per square mile can be an acceptable risk. However, its
value as an indicator is significantly less valuable unless the number of road crossings, cut and fill
slope failures, and distances from stream channels are also evaluated.
Response: We agree and offer the following two-part response to this comment. First, road
density (or roads in general) was considered one of the supplemental indicators. As described in
Section 3.3, the supplemental indicators were not considered sufficiently reliable to be used alone
as a measure of impairment. Road density, and all of the supplemental indicators were only used
when one or more of the target threshold values were exceeded to provide supporting and/or
collaborative information when used in context with all of the other available data.
Secondly, the potential implication of roads within the watersheds of the subject streams was
evaluated on a cases-by-case basis, based on a GIS analysis and field survey conducted by the
USFS (see Appendix B). Factors such as road density, number of stream crossing, distance from
road surface to stream, culvert condition, etc. were all considered in the road analysis. Of all of
the road/stream crossings, 87 percent were evaluated in the field. The supplemental indicator
"road density" (1.5 miles/mile2) that appeared in the draft document has been changed to "roads"
in the final document (see Section 3.3) and the numeric threshold value was changed to a
narrative threshold (i.e., no significant road sources).
E-5
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Appendix E
Flathead River Headwaters TPA
12. Comments pertaining to percent subsurface fines < 6.35 mm threshold value (the following 3
related comments have been addressed together)
Comment 12a. The 35% subsurface fines < 6.35 mm target threshold value assumes too
much risk.
Comment 12b. We recommend no individual year should exceed an upper range, which
to be conservative should not exceed 30 percent. The average should not exceed 20 or 25
percent.
Comment 12c. We are very concerned that the EPA presents averages for highly variable
parameters, without reporting any measures of variability. It is not clear from the
available information that sufficient data were collected to apply a statistical approach.
Specific examples of this failure include analyses associated with McNeil cores,
suspended solids, and fisheries data. With regard to McNeil core data, the EPA
designates an average as the target with no acknowledgment of the great variability
associated with measures of substrate composition.
Response: As articulated in Appendix A of Montana's 303(d) lists, DEQ uses the following methods to
determine reference condition:
Primary Approach
Comparing conditions in the subject water body with baseline data from similar, but
minimally impacted ("reference") water bodies in a nearby watershed.
Evaluating historical data from the subject stream.
Comparing conditions in the subject water body to conditions in other portions of the
same water body.
Secondary Approach
Use literature values
Seek expert opinion
Apply modeling techniques
DEQ uses the primary approach for determining reference condition if adequate regional
reference data are available and uses the secondary approach to estimate reference conditions
when there are no regional data. DEQ often uses more than one approach to determine reference
condition, especially when the regional reference condition data are sparse or nonexistent.
A combination of the above primary and secondary approaches were used to derive the proposed
35% threshold "target" value for subsurface fines <6.35 mm. We began with the "Primary
Approach" by comparing McNeil Core data collected in the subject streams with the available
reference data. Using the McNeil Core data available to them at that time, Weaver and Fraley
(1991) calculated an average value of 31.7% to represent natural or "reference" conditions in
streams with minimal human-disturbance in the Flathead Basin. Values in the "reference"
streams ranged from 24.8% to 39% and the highest reference values came from streams reported
to have significant natural sediment sources. The calculated 95 percent confidence interval for
the reference McNeil core mean (i.e., 31.7%) is plus or minus 2.9. (Ott, 1993) Unfortunately,
the "reference" streams considered by Weaver and Fraley differed from the subject streams in
terms of watershed size, geological characteristics, and history of natural occurrences that effect
stream sediment (i.e., fire, floods).
For those streams where historical McNeil Core data were available (i.e., Coal Creek, North Fork
Coal Creek, South Fork Coal Creek, Whale Creek, and Granite Creek), we then attempted to
define a reference value based on historical conditions. However, the earliest McNeil Core data
dates back only to 1981. There is no easily definable time period between 1981 and the present
E-6
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Flathead River Headwaters TPA
Appendix E
that necessarily represents a reference condition. The effects of forest management had begun
much earlier and continued sporadically throughout the period of record. For this reason, it was
determined it would not be appropriate to use historical data from the subject water bodies to
define a reference condition and/or derive a target value for subsurface fines.
We then evaluated literature values and expert opinion following the "secondary approach".
According to the Flathead Basin Cooperative Program Summary Report published by the
Flathead Basin Commission in 1991, westslope cutthroat habitat is considered threatened when
the percentage of fine materials in spawning gravels in any given year is greater than 35% and
impaired when it exceeds 40 percent.
When considering all of this evidence together, the range of potentially suitable threshold target
values for McNeil Core subsurface fines ranges from a low of 31.7 (the average for "reference"
streams) percent up to 40 percent.
It was not felt that managing to a threshold of "impaired" (40%) was appropriate. At the same
time it was not felt that it was appropriate to select the lowest value from the reference streams
given the wide range in reported values (24.8 to 39) from minimally disturbed streams. The
proposed target value of 35% was selected based on the literature/expert opinion and also
because it is virtually the same as the average value from the reference streams in the Flathead
Basin (i.e., 31.7 plus or minus 2.9).
13. Comment: The use of a running five-year average for the subsurface fines < 6.35 mm target is
inappropriate. The relationship between percent less than 6.35mm and embryo survival to
emergence is an annual occurrence. I don't understand the point of assessing this as a running 5-
year average. The best assessment is a comparison of annual coring results for a site with the
estimate of age 1 fish two years later.
Response: The subsurface fines < 6.35 mm target was selected because it provides a literature-
based link between excessive sediment in the stream and cold-water fish habitat. As with the
other targets and supplemental indicators used in this document, this target is not used alone to
make judgments about the current water quality impairment status of the stream. Rather it is used
in combination with all of the targets and supplemental indicators. A running five-year average
was selected to account for the year-to-year variability in this target value. Year to year
variability appears to be a function of a number of both natural and potentially human-caused
factors and ranges up to 20 percentage points based on the data that has been evaluated (see Table
D-l in Appendix D). It is thought that natural events such as flushing flows or low-flow periods
may account for much of this variability. The running 5-year average was proposed to account
for this variability. The use of the running 5-year average was also selected based upon the
assumption that Montana Fish, Wildlife, and Parks (FWP) will continue to collect data on an
annual basis. With the annual data, it will be relatively easy to calculate the running 5-year
average on an annual basis and to observe trends over time. If FWP cannot continue to collect
McNeil Core data on an annual basis, we will modify the target to an annual not to exceed 35%
threshold at that time.
14. Comment: DEQ should also understand that the thresholds it is using for subsurface fines
mainly concern spawning success. They have no relation at all with surface fines and loss of pool
habitat because of accelerated sedimentation.
Response: We agree and our use of the weight of evidence approach as described in Section 3.3
of the document is predicated upon the fact that there is no single parameter that can be applied
alone to provide a direct measure of beneficial use impairments associated with sediment. The
subsurface fines target was selected specifically to provide one measure of potential sediment
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Appendix E
Flathead River Headwaters TPA
impairment associated with the cold-water fisheries beneficial use. The information provided by
this parameter was then used in combination with the information provided by all of the other
targets and supplemental indicators to reach conclusions about water quality impairment. Surface
fines were specifically addressed by the "surface fines" target and indirectly addressed by the
"percent dingers" target, periphyton siltation index supplemental indicator, etc.
15. Comment: We note when presented with data that exceed 35 percent for subsurface fines, such
as the sample for Red Meadow Creek of 41 percent, DEQ dismisses it as invalid because it is
only one sample.
Response: One sample was collected in 1988 and one in 1989 in Red Meadow Creek, both
shortly after the Red Bench fire. This data was not considered because: 1) it is 15 years old and
does not reflect the current condition in Red Meadow Creek, and 2) because it is possible that it
may be high due to the natural fire event that occurred in that approximate time period. As stated
in Section 5.2, supplemental McNeil Core data collection is proposed in Red Meadow Creek.
Further, although no recent McNeil Core data was available for Red Meadow Creek, none of the
other target or supplemental indicator values suggested that this stream is currently impaired. For
example, the substrate score, percent surface fines, and percent dinger target values were all met
indicating good water quality conditions. The only supplemental indicator value that suggested
impairment was the bull trout data. Although bull trout population densities and redd counts have
declined, there is no indication that conditions in Red Meadow Creek are currently causing the
declines. Cutthroat populations over the same period of record in Red Meadow Creek have
shown no overall trend. Given the complexities associated with the interpretation of fish data in
streams connected with Flathead Lake, it is not appropriate to assume that the problem is in Red
Meadow Creek, when none of the other target or supplemental indicator values suggest that the a
water quality problem exists.
16. Comment:. DEQ says the five-year average of McNeil core data for the North Fork of Coal
Creek (p. 97) indicates "good substrate conditions." However, this conclusion is based,
mysteriously, on a mean value only from the past five years and not the full period of record,
which is 16 years.
Response: DEQ acknowledges that there are extensive data for some streams (20+ years). The
full period of record for all data was used to identify trends, variability, and long-term averages
(See Appendix D). Trends, where identified, were discussed in the waterbody-by-waterbody
discussions in Section 3.4. However, DEQ feels that a McNeil Core value from the early 1980s
does not necessarily represent current conditions in any stream. The purpose of this analysis was
to determine if beneficial uses are currently impaired. Because of the dynamic nature of activities
in the watershed, historic data, while useful, should not be used when making a current
impairment determination. DEQ feels that data from the past five-years is most representative of
current conditions, and a five-year average also accounts for natural variation in the data.
17. Comment: We are concerned about DEQ's inconsistent and inappropriate use of "means" or
"averages" when using quantitative data to determine impairment.
Response: DEQ has provided additional information in Section 3.3.1 and 3.3.2 to better explain
the use of averages.
18. Comment: The draft is rife with conclusions that aren't supported with data. For example, in
numerous places the draft concludes that food web changes in Flathead Lake are the causal agents
for bull trout decline in streams in this evaluation. The draft provides no supporting data.
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Flathead River Headwaters TPA
Appendix E
Response: First, the fact that the introduction of non-native fish and the non-native opossum
shrimp in Flathead Lake in 1981 have caused widespread changes the Flathead Lake ecosystem
resulting in bull trout declines is well documented (Spencer et al., 1991). Deleray et.a.l. (1999)
further emphasized how important the inter-connected lake, river, and tributary system is to
fisheries of the entire Flathead drainage, especially to native fish species. It is indisputable that
the food web changes have had an affect on migratory bull trout populations in those streams
within the Flathead Basin that are connected to Flathead Lake.
Given that we know that the migratory bull trout population has declined due to the food web
changes in Flathead Lake, it would not be appropriate to ascribe a bull trout decline in one of the
interconnected tributaries solely to causal agents that only affect the tributary. Clearly, the
migratory population that enters that tributary has also been affected by changes in Flathead
Lake. The fish population dynamics in the tributaries within the Flathead Basin that are connected
to Flathead Lake are very complex and are likely a function of a variety of both human-caused
and natural factors. For this reason, it is not possible to rely on bull trout alone as an indicator of
water quality in the tributaries.
As stated in Section 3.3.2.4 of the draft report, since it was understood that fish populations may
change due to a variety of both human-caused and natural phenomena, fish data was used only as
supplemental information in combination with the full suite of targets and supplemental
indicators (see Section 3.3 for a complete description of the weight-of-evidence approach used
with targets and supplemental indicators). In no case did the draft document "conclude" that the
food web changes in Flathead Lake were the sole causal agent for bull trout declines in any of the
subject streams. Rather, the available fisheries data provided a "piece of the puzzle" in the
context of the weight-of-evidence approach described in Section 3.3.
Finally, in no case were any of the targets or supplemental indicators used alone to reach a final
conclusion regarding water quality impairment. In all cases, the final conclusion was reached
based on consideration of all of the evidence provided by the full suite of targets and
supplemental indicators used in context with one another.
19. Comment: Discussion of statistical validity of conclusions regarding fish populations is not
present.
Response: As stated in Section 3.3.2.4 of the draft report, since it was understood that fish
populations may change due to a variety of both human-caused and natural phenomena, fish data
was used only as supplemental information in combination with the full suite of targets and
supplemental indicators. As described in Section 3.3, the supplemental indicators were not
considered sufficiently reliable to be used alone as a measure of impairment. Fish data, and all of
the supplemental indicators were only used when one or more of the target threshold values were
exceeded to provide supporting and/or collaborative information when used in context with all of
the other available data. The available fisheries data provided a "piece of the puzzle" in the
context of the weight-of-evidence approach described in Section 3.3. Therefore, since we are
only using the fish data qualitatively and only as supplemental information, we do not believe that
it is necessary to provide a discussion of statistical validity.
20. Comment: The "stable or increasing trend" supplemental indicator for bull trout redd counts and
population densities should be changed to "increasing to a level approaching carrying capacity".
Response: As indicted in our response to Comments 18 and 19, bull trout redd count and
population density data is used in the context of the supplemental indicators. These supplemental
indicators were used only to assist in making current water quality impairment determinations. In
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Appendix E
Flathead River Headwaters TPA
the context of supplemental indicators, we feel that a qualitative measure of a "stable or
increasing trend" is appropriate.
If we chose to use bull trout redd counts and/or population densities as targets (i.e., water quality
goals for the future as opposed to supplemental indicators for making water quality impairment
determinations), such as those shown in Section 4.2, we would agree that the above-suggested
change would be appropriate. However, given the reasons presented in our response to comment
18, we do not believe that bull trout redd counts or population densities are appropriate targets for
assessing compliance with water quality standards, in this case.
21. Comment: Too much reliance has been placed on Pfankuch channel stability ratings. This
method is mainly a qualitative, rapid assessment technique.
Response: As described in Section 3.3.2.3, Pfankuch channel stability ratings were considered
supplemental indicators. As described in Section 3.3, the supplemental indicators were not
considered sufficiently reliable to be used alone as a measure of impairment. Pfankuch ratings,
and all of the supplemental indicators were only used when one or more of the target threshold
values were exceeded to provide supporting and/or collaborative information when used in
context with all of the other available data. The available Pfankuch data provided a "piece of the
puzzle" in the context of the weight-of-evidence approach described in Section 3.3.
22. Comment: Use of visual observations of substrate composition is another low quality parameter.
Visual estimations of substrate are fraught with interobserver bias. Use of this indicator as a
target without a discussion of associated data quality measures is not acceptable.
Response: DEQ recognizes the bias that can be introduced by pebble counts. That understanding
underscored the need to select a suite of targets to evaluate possible sediment impacts. Pebble
counts were used as "one piece of the puzzle" to evaluate sediment impacts on streams in the
Flathead River Headwaters Planning Area. Channel morphology measurements served as a
complement to the pebble count data to evaluate possible changes in channel dimension.
Furthermore, the personnel who conducted the pebble count/substrate analyses were trained
professionals with extensive field experience. These personnel also were contributing authors to
the TMDL report and therefore realized how the data were to be used and the importance of data
bias.
23. Comment: The Flathead assessed 79 sub-watersheds (6th-Code Hydrologic Units, or HUCs) and
found 38% to be "functioning at unacceptable risk" due to road density and locations, 32% to be
"functioning at risk" due to road density and locations, and only 30% to be "functioning
appropriately" in this regard. We ask that you review the Flathead's bull trout biological
assessments and reconsider the TMDL restoration plan in light of them.
Response: The Flathead National Forest was part of the team that prepared this document. As
such, all useable data within the Flathead National Forest's files were used, including the
biological assessments. The conclusions (e.g., functioning appropriately, functioning at risk,
functioning at unacceptable risk) reached in the biological assessment did not necessarily have a
direct relationship to whether or not a water body meets water quality standards. The focus of
this document was on whether or not Montana's narrative standards for sediment were met.
Therefore, the biological assessments were used to provide background information. Also, an
attempt was made to directly obtain and use some of the supporting data that was
collected/compiled when the biological assessment reports were prepared. However, many of the
data contained within the above mentioned biological assessment reports were old and more
recent data was available from other sources. In other cases it was not possible to determine how,
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Flathead River Headwaters TPA
Appendix E
where (specifically), or by what method they were collected. In these cases the data were not
used.
24. Comment: Concerning total suspended solids, this factor represents a significant stressor on fish
and other aquatic life. Thus, it is especially important to account for the severity of this stressor
on aquatic systems. Yet this document does not display any degree of variance.
Response: No recent suspended solids concentration or total suspended solids data were
available for any of the subject streams. The available data, therefore, were used only for
comparison purposes and as collaborating evidence when combined with the other supplemental
indicators and targets. As described in Section 3.3.2.5, suspended sediment concentration data
was considered one of the supplemental indicators and the available data provided a "piece of the
puzzle" in the context of the weight-of-evidence approach described in Section 3.3.
25. Comment: In several places the draft concludes that if cutthroat populations are stable but bull
trout numbers down, then the cause of impairment to the native char cannot be sediment. This
assumes that both species have identical life history strategies and identical sensitivities to
increased sediment in stream systems. That's not necessarily the case.
Response: We agree and considered that in our use of the fisheries data. That is also why fish
data were used only in the context of supplemental indicators.
26. Comment: The determination that Sullivan Creek is not impaired is not supported by data. Table
3-39 says bull trout spawning redd counts are "stable." Yet spawning data in the document
indicates that current redd counts are about 40 percent less than the five-year mean between
1996-2001 (Figure 3-29). How can this condition be considered "stable," and thus fully
supporting aquatic life?
Response: We agree that the use of the word "stable" to describe the bull trout redd count data
presented in Table 3-29 is not appropriate. The language in Table 3-29 and the narrative in the
final document have been changed to "no apparent trend over the period of record".
Nonetheless, the bull trout data evaluated for Sullivan Creek is not conclusive relative to the
water quality impairment status of the stream. As described in Section 3.3.2.4, fish populations
might change from year-to-year due to effects outside of management control such as
temperature, peak runoff, primary productivity, and competition from other fish species, illegal
harvest, invertebrate populations and others. For this reason, fish data were placed in the
supplemental indicator category. As described in Section 3.3, the supplemental indicators were
not considered sufficiently reliable to be used alone as a measure of impairment. Fish data, and
all of the supplemental indicators were only used when one or more of the target threshold values
were exceeded to provide supporting and/or collaborative information when used in context with
all of the other available data.
Using the weight-of-evidence approach described in Section 3.3 it was concluded that Sullivan
Creek was not impaired. Although no data were available regarding McNeil Core subsurface
fines and substrate scores, the other two targets (surface fines and dinger taxa richness) indicated
good water quality conditions in Sullivan Creek. The available macroinvertebrate data suggested
clean, cold water and excellent water quality. The periphyton data suggested no water quality
problems associated with man's actions. A riparian assessment conducted in 2002 indicated
excellent conditions. The Pfankuch results for the downstream sampling site provide the only
indication of a potential source of impairment. However, the low Pfankuck rating at this site are
thought to be largely a result of natural causes.
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Appendix E
Flathead River Headwaters TPA
27. Comment: All conclusions about rebounding redd counts - even though they still remain below
historical averages ~ do not consider additional causal elements. For example, the small
rebounds that have occurred in some tributaries in the last five or six years cannot necessarily be
attributed to improved habitat conditions. During this period, the fish were listed as threatened
and, importantly, all legal harvest was curtailed.
Response: We agree and that is why fish data were only used in the context of supplemental
indicators. See responses to Comments 18, 19, and 20.
28. Comment: DEQ needs to re-evaluate this draft TMDL before it delists any stream. DEQ needs
additional data.
Response: Considerable additional data were collected and evaluated relative to all of the subject
streams and a rigorous weight-of-evidence approach was used to verify water quality impairments
as described in Section 3.3. The additional data that has been collected and evaluated has been
described previously in our response to Comment 9.
29. Comment: A huge amount of sediment was contributed to Mathias and South Coal. However,
this material has been transported downstream over the years, and its now deposited in Lower
Coal Creek and is causing the chronic high sediment levels.
Response: Although we have been unable to quantify the amount of sediment that has been
historically delivered to Lower Coal Creek, we agree that the current degraded condition of
Lower Coal Creek is likely at least partially a result of past actions.
30. Comment: I totally disagree with the lower Coal Creek impairment summary.
Response: Comment noted. Based on discussions with numerous water quality specialists,
hydrologists, and fisheries biologists employed by the U.S. Forest Service, U.S. Fish and Wildlife
Service, Montana Fish, Wildlife and Parks, Montana Department of Environmental Quality, and
U.S. EPA, there is much disagreement over the cause of water quality impairment in Coal Creek.
That is why the next step in the process for Coal Creek involves further study as described in
Sections 4.4 through 4.6. As mentioned in earlier comments, the Flathead Basin Commission is
applying for grant funds to implement this study.
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Flathead River Headwaters TPA Appendix F
APPENDIX F: PUBLIC NOTICE OF AVAILABILITY
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Flathead River Headwaters TPA
Appendix F
FOR IMMEDIATE RELEASE FOR MORE INFORMATION
October 20, 2004
Ron Steg
(406) 457-5024
steg.ron@epa.gov
SEEKING COMMENTS ON THE WATER QUALITY ASSESSMENT AND TMDLS FOR THE
FLATHEAD HEADWATERS PLANNING AREA
HELENA - The Montana Department of Environmental Quality and United States
Environmental Protection Agency has released a draft water quality protection plan for the
Flathead River Headwaters TMDL Planning Area. The document addresses twelve water bodies
and includes a Total Maximum Daily Load (TMDL) for sediment in the Coal Creek Watershed
where the Bull Trout population has declined. A TMDL is the total amount of a pollutant that a
water body may receive from all sources without exceeding water quality standards. The
Flathead River Headwaters is found in Flathead County near Kalispell, Montana.
The DEQ invites members of the public to attend an open house on Monday November 8, 2004
in the "Large Conference Room" at the Montana Department of Fish, Wildlife and Parks offices
at 490 North Meridian, Kalispell Montana. Open house hours are from 3:00 to 8:00 pm. A short
presentation will start at 6:00 pm. Members of the public may stop by at a time convenient to
speak with a water quality specialist about their questions and comments.
The Department will make reasonable accommodations for persons with disabilities who wish to
participate in this open house or who need an alternative accessible format of this notice. If you
require an accommodation, please contact Carole Mackin, no later than 5:00 p.m., November 3,
2004 at (406) 444-7425; fax (406) 444-6836, or by email at cmackin@state.mt.us.
The draft document is available for review on the DEQ web site:
http://www.deq.state.mt.us/index.asp. Public comments will be accepted until 5 p.m., November
20, 2004. The comments may be mailed to Montana Department of Environmental Quality, PO
Box 200901, Helena, Montana 59620-0901 or emailed to TMDLComments@state.mt.us. For
more information please contact Ron Steg, EPA, (406) 457-5024, steg.ron@epa.gov or Robert
Ray, DEQ Watershed Program Manager, 406-444-5319, rrav@state.mt.us .
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