an investigation of the potential to restore native trout

University of Calgary

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Graduate Studies Legacy Theses

2000

An investigation of the potential to restore native

trout populations: Goat Creek, Banff national park,

Alberta

Tough, Elizabeth

Tough, E. (2000). An investigation of the potential to restore native trout populations: Goat

Creek, Banff national park, Alberta (Unpublished master's thesis). University of Calgary, Calgary,

AB. doi:10.11575/PRISM/15482

http://hdl.handle.net/1880/39554

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An Investigation of the Potential to Restore Native Trout Populations: Goat Creek, Banff National Park, Alberta

Elizabeth Tough Masters Degm Project

Faculty of Environmental Design University of Calgary

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Thanks to the EVOS faculty, particularly Dr. Grant Ross, my supen/isor, who provided just the right mix of support, critique and advice on this MDP. Dr. Ken Sato provided thoughtfbl comment on the document, and came all the way from Ottawa for the defense. Dr. Stephen Henero started me on the trail of this fascinating and fun project. And Dr- Rich Revel did what I knew he would do and threw down the gauntlet - I'm glad you had fun.

I gratefully acknowledge the financial support of TransAlta Utilities Corp. and Parks Canada. Charlie Pacas from Parks Canada and Roger Drury from TransAlta not only arranged the financial support for the project, but lent their time, expertise, and insight. Thank you both.

Faculty of other departments at University of Calgary provided much appreciated support. Helen Butler from the Department of Geography lent her own field equipment. Jon Greggs of Geological Sciences granted use of laboratory facilities, and Dr. Leland Jackson from the Department of Biological Sciences lent his time. expertise, equipment and laboratory, and solved the mystery of the sediment filters that didn't filter.

The help of many professionals who answered my innumerable questions and sent weighty packages of information on up-to-the-minute developments in stream restoration is gratefully acknowiedged. Daryl Fields of BCHydro. Jeff Lutch and Mark Buktenica from the United States Park Service, and Bill Horton and Ned Homer of Idaho Fish and Game all provided great information.

Peter Eaton carried half the load of the big job of fieldwork and most of the load of field equipment. Karen Oldershaw and Glen DePaoli took a huge load off my mind by providing absolutely reliable fieldwork (and dealing admirably with the only grizzly to make an appearance). Paul Godman from TransAlta and Elaine O'Neil from Parks Canada lent their time, expertise and senses of humour to the fieldwork. Thank you all.

Thanks to Christine, who not only provided expert knowledge on benthic invertebrates, but made devastatingly good cocktails to go with very late night problem-solving sessions. And to Karen Sharp, who gives great advice and gave me a welcoming home in the West.

Carol: thanks for distracting me.

Thanks to Todd for teaching me how to sleep and saying it's okay to take a day off. 1'11 remember that.

And always, thanks to my parents, for your continued support, friendship and love. Couldn't have done it without you.

ABSTRACT

This project investigated the potential to restore native fish populations and their associated habitat in Goat Creek, Banff National Park. The laws. policies and management plan for Banff National Park established the scope and goal of the research and management recommendations, which were to restore natural Row patterns in the impounded stream and to re-establish a native fish population. Changes to the fish community and habitat resulting from impoundment for hydroelectric power generation and introduction of non-native fish were determined from comparison between historical information and data gathered in the field. Field data were analyzed using preference curves for cutthroat trout and bull trout to determine the suitability of the habitat for these native fish. The analysis showed that the limiting habitat elements were poor pool and cover habitat, high summer water temperatures, and the presence of non-native brook trout. Changes to the hydrology of Goat Creek from impoundment reduced watershed area by 41.6% and reduced largest recorded annual flood by 78.8%. Extreme flow events from dam failures and stable annual flows created the existing instream habitat. Restoration of a native fish population in Goat Creek would require removing brook trout and constructing bamen to prevent their recolonization, and improving instream habitat to address limiting fadon. Increased water releases from power generation structures during the months of May, June, July, and August would mimic natural flow patterns and address the Banff National Park goal of restoring more natural Rows. As well as physical management of water flows, fish populations, and instream habitat, restoration of Goat Crsek would involve collaboration with the Alberta provincial government and creation of a public information program.

Key words: watershed planning. stream restoration, National Parks, stream impoundment, non-native fish, cutthroat trout, bull trout

.......................................................................... EXECUTIVE SUMMARY

.................................................................. CHAPTER 1 : INTROOUCTION

PURPOSE ................................................................................... ............................................................................... OBJECTIVES

METHODOLOGY .......................................................................... Phase 1 ............................................................................. Phase 2 ............................................................................. Phase 3 ............................................................................. Phase 4 ............................................................................. Phase 5 .............................................................................

CHAPTER 2: CONTEXT ................................................................

TARGET SPECIES ........................................................................ Cutthroat trout ..................................................................... Bull trout ............................................................................

.................... EFFECTS OF IMPOUNDMENT ON SALMONID HABITAT Flow modification ............................................................... Sediment ........................................................................... Temperature. ...................................................................... Riparian areas ..................................................................... Benthic community ............. ... ............................................. Fish community ...................................................................

INTRODUCTION OF NON-NATIVE FISH POPULATIONS ..................... Hybridization ....................................................................... Corn pe tition ........................................................................ Predation ...........................................................................

......................................................... CHAPTER 3: RESTORATION

INSTREAM FLOWS ....................................................................... ...... ......................... BCHydro and the Alouette River. 8C .......

............................................................. I NSTREAM STRUCTURES Projects using instream techniques ..........................................

RIPARIAN VEGETATION ............................................................... REMOVAL OF NON-NATIVE SPECIES .............................................

Elemfishing ...................................................................... Chemical Piscicides .............. ,... ..... .................................... Angling ..............................................................................

........................................................... CHAPTER 4: GOAT CREEK 32

........................................................................... INTRODUCTION ................................................ LEGAL AND POLICY FRAMEWORK

............................................................................. Federal Fisheries Act ............................................................. Fisheries Act Regulations ............................................ National Parks Act .....................................................

............................................................. Parks Policy ........................... Banff National Park Management Plan

Provincial ........................................................................... Water Act .................................................................

......................................... Bull h u t management plan . TransAlta Ubl~ties ................................................................. .............................................................................. STUDY AREA

....................................................................... Area Climate HISTORY OF DEVELOPMENT ........................................................ HISTORICAL CONDITIONS ............................................................

Watershed ......................................................................... ................................................................................ Flows

Fish and habitat .................................................................. ..................................................................... CURRENT HABITAT

Representative reaches ........................................................ .................................................................... Data collection

................................................................ Discharge Temperature .............................................................

..................................................................... Survey ................................................................. Substrate

.......................................................... Fish population Instream cover .......................................................... Riparian vegetation .................................................... Wafer characteflstics ..................................................

.................................................. Benthic invertebrates HABITAT SUITABILITY FOR TARGET SPECIES ................................

..................................................................... Cutthroat trout ............................................................................ Bull trout

Limiting Factors ...................................................................

GOAT CREEK RESTORATION POTENTIAL ...................................... Removal of non-native species ............................................... Flow Modification ................................................................. lnstrearn techniques ............................................................. Riparian Areas ....................................................................

CHAPTER 5: SUMMARY AND RECOMMENDATIONS ........................

.................................................................................. SUM MARY RECOMMENDATIONS ..................................................................

Organizational Recommendations ........................................... Specific Recommendations ...................................................

REFERENCES .............................................................................

APPENDIX I: Determination Of Historical Flows In Goat Creek ............... APPENDIX II: Historical Flow Data .................................................... APPENDIX Ill: Habitat Suitability Curves ............................................

Table 1 Table 2 Table 3 Table 4 Table 5 Table 6 Table 7 Table 8 Table 9 Table 10 Table 11 Table 12 Table 1 3

Cutthroat trout life stages and habitat needs Bull trout life stages and habitat needs lnstream habitat restoration techniques Changes in hydrological regime in Goat Creek Substrate size categories Results of electrofishing activities Goat Creek suitability for cutthroat trout Habitat suitability results for cutthroat trout Habitat suitability results for bull trout Costs for scenario one Costs for scenario two Limiting factors and instream restoration techniques Summary of issues, effects and restoration techniques

LIST OF FIGURES

Figure 1 Figure 2 Figure 3 Figure 4 Figure 5

Figure 6 Figure 7 Figure 8 Figure 9 Figure 10 Figure 11 Figure 12 Figure 13 Figure 14

Figure 15 figure 16 figure 17 Figure 18 Figure 19

Figure 20 Figure 21 Figure 22 Figure 23

Goat Creek Watershed Climate at Town of Banff Timeline of management activities on Goat Creek TransAlta's Spray River system generation system Changes to drainage in the Spray River watershed from impoundment Changes to Goat Creek hydrograph following regulation Representative reach 1 Representative reach 2 Representative reach 3 Goat Creek hydrograph summer 1998 Goat Creek summer hydrograph 1999 Reach 1 maximum and minimum temperatures 1998-1 999 Reach 2 maximum and minimum temperatures 1998-1 999 Reach 3 maximum and minimum temperatures with comparison to Healy Creek Goat Creek Reach 1 Goat Creek Reach 2 Goat Creek Reach 3 Goat Creek percent substrate composition by reach Percent composition by fork length of Goat Creek brook trout population Percent instream cover by reach Shrub species for Goat Creek Herb species for Goat Creek Hydrographs for scenarios one and two

EXECUTIVE SUMMARY

Indigenous salmonid populations in Alberta have declined over the last century,

Among these populations, cutthroat trout and bull trout have disappeared from

much of their original habitat in the province as they have elsewhere in western

Canada and the United States. Studies base this decline on habitat degradation

from human manipulations and on the introduction and subsequent dominance of

non-native fish species. The purpose of this project is to identify, assess, and

recommend stream habitat management activities that address effects of

impoundment and non-native species stocking for salmonids native to Alberta.

Goat Creek. in Banff National Park. provides a case study on which to focus

investigations. The laws, policies and management plan for Banff National Park

established the scope and goal of the research and management

recommendations, which were to restore natural flow patterns in the impounded

stream and to re-establish a native fish population. Parks Canada's definition of

ecological integrity determined the context for this project.

Restoration of degraded habitat and fish populations needs to focus broadly, on

activities affecting watershed processes rather than narrowly on a single stream

channel. To restore impounded streams populated with non-native fish. several

techniques are available. Flow augmentation. either overall or to mimic natural

hydrographs, will increase useable habitat area and redistribute substrate to

create more diverse instream habitat. Successful methods to remove non-native

fish include electrofishing and use of poisons. Placement of instream structures

or woody debris creates habitat both directly, in providing fish cover, and

indirectly, in affecting scouring and deposition of sediments.

Goat Creek is part of the TransAlta Utilities Corporation (TAU) power generation

system on the Spray River watershed, adjacent to Banff National Park (BNP).

Current habitat and fish populations in Goat Creek are the result of changes over

the last 47 years since impaundment and stocking of non-native trout. Historical

analysis of Goat Creek indicates that impoundment structures reduced

watershed area, annual floods, minimum discharges. and mean annual

discharge to varying degrees. The most important flow change, from the

perspective of the Banff National Park Management Plan, is the change from a

natural hydrograph, with peak flows from May to August, to a steady discharge

over the year. Brook trout stocked into Goat Pond by Alberta fisheries managers

displaced native cutthroat trout and other native fish species and now dominate

the fish community in Goat Creek

Habitat data gathered from representative reaches on Goat Creek and analyzed

using Habitat Suitability Indices (HSI) indicate that current habitat for cutthroat

and bull trout is limited by lack of good quality pools. Other habitat elements rate

high on the HSI scales for both species and all life stages.

To meet Parks Canada's goal of restoring ecological integrity to Goat Creek,

non-native fish would have to be removed, a native cutthroat trout population

stocked, and flows would have to be augmented in the historic high flow season

from May to August to mimic the natural hydrograph. To successfully eradicate

non-native trout species, barriers to fish movement would have to be constructed

on flow outlets on TAU facilities.

Because Goat Creek originates on provincially managed lands, management of

Goat Creek falls not only to BNP, but also to the Province of Alberta, and to

TransAlta Utilities. All three organizations have commitments in policy and law to

managing environmental impacts on aquatic environments and to working with

neighbouring jurisdictions.

Recommendations for restoring Goat Creek:

The recommendations provide a framework for planning if Parks Canada

chooses restoration of Goat Creek as an element of its goal to restore ecological

integrity.

Organizational

1. It is recommended that any restoration plans for Goat Creek focus on

restoring ecological integrity by restoring natural structure and functions.

2. It is recommended that Parks Canada create a public information program

and public consultation program to educate the public on its plans to restore

aquatic ecosystems and to encourage support for such programs.

3. It is recommended that restoration potential for Goat Creek be reviewed in

context with other projects investigating restoration potential on streams in

BNP.

4. It is recommended that Parks Canada collaborate with provincial fisheries

managers on any restoration plan for Goat Creek.

Specific

5. It is recommended that Parks Canada and TAU use the information in this

report on historic conditions in Goat Creek in defining restoration goals.

6. It is recommended that Parks Canada work with TAU to determine feasibility

of building structures to block fish passage through flow outlets.

7. It is recommended that Parks Canada investigate the possibility of using

piscicides in BNP.

8. It is recommended that Parks Canada and TransAlta Utilities work together to

define a water budget and determine desired flow amounts.

9. It is recommended that Parks Canada include use of large woody debris in

the stream to work in concert with increased flows and accelerate habitat

formation.

CHAPTER 1

INTRODUCTION

Indigenous salmonid populations in Alberta have declined over the last century.

Among these populations, cutthroat trout and bull trout have disappeared from

much of their original habitat in the province as they have elsewhere in western

Canada and the United States. Investigations of such populations concluded

that habitat loss and degradation are primary concerns (Mclntyre and Rieman

1995). Others (Behnke in Mclntyre and Rieman 1995) concluded that 'brown

trout. brook trout, and rainbow trout, along with changes in flow and water quality

were responsible for the demise of the westslope cutthroat trout in [drainages it

originally inhabited]".

PURPOSE

The purpose of this project is to identify and assess stream habitat management

and enhancement activities that address effects of impoundment and non-native

species stocking on native salmonids in Banff National Park and to recommend

management actions for restoring fish habitat and an indigenous fish population.

The National Parks Act, Parks Policy, and the Banff National Park Management

Plan all identify ecological integrity as a goal in Park management. Parks

Canada defines ecological integrity as:

"the condition of an ecosystem where 1 ) the structure and function of the ecosystem are unimpaired by stresses induced by human activity, and 2) the ecosystem's biological diversity and supporting processes are likely to persistn

This project examines restoration potential for Goat Creek within the context of

this definition of ecological integrity. The structure (the fish community and its

associated habitat) of the Goat Creek ecosystem has been affected by stocking

CHAPTER 1: INTRODUCTION

of non-native species and regulation of water flow. The effects of flow

impoundment have altered the functions associated with natural discharge

patterns and sediment supply (including instream habitat creation and inputs

from riparian areas).

OBJECTIVES

The study objectives are:

To investigate the potential to improve fish habitat so that indigenous fish

populations can be restored and maintained;

to identify the effects on salrnonid habitat and native salmonids of stream

impoundment and introduction of non-native fish species;

to assess the effectiveness and feasibility of various restoration strategies,

including direct habitat redamation techniques and flow alteration; and

to use this assessment to make recommendations on management actions

for restoration of fish habitat and an indigenous fish population.

METHODOLOGY

Phase 1

Phase 1 was a literature review of native salrnonids in Alberta and their habitat

needs; of effects of stream impoundment on salmonid habitat; and of effects of

introducing non-native fish species on indigenous salmonids. These reviews

provided a context and guide on which to base further investigation.

Phase 2

In phase 2 1 broadened the literature review to identify restoration strategies for

stream habitats. I focussed on those strategies and activities that specifically

address the effects of flow alteration and presence of introduced species

identified in phase one. Restoration strategies focussed on modifications to flow.

physical changes to stream channels. and re-introduction of native salmonids.

CHAPTER I : INTRODUCTION

Phase 3

To illustrate effects of human uses on fish habitat I completed a case study of

Goat Creek in Banff National Park (BNP). Both impoundment and introduction of

non-native species have affected the fish community and habitat in this stream.

Field data collection provided the basis for describing the current state of Goat

Creek; historical records identified forces that created that state. This case study

put the results of the literature review in context and sewed as a concrete

example of human stresses and biological responses in stream habitat needed to

ground restoration work in reality. Historical information on past biological

capacity guided in defining targets for restoration (Rabeni and Sowa 1996;

Ebersole. Liss, and Frissell 1996).

Phase 4

Phase 4 involved investigating the feasibility of successfully implementing the

various restoration strategies. In the United States and in western Canada.

where native trout are in decline. numerous projects have begun processes for

restoration (Young 1995; Columbia River Basin Fish and Wildlife Program 1 996).

Research into these programs. and discussions with specialists in the field

pointed to successful and unsuccessful measures. This research focussed on

projects addressing the effects of impoundment and of competition with

introduced species. However. the research also investigated feasibility of

restoration strategies in the political, economic, and social context by identifying

resistance to or non-participation in such restoration projects by those with a

stake in the outcome. Ways in which any such resistance has been mediated

through discussion or education were also identified.

Phase 5

To prepare recommendations for restoring fish habitat. I assessed potential

restoration strategies according to likelihood of success in addressing the effects

identified in previous phases. The assessment was based on my interpretation

of the results of the discussion with specialists, the literature, from the

CHAPTER 1: INTRODUCTION

examination of similar projects, and from information about Goat Creek. It

included aspects of habitat ecology. hydroelectric power generation and

engineering, and economics. The assessment indicated which potential

restoration strategies are the most practical to pursue in different situations as

well as those specifically aimed at restoring Goat Creek. The recommendations

are based on this assessment. Also. I included in the recommendations. ways in

which deficiencies identified in methods could be addressed.

CHAPTER 2

CONTEXT

TARGET SPECIES

To focus this study I selected cutthroat trout and bull trout (Salvelinus

confluentus) as the target species for habitat restoration, since both are native to

Alberta and are in decline.

'Explorers and surveyors of the late 1800s wrote that trout 'of two kinds'

abounded 'in all the streams from the Bow River to h e Boundary Line' [Montana

border] in Alberta. The fish are recognizable in written descriptions from that

time as bull trout and cutthroat troutn (Mayhood 1998).

Westslope cutthroat (0. clarki lewisi), the subspecies native to Banff National

Park (BNP), and bull trout coevolved, resulting in some unique characteristics in

the cutthroat trout. The westslope subspecies differs from the other subspecies

by being less piscivorous (Trotter 1987). possibly as a result of coevolving with

the highly piscivomus bull trout. Studies (Mclntyre and Rieman 1995; McPhail

and Baxter 1996) have shown that sympatric populations of bull and cutthroat

trout populations segregate regarding use of habitat and prey meaning the two

can coexist in the same stream. Both bull and cutthroat trout are vulnerable to

displacement through competition by non-native trout species. Brook trout and

other introduced species have displaced native trout in many areas of Canada

and the United States (Behnke 1992; Mclntyre and Rieman 1995; Banff-Bow

Valley Study 1996; McPhail and Baxter 1997; Meyer 1998; Buktenica 1998).

CHAPTER 3 RESTORATION

Cutthroat Trout

The species cutthroat trout consists of 1 3 recognized subspecies, all

geographically distinct and with genetic variations (Hickman and Raleigh 1982;

Trotter 1987; Behnke 1992). The subspecies native to Alberta is the westslope

cutthroat trout (0. clarki lewisi), who's native range covers western Montana.

northern Idaho and southern Alberta (Trotter 1987). The Bow River drainage is

the northern limit of the westslope cutthroat trout range (Mayhood 1998). The

westslope subspecies is less piscivorous than other cutthroat trout (Trotter 1987;

Behnke 1992), with a diet of aquatic invertebrates. Behnke (1992) states that the

westslope cutthroat trout is not piscivorous because it coevolved with the highly

piscivorous bull trout.

Across the historic range the subspecies is in decline, as are most of the other 12

subspecies (Hickman and Raleigh 1982; Behnke 1992; Banff-Bow Valley Study

1 992). Habitat degradation and fragmentation. introduction of non-native

species, and angling pressure account for the decline of all subspecies of

cutthroat trout everywhere in its range (Mclntyre and Rieman 1995; Schindler

and Pacas 1996; Thompson and Rahel1996). Road and rail development and

hydroelectric impoundment cause habitat degradation and fragmentation in Banff

National Park (Banff-Bow Valley Study 1996). These developments affect

instream flows, alter the natural pattern of floods, and change instream habitat

and water quality. The introduction and subsequent dominance of non-native

fish species alters the composition of the native fish population through

hybridization, competition and predation. The Banff-Bow Valley Study (1 996)

found that development impacts and the effects of over fishing reduced the

populations of cutthroat trout in 8NP. Cutthroat trout, once abundant in the Bow

Valley are now virtually absent from the Bow River below Lake Louise (Banff-

Bow Valley Study 1996).


The International Union for the Conservation of Nature (IUCN). which monitors

World Heritage Sites, considers westslope cutthroat trout a Species of Special

Concern (Banff-Bow Valley Study 1996). Westslope cutthroat trout are under

consideration for designation as threatened species under the United States

Endangered Species Act. Cutthroat trout habitat requirements are shown in

Table 1.

Table 1 : Cutthroat trout life stages and habitat needs (Information summarized from Mudry and Green 1976; Hickman and Raleigh 1982; Trotter 1987; Borek and Rahel1991; Mclntyre and Rieman 1995; Herger et al. 1996; and Young 1996)

Life Stage All

Adult Cutthroat trout begin to mature at age 3 but usually spawn first at age 4 or 5. They spawn From March to July when water temperatures reach 10°C Juvenile

Fry Fry emerge roughly two weeks after hatching when they are 20mm long. They rapidly disperse to nearby resting areas with good cover Embryo Embryos hatch after 28- 49 days.

Dodrabla habitat features Streamside vegetation for canopy shade, allochthonous input, and bank stabilization Dissdved oxygen levels between 7 and 9mg/L pH range of 7-9, with 7.5-8.5 as optimal A base flow of 50% of average annual daily flow Cdd water with a temperature range of 7-1 6°C with an optimal r a m of 9-1 2°C Water velocities of 0.14.3m/s and depth greater than 1 5cm Cover for hiding. resting and feeding in the form of overhanging vegetation, undercut banks, deep water, and surface turbulence Substrate suitable for aquatic insects composed mostly of rubble with tow percentage of fines Poo1:riffle ratio of 1:1 to provide both resting areas and food production areas Water velocities of 0.25-O.Sm/s and depths of 45-75cm Prefer instream rather than streamside cover in the form of main channel pools. substrate cover, and log jams Low substrate embeddedness to allow fish to enter substrate for winter cover Lower velocities and shallower water than other life stages, with velocities <O.O8m/s Cover along stream margins, low velocity areas, backwaters, and side channels Rubble 1040cm along stream margin for winter cover

Velocities of 0.3-0.4ds at depth of 17-20cm Gravel substrate with low embeddedness low percentage of fines Substrate size of 2-7 5rnm depending on size of spawners Incubation temperature around 10°C


Bull Trout

Original range of bull trout covered most of Oregon. Washington. Idaho.

Montana, and British Columbia, extending into western Alberta and southern

Yukon and Northwest Territories. Now. however. its range has contracted in the

south and populations are in decline over its remaining range (McPhail and

Baxter 1996). Bull trout are a member of the char species along with brook trout

(Salvelinus fontinalis), and like all char it is a fall spawner (US Fish and Wildlife

(USFWS) 1998).

Bull trout are listed as threatened species under the United States Endangered

Species Act (US Fish and Wildlife (USFWS) 1999). United States Fish and

Wildlife Service (USFWS) considers bull trout an indicator species whose

condition reflects the state of the ecosystem (Banff-Bow Valley Study 1 996). Bull

trout are Alberta's Provincial fish and are listed as a Species of Special Concern

in Alberta (Alberta Environment n.d.). The Fish and Wildlife Management

Division of Alberta Environment prepared a Bull Trout Species Management and

Recovery Plan in 1995 to address population declines in bull trout. A zero limit

on bull trout and an information and education program, as well as plans to

protect and restore bull trout habitat are all designed to increase bull trout

populations.

Bull trout in Banff National Park are subjected to the same stresses of habitat

degradation as cutthroat trout. Like cutthroat trout. bull trout spawn in tributaries

that are now modified by hydroelectric dams and road and rail construction. Bull

trout are vulnerable to displacement by brook trout. In stream for which data

exists, brook trout now occupy 100% of bull trout habitat (Banff-Bow Valley Study

1996). Brook trout reproduce much younger than bull trout and populations of

brook trout grow quickly (Colorado DNR 1998; Buktenica 1998). Brook trout

hybridize with bull trout to produce sterile offspring, further limiting the numbers

of bull trout (Banff-Bow Valley Study 1996; Buktenica 1998; Meyer 1998).


Table 2: Bull Trout life stages and habitat needs (Information summarized from Pratt 1985; Shepard 1985; Carl 1985; McPhail and Baxter 1 996; and Fernet and Bjomson 1997) I ~ i f e stage I Desirable Habitat features I

Populations exist at low densities. l Temperature < 15°C Base flows high percentage of average annual daily flow for winter cover habitat

Adult and redd cover Deep pools for cover and winter cover

Stream resident populations rarely grow larger than 300mm and average 200mm. Highly piscivorous. favouring mountain whitefish (Prosopium williamson~ or other bull trout

Juvenile 1 Age 1 +, 2+, and 3+ As they grow, juveniles change their feeding habits from aquatic insects to small fish once they reach -1 1 Omm. They grow rapidly, often reaching 60-70mm by the end of the first summer.

FV Eggs hatch after 51 days(at 10°C) to 126 (at 2OC) days, with better survival rates at lower temperatures Fry emerge from gravels 223 days after deposition Newly emerged fry measure 17.0 to 26.3 mm Embryo Bull trout redds are relatively large - up to 1.5 X 2m. Redd are associated with bank cover and spring or groundwater input Spawning takes place in fall and could be triggered by temperature (around 9°C) or other factors such as daylight levels

Cold temperatures Presence of prey population optimal . Depths greater man O.Sm Velocities between 0.1 and 0.4 rn/s Pools for early summer cover with velocities 0.1 -0.25rn/s and depths 0.1 to 1 .Om Pools associated with submerged cover Temperature 42OC . Coarse substrate Cover - large woody debris dams that allow flow through, undercut banks Large loose gravel for interstitial cover along banks Shallow water 0.1 to 0.4m deep and low velocity (<I 6cm/s) Instream cover (unembedded rocks, woody debris) Substrate suitable for aquatic insects Spawning sites characterized by low gradient High percentage of small gravel (20mm) Low velocities from 0.25 to 0.5rnls Proximity to cover Depths of 1 Ocm - 1 .Om

Optimal development temperatures of 2 - d o c


EFFECTS OF IMPOUNDMENT ON SALMONID HABITAT

Dams are one of the main causes of stream habitat degradation and elimination

of lotic habitat in North America (Holden 1980; Petts 1989; Mclntyre and Rieman

1995; Bain and Trawnichek 1996). Damming results in a direct loss of free

flowing river habitat and creates barriers to upstream spawning areas (Petts

1984; Prowse and Conly 1996)). Reservoirs created in place of streams change

the habitat from a lotic to a lentic environment. Dam effects on fish and fish

habitat are both immediate and delayed (Holden 1980; Prowse and Conly 1996).

Immediate, or first order impacts block upstream and downstream migration

either to headwater streams and lakes or to downstream rivers and lakes.

Second order impacts follow, with low flows affecting habitat structure. This

study focuses on the downstream effects of dams, specifically hydroelectric

structures. The downstream effects of dams and associated structures include

Row and temperature changes, disruption of the sediment regime, and the

resulting effects on habitat structure and the organisms it supports. These

effects are described in the following sections.

Flow Modification

Dams alter water flow into downstream river reaches by reducing flows,

dewatering, or flooding stream reaches. If water flows are generated through

turbines, flows can fluctuate hourly, daily, monthly, and annually. Large daily

fluctuations can preclude the development of off channel refuges or deep, slow

pools required by stream fish (Holden 1 980). With short-term flow fluctuations,

the rate of flow increase or decrease is a most important factor in determining

impacts on downstream environments (Petts 1984). Rapid increases in flow can

increase streambank erosion and lead to loss of riparian habitat (Federal

Interagency Stream Restoration Working Group (FISRWG) 1998). lnstream flow

fluctuations favour adaptable species, often reducing species diversity and

biomass (Schindler and Pacas 1996).


Lower flows reduce the area of useable habitat, as water depth and stream width

decrease (Petts 1984). Also, at lower flows, the length of the deepest part of the

stream (the thalweg) decreases because the thalweg meanders less at lower

flows (Herger et al. 1996). Lower flows combined with altered sediment regimes

change channel structure. Depending on the stream environment, the channel

may become shallower or deeper based on flow rates and availability of

sediment (Petts 1984; FISRWG 1998).

Sediment

Flow regulation reduces flood magnitudes and lowen the ability of flows to move

sediment, resulting in accumulation of fine material in the substrate (Petts 1984;

FISRWG 1998). Channels aggrade when there is a source of sediments and the

reduced flows are not sufficient enough to carry them away (Bovee 1982; Petts

1984). Impoundments isdate sediment sources coming from upstream areas

(Ward and Stanford 1985; Prowse and Conly 1996). Sediments previously

available from upstream sources used in shaping the stream are reduced as they

collect behind the dam (Holden 1980; Petts 1984). If flows remain great enough

to transport sediment, the channel will degrade since no new sediment is

available to replenish supply (Bovee 1 982; Prowse and Conly 1 996; Fl SRWG

1998). The release of clear, sediment-free water from reservoirs into channels

with transportable bed materials can lead to erosion. Such channel degradation

and scour only occur, though, if regulated flows are sufficient to move substrate.

Both channel degradation and aggradation occur under natural conditions.

However, under natural conditions, inputs of new sediment are ongoing. In an

impounded stream, when sediment is removed and not replaced, the channel

becomes armoured (Armitage 1984). If the channel aggrades under modified

flows, sediment collects in interstitial spaces in the sediment and reduces

spawning area and habitat for benthic invertebrates (Armitage 1984;Ward and

Stanford 1985). The reduction in sediments that create stream structure reduces

habitat variability below dams, especially the slower, fine-bottomed pool areas


required by young fish as resting areas (HoMen 1980; Petts 1989; Swales 1989).

Without new sources of sediment, the natural riffle:nm pattern that provides the

balance of habitat for fish and benthic invertebrates can be lost (Swales 1989;

FISRWG 1998).

The effects of lowered sediment input from upstream sources diminish further

downstream of the dam as other sources of sediment from tributary streams and

channel-bank erosion enter the stream (Petts 1984; Prowse and Conly 1996).

Temperature

Depending on the use of the dam and the water flows different effects will be

observed (Holden 1980). If the reservoir outlet releases epilimnion-level water

receiving bodies will experience higher temperatures than normal. If the outlet is

in the hypolimnion levels of the reservoir, cooler water will flow through and

depress the temperature in the downstream river (Holden 1980; Prowse and

Conly 1 996; Schindler and Pacas 1996; FISRWG 1998). Also, dams that create

relatively constant flows can result in constant temperatures. Unnaturally low

flows allow water to warm up and hold less dissolved oxygen (Armitage 1984;

Ward and Stanford 1985; FISRWG 1998). a limiting factor for salmonid

populations (Hickman and Raleigh 1982; Schindler and Pacas 1996). Colder

waters from hypolimnion-level discharge are often oxygen poor.

Changes in the temperature regime can favour one species over another,

interfere with seasonal triggers to migration and spawning. alter the productivity

of the stream, and change the availability of invertebrate organisms (Petts 1984;

Prowse and Conly 1996; Schindler and Pacas 1996).


Riparian Areas

The "energy supplied by riparian vegetation drives the stream community and, in

part. determines its structure" (Risser and Hanis 1989). Up to 95% of the energy

available to small streams comes from riparian vegetation (Risser and Ham's

1989). The interaction of flooding, sedimentation and flow changes alters the

characteristics of the riparian community (Petts 1984; Schindler and Pacas 1996;

FISRWG 1998). Channel changes below dams affect the rate of recolonization

and development of riparian and floodplain vegetation (Petts 1984). Under

natural conditions, floods erode fine sediments from the channel and deposit

them on the bank, replenishing the soil layer and providing soil and nutrients to

the riparian plant community. Established riparian vegetation traps sediments

from overland flow and reduce bank erosion and channel change (Petts 1984).

"River impoundment can alter [riparian areas because] .. . the depletion of fine

suspended solids would reduce the rate of over-bank accretion, so that new

floodplains would take longer and longer to mature, and the soils would remain

infertile" (Petts 1 984: 127). Thus recolonization of historic floodplains by riparian

vegetation is slowed due to lack of soil and nutrient deposition.

Benthic Community

Flow and temperature are the most important factors controlling the benthic

invertebrate community (Arrnitage 1984). Flow regulation affects the benthic

invertebrate community through interactions between flows and temperatures

(Petts 1984; Schindler and Pacas 1996). Reduced flows result in lower velocity

which allows water temperatures to rise. and reduced wetted width which directly

reduces amount of instream habitat (Ward and Stanford 1985; Arrnitage 1989).

Sedimentation in interstitial spaces in the substrate also reduces the total amount

of habitat available to benthic invertebrates (Arrnitage 1989). In comparison

studies between natural and dammed streams, impounded streams exhibited

reduced diversity of benthos. alterations of the mmmunlty composition, and


higher standing crops (Petts 1984; Henricson and Sjoberg 1984). Increased

standing crops are associated with stabilized discharges and higher water

temperatures (Mudry and Green 1976; Ward and Stanford 1985). Species

adapted to naturally fluctuating temperatures will suffer in habitat with more

stable temperatures (Armitage 1984). Unnatural flow fluctuations, low summer

water temperatures and low DO levels result in decreased standing crops (Petts

1984). Cornmunlty composition changes as habitat conditions change and

favour one species over another. Discharge levels affect the availability of food,

resulting in changes in the dominance of different functional feeding groups

(Henricson and Sjoberg 1984). Grazers will increase if instream algae growUl is

favoured by higher temperatures. while numbers of shredders will decrease with

lower amount of large woody debris (LWD) avaifable from riparian areas

(Henricson and Sjoberg 1984; Ward and Stanford 1985). Allochthonous input is

important in the productivity in stream and thus to the benthos (Petts 1984).

Reduction in stream width from much lower discharges will leave bank areas

unvegetated. perhaps for decades, limiting inputs from the riparian ecosystem.

Fish Community

"River flow is one of the primary environmental characteristics inff uencing riverine

fish populations . . . major changes to the natural flow regime can have severe

effects on fish stocks: (Swales 1989: 189). Although dams can have positive

effects on fish habitat by lowering levels of suspended sediment, regulating

temperature, and regulating large floods and preventing drought. flow

modification and associated effects often cause changes in fish populations

(Holden 1980; Petts 1984; Ward and Stanford 1985; Petts 1989; Swales 1989;

FISRWG 1998). Discharge directly affects width, depth, velocity. and variations

and timing of flows. Reduced discharge means less useable habitat. Changes

to timing and amounts of flow and to temperature result in changes in fish

community structure (Ward and Stanford 1985). The standing crop can either

increase or decrease depending on habitat conditions and species present (Ward

CHAE'TER 3 RESTORATION

and Stanford 1985; Prowse and Conly 1996). 'Exotic fish . . . find suitable

conditions below dams where indigenous species have been reduced or

eliminated by the altered thermal, sediment and flow conditions (Ward and

Stanford 1 985).

Dams are one of the main causes of stream habitat degradation and removal in

North America (Holden 1980; Mclntyre and Rieman 1995; Bain and Trawnichek

1996). Damming results in a direct loss of free flowing river habitat and creates

barriers to upstream spawning areas (Petts 1984). Reservoirs created in place

of streams change the habitat from a lotic to a lentic environment. Dam effects

on fish and fish habitat are both immediate and delayed (Holden 1980).

Immediate, or first order impacts, block upstream and downstream migration

either to headwater streams and lakes or to downstream rivers and lakes.

Second order impacts follow, with low flows affecting habitat structure. This

study focuses on the downstream effects of dams, specifically hydroelectric

structures. These effects indude flow and temperature changes, disruption of

the sediment regime, and the resulting effects on habitat structure and the

organisms it supports.

INTRODUCTION OF NON-NATIVE FISH POPULATIONS

Non-native trout species have been stocked in water in western North America

for decades, usually to improve angling potential (Wooding 1994). Historically

fisheries managers in Canada, the United States, and as far off as Chile and

Argentina. responded to angler wishes by stocking more preferred species such

as brook trout (Wooding 1994; Mclntyre and Rieman 1995; Schindler and Pacas

1996). Wooding (1 994: 102) spells out the attitude, saying, 'brook trout. because

of their unblemished reputation, endearing characteristics and adaptability to

foreign waters, are among our most successful piscatorial goodwill

ambassadorsn. Historically, records of fish stocking in provincial waters in

Alberta are not well documented (Stelfox pers. camm.), but widespread


introduction of eastern brook trout into lakes and rivers in the southwestern part

of the province is noted in fisheries records. Rainbow (Oncorhynchus mykiss),

and lake trout (Salvelinus namaycush) were also introduced in the decades up to

1987 (Stelfox pers. comm.). Similar, better documented, introductions occurred

in BNP (Thompson and Wiebe 1974; Pams pers. comm.). As a result of these

introductions, many lakes and rivers in BNP now support populations dominated

by non-native species (Banff-Bow Valley Study 1996).

Three types of effects can occur when non-native species are introduced into

waters with native fish populations: hybridization, competition. and predation.

Hybridization

The main factor differentiating trout (cutthroat tmut) from char (bull trout) is

spawning time, with char spawning in the fall and trout in the spring and summer

(Wooding 1994). Spawning timing determines which species will be most at risk

from hybridization with which non-native fish. Non-native fish historically

introduced into Alberta include lake and brook tmut, both chars, and rainbow

trout, a trout. Rainbow and cutthroat tmut will hybridize, as will brook and bull

trout. Hybridization with non-native species alters genetic strains of native fish.

This has happened with the various subspecies of cutthroat trout and bull trout

across their historic ranges (Mclntyre and Rieman 1995; Buktenica 1998). Brook

trout and bull trout readily hybridize to produce sterile offspring. reducing the

reproductive success of bull trout (Banff-Bow Valley Study 1996; BuMenica 1998;

Meyer 1998; Temple et al. 1998).

Competition

The principal competitors of salmonids are other salmonids because of overlaps

in requirements for space and food (Stream Enhancement Guide 1980).

Introducing species into waters where they did not evolve means that the new


mixed populations have not been subjected to natural selection that would have

produced differences in resource use and thus lessened the effects of

competition (Fausch 1988). Therefore combinations of fish species, such as

westslope cutthroat and brook trout, compete strongly for limited resources. The

cutthroat trout does not persist for long after introduction of brook trout in most

areas (Fausch 1988; Mclntyre and Rieman 1995). Brook trout also dominate bull

trout in most of the bull trout's original habitat (Banff-Bow Valley Study 1996;

U S M S 1998). Brook trout begin reproducing as young as 18 months so

populations can quickly grow and take over available habitat. This factor

combined with the potential for reducing bull trout productivity through

hybridization favours growth of brook trout populations and they supplant bull

trout populations (USFWS n.d.; Banff-Bow Valley Study 1996)

"Competition among streamdwelling salmonids usually involves aggressive

interactions among individuals in an attempt to secure optimal sites for feeding

and predator avoidance" (DeStaso and Rahel 1994). Therefore the more

dominant fish succeed. Brook trout often displace cutthroat trout and their

dominance is influenced by several factors. Since brook trout spawn in fall, their

young emerge in the spring. Cutthroat trout spawn in the spring and their young

emerge in the fall. This gives young of the year brook trout a size advantage

over cutthroat trout of the same age, with differences of up to 20 mm (DeStaso

and Rahel 1994). This greater size gives brook trout young of the year a

competitive advantage and young of the year cutthroat trout may experience

increased mortality over natural levels because they are unable to compete

(DeStaso and Rahel 1994; FISRWG 1998). Since natural mortality rates are

roughly 99%. any increase could quickly decimate a population (Hunter 1991 ).

Also, brook trout mature one to two years earlier than cutthroat trout and thus

produce more offspring (DeStaso and Rahel 1 994; Wooding 1994).

Habitat features also play a role in competition between native and introduced

species.


"In general, species alterations may be associated with three impacts: the establishment of lethal conditions for one, or more, life-history stage or stages; the alteration of environmental conditions in favour of a competitor, prey or predator; or the introduction of exotics either intentionally or accidentally" (Petts 1 984236).

The interaction of flow regulation effects and the presence of non-native species

can have great impacts on native populations. Since native populations evolve in

a stream habitat with naturally fluctuating flows and specific conditions, changing

those conditions stresses the population (FISRWG 1998).

"The introduction of exotic species has induced the local extinction of many native species which, although reduced in population, might otherwise have maintained a reproductive stock under the regulated flow regime" (Petts 1984).

"As the habitat becomes marginal for the [native] species. it becomes more preferred for the exotic competition. At that point, the [native] species becomes more detrimentally impacted by the exotic species than by the habitat change" (Holden 1980).

Griffith (1972) and De Staso and Rahel (1994) found that water temperature and

velocity affected interactions between native and introduced salmonids. DeStaso

and Rahel(1994) found that at 10°C cutthroat trout used much higher stream

velocities than brook trout, but at 20°C they used similar stream velocities. Thus

there is less overlap of habitat use at lower temperatures and DeStaso and

Rahel noted that the species appear to be equal competitors at lower

temperatures. Griffiths' 1972 study showed differences in habitat use related to

velocity. Cutthroat trout used areas of low velocity when brook trout were not

present, but not when brook trout were present. Therefore in streams with lower

velocities, with brook trout present, cutthroat trout will have less habitat available

than at higher velocities. Both studies note that brook trout tend to dominate in

streams with low gradient and low velocity, often at low elevations. De Staso and

Rahel (1 994) also note that in some streams brook trout do not displace cutthroat

trout. They attribute this to low winter flows dewatering redds and freezing of

eggs due to anchor ice. Cutthroat trout redds are not vulnerable during winter,


and those fish are better adapted to fast current and lower temperatures in high

elevation streams (Griffth 1972; De Staso and Rahel 1994).

Predation

Some introduced species. including brook trout and lake trout, are piscivorous

(Wooding 1 994). Westslope cutthroat trout, having evolved with piscivorous bull

trout, feeds on aquatic invertebrates (Trotter 1987; Behnke 1992). This trait may

make them more vulnerable to domination by mare piscivorous introduced

species. Bull trout population levels have declined since the introduction of non-

native species because anglers saw the piscivorous bull trout as a threat to the

introduced species that were their favoured targets (Alberta Environment n.d.).

Large scale removal of bull trout by anglers to protect non-native stocks led to

rapid population declines.



"All restorations are exercises in approximation and in reconstruction of naturalistic rather than natural assemblages of plants and animals with their physical environmentsn (National Research Council 1992: 18)

In the 1930s, an emphasis on conservation and preservation of wet lands

emerged in the United States. In 1934, the United States Bureau of Sport

Fisheries began a nationwide program of stream suweys and habitat

improvement projects (Hunter 1991 ). Even at that time, though, some wonied

that enthusiasm for instream works would not address limiting factors (Hunter

1991 ). Limiting facton on fish populations were not identified and thus little

benefit resulted from the works. In 1952, the United States Forest Sewice

produced a fish stream improvement handbook that incorporated lessons learned

from past mistakes (Hunter 1991 ). They recognized that fewer, better designed

works placed after an evaluation of impacts on the stream, would be more

successful. In 1967, the Guidelines for the Manaaement of Trout Stream Habitat

in Wisconsin, by Ray R. White and O.M. Brynildson took the process further

(Hunter 1991). The guidelines emphasized pre-project planning and focused on

bank stability, recognizing the interdisciplinary nature of stream improvement

(Hunter 1991).

Fisheries managers now stress a holistic approach that involves project planning,

defining clear objectives, correctly identifying limiting factors on stream habitat,

and post-project monitoring (Bmokes et al. 1996; FISRWG 1998; British

Columbia Ministry of Environment 1994; Bozek and Rahel 1991 ). Habitat

restoration focuses less on building instream habitat structures and more on a

land use planning approach. The National Research Council (1 992) states that

restoration should begin with improved land management practices that allow

natural restoration to occur, such as erosion control, grazing management and

flow management.


In defining restoration objectives, decisions must be made about the desired

future condition: whether it should be pristine, naturalistic, or aesthetically

pleasing (Brookes and Sear 1996). Historical analysis of watershed

characteristics, instrearn habitat. and fish populations points to causes of

degradation and can help in defining future scenarios and setting realistic and

appropriate goals (Kondolf and Downs 1996; Ebersole et al. 1997).

To restore streams. managers must have an understanding of fish habitat needs

and identify the factors that liml fish populations. Once identified, limiting factors

can be specifically addressed (Bozek and Rahel 1991 ; FISRWG 1 998). When

limiting factors are not correctly identified, restoration may not be successful if

limiting attributes are not addressed (Bustard 1984; Stream Enhancement Guide

1980).

To restore streams affected by flow regulation, non-native species presence. and

degraded habitat several restoration techniques can be used. An assessment of

instream flow needs and capabilities addresses overall watershed issues, as well

as instream habitat; instream habitat structures improve habitat directly; and

methods to eradicate or reduce nonnative species may be necessary for

reestablishment of native fish populations.

INSTREAM FLOWS

Flows below dams are reduced from historic levels causing changes in instream

and riparian habitat (Petts 1984; FISRWG 1998). As part of a restoration effort.

capabilities and needs for increased flow need to be addressed. Bain and

Trawnichek (1996) confirmed that enhancing river flows resulted in a predicted

faunal restoration. A multi-agency effort (FISRWG 1998) in the United States

concludes that

"The modification of operation approaches, where possible, in combination with the application of properly designed and applied best management practices. can

2 1


reduce the impacts caused by dams on downstream riparian and floodplain habitats".

Methods to determine instream flow needs developed in the 1970s to address

conflicts between water user values. including recreational, aesthetic, fisheries,

and industrial users (Petts 1984; Stalnaker et al. 1995; Cardwell et al. 1996).

Older methods of assessment often resulted in recommendations for minimum

flows in streams. Newer methods assess the instream effects of alternative

development scenarios and determine minimum and optimum flows considering

carrying capacity for fish populations.

Ways to determine instream flows range from the simple, involving no field data

gathering, to detailed, requiring large amounts of field data, fish habitat

requirements. and sophisticated computer programs. Incremental methodologies

for balancing instream flow needs with recreational users and industry needs

allow for flexibility and are used for bargaining in highly controversial situations.

The method can be expensive and time-consuming, but is based on fish needs

and habitat variables (Bovee 1982; Stalnaker et al. 1995). In situations where

there is little controversy, standard-setting measures based on historical water

flows can and have been applied (Stalnaker et al. 1995; FISRWG 1998).

In standard setting techniques, hydrological records are analysed to determine

flows. For a minimum flow, one method selects the median flow for the lowest

flow month as adequate throughout the year. another uses median monthly flows

to mimic an natural flow pattern (Stalnaker et al. 1995; FISRWG 1998).

The lnstream Flow Incremental Methodology (IFIM) is a procedure for

determining instream flows when multiple users with varying needs and values

are included in the process. l FIM uses two types of tools to display effects on

habitat for different flow levels. One tool uses statistical analysis relating

standing crop of fish to environmental features in the stream. The other links

hydraulics with fish behaviour (Bovee 1982; Stalnaker et al. 1995). calculating

C-R 3 RESTORATION

amounts of different quality habitat at various flows by using suitability criteria.

Several suitability cunres have been developed for various species (Stalna ker

1980; Hickman and Raleigh 1982; Fernet and Bjomson 1997). These look at

each habitat element separately and assign values between zero and one, one

being optimum, to levels of, or presence of each habitat element as they relate to

each species (Hickman and Raleigh 1982; FISRWG 1998; Stalnaker et al. 1995).

Both tools require large amounts of data and produce stream-specific results.

Water budgets are another method to manage flows for multiple users,

developed in the United States (Stalnaker et al. 1995). Water budgets allot a

portion of water stored in a reservoir for fisheries benefit uses that could be

released when most needed. This concept is now considered during evaluation

of water storage projects in the United States (Stalnaker et al. 1995) and in

British Columbia (BCHydm 1 998).

BCHydro and the Alouette River, British Columbia

BCHydro operates a hydroelectric facility on the Alouette River in southern British

Columbia. Impoundment structures built in the 1 920s greatly lowered flows in

the river from historic levels; however, flows are stable, since generating facilities

release water from turbines into another river. In 1995, in response to

community concerns about the state of the habitat and fish population in the

Alouette River, BCHydro agreed to increase base flows from 0.566 m3/s (20 cfs)

to 1.981 m3/s (70 cfs) until the development of a formal Water Use Plan. To

develop the Water Use Plan, the Alouette Stakeholder Committee was struck,

which included members from BCHydro, community groups, and all levels of

government. This committee reached agreement on all major aspects of the

Water Use Plan based on five objectives that addressed economic, recreational,

ecological, and scientific issues. To measure water use and ecological effects

they considered the amount of high quality fish habitat and the similarity of the

hydrograph to a natural hydrograph. Also, recognizing levels of uncertainty in


existing knowledge of fish habitat in the river, the committee proposed a flexible

and adaptive management plan. To allow such flexibility the committee

proposed a water budget that would allow modifications to agreed upon flows,

providing for flood protection, normal fish water releases, flushing flows, and

monitoring. The annual budget is set at $440,000 and within that budget, over a

four year cycle, the Alouette Management Committee can manage flows for

greatest effect. Studies to assess fish habitat and population health and to

monitor effects of flow increases are ongoing (BCHydro 1996).

INSTREAM STRUCTURES

Some fisheries managers have criticized the use of instream structures since the

1930s, saying that such structures do not address the causes of degradation,

and provide only a band-aid solution (Hunter 1991 ; Beschta et al. 1994).

Beschta at al. (1994) believe the emphasis on using instream structures stems

from various reasons ranging from political pressures that limit solutions, funding

limitations and management styles that focus on quantifiable results, a

reductionist perspective, and limited understanding of ecological processes.

They conclude that abusive land practices cannot be addressed by structural

additions to stream channels and that restoration should focus on the larger

scale of land use management.

However, instream structures can be used to improve habitat quality in streams

degraded by low flows due to regulation, along with a wider management

approach (Petts 1989; Swales 1989). Recovery of degraded streams with trout

populations at risk can be accelerated using instream habitat restoration

techniques that are based on an understanding of hydrology, channel

characteristics, fish habitat requirements, and limiting factors (House 1996).

lnstrearn structures can reproduce key characteristics of productive trout

streams, including habitat diversity and cover (BC MELP/MoF 1994; Bmokes et

al. 1996).


lnstream structures can create pools. provide hiding cover. improve substrate for

spawning and benthic habitat, encourage riparian vegetation growth, and help

regulate water temperature. Identification of limiting factors of fish populations is

critical in success of restoration efforts using instream structures. Efforts to

improve pool habitat for adult fish. for example, will not help the population if

juvenile habitat limits success (Flosi and Reynolds 1991 ; Hunter 1991 ; FISRWG

1998).

Success also depends on selection of and siting of materials (Stream

Enhancement Guide 1980; Wesche 1985; Flosi and Reynolds 1991 ; BC

MELPlMoF 1994). Emphasis in current restoration projects is on using naturally

available materials. Such materials are inexpensive. especially if available near

the site, and, if flood flows move structures downstream, aesthetics are not

adversely affects as they would be with use of cement and wire constructions

(BC MELPIMoF 1994). Structures must also be placed so that they do not cause

negative effects on instream or riparian habitat. The methods must suit hydraulic

and geomorphic conditions or will result in erosion or filling pools with sediment

(Flosi and Reynolds 1991; BC MELPlMoF 1994; Stream Enhancement Guide

1980).

According to Wesche (1985) the most commonly used in-channel treatments to

improve fish habitat are current deflectors, overpour structures such as dams and

weirs, bank covers, and boulder placements. These structures can be used

alone or together and have been used successfully in the past to improve habitat

(Stream Enhancement Guide 1980; Wesche 1985; Swales 1989; Brookes et al.

1996; House 1996;Hiderbrand et al. 1997). In Table 3 the variety of structures

used, their function, and the environments for which they are best suited are

summarized.

Table 3: Instream habitat restoration techniques (Summarized from Nelson et al, 1978; Stream Enhancement Guide 1980; Bustard 1984; Wesche 1985; Tripp 1986; Flosi and Reynolds . . i 991 ; Brookes et al. 1996; Erickson 1996; Hiderbrand et al. 1997) Type I Function I Suitability ~eflectors

Narrow channel by at least 3O0/0 Spaced 5-7 channel width apart Easy to construct with rocks or logs Lou possibility of destruction by

I high flows Limited disturbance to bed and bank

1 Build below riffle to preserve riffle

I but also build pool

Direct flow and eliminate accumulated sediment Narrow the channel to increase velocity Scour pools Enhance pool-riffle ratios Help keep water temperatures cool Encourage development of riparian vegetation by means of silt bar formation Protect stream banks from erosion Remove silt from spawning gravels

Wide, shallow, low gradient streams lacking pools Not usually successful In gradient > 3% Reaches with low sediment loads Opposite bank must be stable to prevent erosion

Weirs and check dams Low cost if built from natural materials Can create pools up to 70% larger than natural Spaced 5-7 channel widths apart low enough to allow fish passage

Substrate placement

Impound flow above weir to create pool Increase velocity downstream and create a scour pool Aerate water

Improve spawning and benthic habitat

Smaller streams (< 9m) with slopes of ) 0.5 - 20% without high flood flows Ftows < 2.83m3/s (100cfs) Straight reaches with few pools Stable bed and banks Low sediment load

Stream width <14rn, slope < 0.3 % I 1 Provlde cover I Stable nows, I

Boulders (60-100 cm diarneter)randomly placed in cluster of four to eight

Provide rearing habitat Restore meanders and pools.

Dense spawning populations Boulders have greatest effect in stream with <20% pools

Cover structures

Large woody debris An alternative to fixed structures in deficient channels because pieces are free to shift and adjust

Provide overhead cover

8

Creates complex habitat Increases number of sites where scouring and deposition occur

6 Material used for cover chosen based on d u

target fish species Potential for debris accumulation

~

Best in stable low order streams

E

2

CHAPTER 3: RESTORATION

Projects using instream techniques

Although artificial instream structures have been used for a century (Hunter

1991; Beschta et al. 1994). many instrearn restoration undertakings were not

monitored so there are limited records of successes and failures (Beschta et al.

1994; House 1996; Koning 1998). Those records that exist showcase failures

and successes, although reasons for outcomes are not often given. For this

reason, examples of failures, though there are many (Beschta et al. 1995). are

not included here. It is sufficient to note that, in the records of stream

restorations using instream techniques, failures out number successes.

House (1 996) reports on a restoration project that placed wood and boulder

structures in a stream to increase habitat for salmonids in a section of a stream.

After restoration, the treated section of the stream. representing 2% of habitat,

supported 24% of the population of the target species. This study also examined

the durability and success of instream works including boulders and wood. All

such structures remained in place over the twelve year span of study. Structures

that did not span the width of the stream maintained pool depth, while those

structures that spanned the channel trapped gravel bed load and created pool

habitat (House 1996). House concludes that instream structures are interim

methods for stream restoration, only used until activities that caused the initial

degradation are modified or eliminated.

Another study (Tripp 1986) tested the effect of large woody debris (LWD)

placement on pool habitat creation. Only pieces of LWD smaller than what might

be moved by major flood were anchored (Tripp 1986). Some LWD was laid on

the streambed to deflect flows downward and scour a pool, and some were

imbedded to make plunge pools. Winter storm flows filled all pools, but over the

next season, new ones were scoured. The thalweg profile was more variable

after LWD and the number of pools increased from four to 12. After the winter


storm event obliterated pools, subsequent scouring created 21 new pools. In the

control section where no LWD was added, little channel change occurred.

Placement of large woody debris (LWD) into the stream channel has produced

other successes in improving habitat (Hiderbrand et al. 1997; Young 1996).

Hiderbrand et al. (1997) showed that 70% of the pools in one channel were

created by LWD. Young (1996) found that cutthroat trout use of pools created by

LWD was proportionately high compared to pools created by meanders. This

study also found that the siting of LWD for stream habitat enhancement based on

planning and expertise led to better results that random placement.

RIPARIAN REVEGETATION

Riparian vegetation plays a part in the structure and function of the stream

ecosystem (Ohmart and Anderson 1 986). It helps control temperature, sta bikes

banks, provides food sources to stream organisms, and is a source of LWD

(Ohmart and Anderson 1986; FISRWG 1998). Along streams with reduced

flows, the riparian community can be affected by a lower water table. and may be

isolated from the channel if lower flows result in a narrower channel. Without

periodic flood flows that deposit fine material on the banks, revegetation will be

hampered by lack of soil. Even if vegetation begins reestablishing on newly

exposed banks immediately, it takes decades to grow to a size useful in LWD

(Erickson 1996).

Native plants should be used in any revegetation effort. so an understanding of

natural plant communities at the site is necessary (FISRWG 1998). Planting and

transplanting vegetation is an established method for long-term restoration of the

watershed (Flosi and Reynolds 1991). Willow sprigging, which uses willow

cuttings is inexpensive and effective. (Stream Enhancement Guide 1980; Nelson

et al. 1978; Flosi and Reynolds 1991 ; FISRWG 1 998). Willows grow quickly and

cuttings can be easily gathered from vegetation on the site. Once shrubs are


established they will intercept fine material from overland runoff and begin

establishing a soil cover that will support other species (FISRWG 1998). Sedges

and grasses are also used to stabilize stream banks and can be direct seeded if

soil exists (Nelson et al. 1978).

REMOVAL OF NON-NATIVE SPECIES

Generally, three methods are available for removing unwanted fish from streams:

eledrofishing, chemical pisdcides. and selective angling. Wih any method.

barriers to reentry of non-native fish are necessary (Stream Enhancement Guide

1980).

Also, with any method. there may be strong public opposition to removing non-

native species. Brook tmut and other non-native species in Alberta, are

favourites of anglers (Wooding 1994). Many current projects focusing on non-

native species removal, in United States National Parks and in Alberta, have met

with resistance from anglers (Lutch pers. comm.; Paul pers. comm.).

Electrofishing

Electrofishing involves generating either a DC or an AC electric current (either

with a gasoline-powered generator or batteries) through various styles of

electrodes into the water to create an electric field. The electric field stuns fish

within an effective zone of roughly one meter radius, then fish are collected with

a net. It is an effective fisheries management tool used for making population

surveys, but labour time involved and inefficiencies in removal limit the method

for removing entire populations from a stream (Thompson and Rahel 1996).

One study assessed depletion-removal electrofishing on three small streams as

an alternative to piscicides (Thompson and Rahef 1996). Thompson and Rahel

conducted three-pass electrofishing on an enclosed reach, taking 206 hours for a


section 1.6 m wide and 4 km long. In these three passes. they estimate they

removed 73-1 00% of age 0 b m k trout and 59-1 00% of older fish. but note that

these are higher efficiencies than other studies. They were not able to

completely eradicate brook trout, and neither did any other study. Very low

numbers of brook trout can quickly multiply and dominate a community of

cutthroat trout within five years (Behnke 1992) so complete removal of brook

trout would be necessary to restore cutthroat trout.

Idaho Fish and Game Department is also trying to remove non-native brook trout

using backpack eledrofishing, with varying degrees of success (Homer pers.

comm.). They found that success in removing brook trout was related to the type

of habitat. Streams with dense riparian vegetation of alder and willow reduced

success rates. but in streams with little riparian vegetation removal rates were

higher. Ineffective removal of young of the year lessened the effects here as in

other projects (Homer pers. comrn., Paul pers. comm.). Since brook trout mature

at one or two years of age, any removal that misses young of the year will not be

successful.

Chemical Piscicides

Piscicides, while they remove non-native fish, also kill non-target fish and food

organisms in the stream. They also have the potential to affect waters

downstream. outside the target area (Thompson and Rahel 1996). Rotenone, a

common piscicide, has been used by biologists for decades to remove non-

native fish populations before restocking with native fish (Colorado DNR 1998).

Its effects are neutralized by potassium perrnanganate. Even with relatively high

removal rates, mufti year treatments are often necessary to remove all fish

(Colorado DNR1998).

In Crater Lake National Park in Oregon, fisheries managers are working to

reestablish bull trout populations in Sun Creek that were diminished by


competition and hybridization wlh non-native brook trout (Buktenica 1998). The

Sun Creek project began in 1991 and centers around the removal of non-native

brook trout using chemical poisoning with Antimycin, which is not available for

use in Canada. The brook trout population has been dramatically reduced in an

attempt to stabilize and increase the numbers of bull trout.

In 1998, Colorado Department of Natural Resources treated eleven miles of

Beaver Creek with rotenone to remove populations of brook, rainbow, and brown

trout as part of an effort to reestablish a native cutthroat trout population

(Colorado DNR 1998). The project took 25 workers three days to complete.

Biologists set up ten sites for drip stations to apply rotenone. and some workers

walked the length of the stream spraying rotenone into remote areas. DNR

constructed a barrier to prevent fish movement up from downstream waters and

applied potassium permanganate at the barrier. The Beaver Creek project

follows a successful project in West Beaver Creek, in which non-native fish were

removed by rotenone and native cutthroat trout were stocked. Four years after

the first stocking and two years after the second, a population of cutthroat trout

are now established.

Angling

Experienced anglers. who can correctly identify trout species have been used to

remove non-native species. This however, has not been found to be a

successful method to eradicate fish, particularly with brook trout (Paul pers.

comm.). In a study on Quirk Creek in Alberta, anglers have been removing all

brook trout caught for two years in an effort to reduce the population (Paul pers

comm.). Even though they have caught large numbers of brook trout, the

population remains constant. This may be because, unlike native trout, brook

trout begin to reproduce before they reach a size that is vulnerable to angling.

CHAPTER 4 GOAT CREEK, ALBERTA

INTRODUCTION

In 1952 TransAlta Utilities (TAU) completed construction of facilities on the Spray

River system to hold water for power generation modifying flows in Goat Creek

(Johns pers. wrnm.). The modifications to instrearn flows have changed fish

habitat and may have been a factor in changes in fish populations. Information

about the historic and current Ash community in Goat Creek indicates the

comrnunlty has changed over the last 25 years from one of native to one of

introduced species (Courtney et al. 1992). Both Parks Canada and Alberta

fisheries managers stocked non-native species into Banff National Park and

adjacent waters from the 1930s to the 1980s. Indigenous fish populations in

Goat Creek, in BNP have thus been subjected to both types of stresses

examined in the foregoing chapters: competition from introduced species and

effects of flow regulation.

In 1974 Thompson and Wiebe found that Goat Creek's fish population consisted

of 94 percent cutthroat trout, and found spawning beds in the lower reaches of

Goat Creek that they believed were used by cutthroat trout from both Goat Creek

and the Spray River. In 1992, when Environmental Management Associates

(EMA) electrofished seven sites in Goat Creek and in the Spray River

downstream of Goat Creek, they found only brook trout (Courtney et al. 1992).

Changes to fish habitat from lower water levels may also have been a factor in

this population change from a native species to an introduced exotic that is more

able to adapt.

CHAPTER 4 GOAT CREEK

LEGAL AND POLICY FRAMEWORK

Goat Creek runs for roughly six km from its beginning on provincial land before

crossing into 8NP. Because the stream crosses jurisdictions and is managed by

TAU, laws and policies affecting federal and provincial governments. as well as

corporate policies for TAU are reviewed here.

The National Parks Act, Parks Policy, and the Banff National Park Management

Plan all identlfy ecological integrity as a goal in Park management. Parks

Canada defines ecological integnfy as:

'Yhe condition of an ecosystem where 1) the structure and function of the ecosystem are unimpaired by stresses induced by human adivlty, and 2) the ecosystem's biological diversity and supporting processes are likely to persist"

This project examines restoration potential for Goat Creek within the context of

this definition of ecological integrity.

Federal

Fisheries Act

The Fisheries Act, administered by Department of Fisheries and Oceans (DFO).

controls all activities that could have an effect on fish or fish habitat. Some

sections apply directly to environments like Goat Creek's in addressing flows

below dams in Section 22:

(3) The owner or occupier of any obstruction shall permit the escape into

the river-bed below the obstruction of such quantity of water. at all times,

as will, in the opinion of the Minister, be sufficient for the safety of fish and

for the flooding of the spawning grounds to such depth as will. in the

opinion of the Minister, be necessary for the safety of the ova deposited

thereon.


The Act also covers devices to prevent escape of fish where the Minister deems

necessary, in Section 26:

(3) The Minister may authorize the placing and maintaining of barriers,

screens or other obstructions in streams to prevent the escape of fish held

for fish breeding purposes or any other purpose that the Minister deems in

the public interest, and no person shall injure any such barrier, screen or

other obstruction.

And Section 30:

(1 ) Every water intake, ditch, channel or canal in Canada constructed or

adapted for conducting water from any Canadian fisheries waters for

irrigating, manufacturing, power generation, domestic or other purposes

shall, if the Minister deems it necessary in the public interest. be provided

at its entrance or intake with a fish guard or a screen, covering or netting

so fixed as to prevent the passage of fish from any Canadian fisheries

waters into the water intake, ditch, channel or canal.

Even providing specifications on the structure of fish guards

(2) The fish guard, screen, covering or netting referred to in subsection (1 )

shall

(a) have meshes or holes of such dimensions as the Minister may

prescribe; and

(b) be built and maintained by the owner or occupier of the water intake,

ditch, channel or canal referred to in subsection (l), subject to the


approval of the Minister or of such officer as the Minister may appoint to

examine it-

Duty of owner to keep in repair

(3) The owner or occupier of the water intake, ditch, channel or canal

referred to in subsection (1) shall maintain the fish guard. screen, covering

or netting referred to in that subsection in a good and efficient state of

repair and shall not perrnl its removal except for renewal or repair.

The Fisheries Act also addresses destruction of fish in Section 32:

No person shall destroy fish by any means other than fishing except as

authorized by the Minister or under regulations made by the Governor in

Council under this Act.

The Act's most allencompassing Section (35) states that:

(1 ) No person shall carry on any work or undertaking that results in the

harmful alteration, disruption or destruction of fish habitat.

Unless authorized by the Minister, or under regulations under the Act.

Fisheries Act Regulations

Fish Toxicant Regulations

Section 6 of the regulations allows use of fish toxicants when

(a) the Minister or the chief fishery officer is satisfied that the eradication of

any fish that is a pest by the use of fish toxicants in any waters set out in

section 4 and the subsequent restocking of those waters will enhance

fishing in those waters


When and if (Section 7)

the deposit does not adversely affect fish in the waters adjacent to the

waters where the deposit is made.

Also, the Department of Fisheries and Oceans Policy for the Management of Fish

Habitat states as its long-term policy obiective, an overall net gain in the

productive capacity of fish habitat.

National Parks Acf

The Ministry of Canadian Heritage administers the National Parks Act, which

mandates maintaining ecological integrity and including public participation in

management activities. The mandate for ecological integrity forms the basis for

this project in investigating the potential for native species reintroduction. Public

participation will be needed to ensure success in any attempt to restore fish

populations.

5. (1.2) Maintenance of ecological integrity through the protection of

natural resources shall be the first priority when considering park zoning

and visitor use in a management plan.

5. (1 -4) The Minister shall, as appropriate, provide opportunities for public

participation at the national, regional and local levels in the development

of parks policy, management plans and such other matters as the Minister

deems relevant.


Parks Policy

Several sections of the Parks Policy apply to the issues around Goat Creek. It

states that (S. 3.2) Ecosystem-Based Management will form the framework for

undertakings in the Parks. The subsections that apply directly are:

3.2.3

National park ecosystems will be managed with minimal interference to

natural processes. However, active management may be allowed when

the structure or function of an ecosystem has been seriously altered and

manipulation is the only possible alternative available to restore ecological

integrity.

3.2.5

Where manipulation is necessary it will be based on scientific research,

use techniques that duplicate natural processes as closely as possible.

and be carefully monitored.

3.2.10

A species of plant or animal, which was native to but is no longer present

in the park, may be reintroduced after scientific research has shown that

reintroduction is likely to succeed and that there will be no significant

negative effects on the park and neighbouring lands. Parks Canada will

seek the cooperation of adjacent land owners and land management

agencies to ensure success of reintroduction programs.

3.2.1 1

All practical efforts will be made to prevent the introduction of exotic plants

and animals into national parks, and to eliminate or contain them where

they already exist.


3.2.1 2

Fish stocking will be discontinued except where necessary to restore

indigenous fish populations that have been adversely affected by habitat

modification.

Banff National Park Management Plan

Based on the National Parks Act and on Parks Canada's policies, the

management plan for BNP focuses on reducing stress on the environment and

restoring natural processes wherever possible. It recognizes the need to work

cooperatively with other land managers in neighbouring jurisdictions on issues

such as land use, and habitat security. As well as initiating programs to help

people understand the effect of their actions on the ecosystem.

For aquatics specifically, BNP management plan notes that over the past

century, activities such as the construction of dams and the introduction of non-

native fish have affected the aquatic resources. To address this, the

management plan seeks to maintain and, if possible, restore natural water flow,

water levels, and the biodiversity of the park's aquatic ecosystems. To do his

BNP will work with TAU to restore more natural water flow in the Cascade and

Spray systems.

Provincial

Since Goat Pond and part of Goat Creek fall under provincial jurisdiction, Alberta

laws will apply. Alberta Environmental Protection's Natural Resource Service is

responsible for management of water resources within the province and of water

matters held in common with other provinces and the federal government. They

also oversee conservation of Alberta's fish and wildlife resources.


Water Act

The Water Act's aquatic environment protection strategy (Section 8). stresses

biodiversity as:

the variability among living organisms and the ecological complexes of

which they are a part, and includes diversity within and between species

and ecosystems.

And states that

(2) The Minister must establish a strategy for the protection of the aquatic

environment as part of the framework for water management planning for

the Province.

Bull Trouf Management Plan

Alberta Environment's Natural Resource Service considers bull trout a

threatened wildlife species and had developed a management and recovery plan

for the fish. The plan protects existing stock from losses and plans to reestablish

bull trout and its associated habitat where feasible.

TransAlta Utilities

TransAlta is organized into five business segments, each with a clearly defined

strategic mandate: Generation, Transmission 8 Distribution, Independent Power

Projects, New Zealand and Energy Marketing. Generation department oversees

the facilities on the Spray River watershed. There is also a department of

Sustainable Development that oversees environmental policy and addresses

environmental issues such as green house emissions.

In TAU'S generating capabilities, coal is the major fuel source, with a potential of

3.676 MW. Hydro is second at 800 MW of generating capability, followed by gas


and other at 798 MW capacity (TransAlta). The thirteen hydroelectric plants

mainly provide electricity during periods of peak demand.

TAU'S corporate environment policy states that TransAlta Corporation will:

meet or surpass all environmental legislation, regulations, and other

applicable requirements and continuously improve the company's

environmental performance consistent with defined goals.

fully integrate environmental and economic considerations into the company's

processes of planning, constructing. operating and decommissioning.

ensure that the environmental impacts and risks of company activities are

identified, assessed and managed.

proactively advocate socially responsible laws and regulations and, where

appropriate, market-based and voluntary approaches for achieving

environmental objectives.

inform and encourage meaningful consultation and collaboration with

employees, customers, contractors and the public related to the company's

operations and its impact on the environment.

be an environmentally responsible neighbour in the communities in which the

company operates.

identify and develop new business practices and business opportunities

which represent solutions to environmental problems and create value for

shareholders.

use a performance assurance process to assess compliance with this policy

and the company's environmental management system; performance

assurance results will be reported periodically to the board of directors.

All the laws, regulations, and policies outlined here form the legislative framework

for the management of Goat Creek. Any plan for restoration should be based on

and work within this ftamework.


STUDY AREA

Goat Creek is a second order stream that begins immediately below Goat Pond

outside Banff National Park (BNP) and runs for roughly six km before entering

BNP Park in a valley between Mount Rundle and the Goat Range. It then flows

into the Spray River roughly ten km upstream of the town of Banff. Figure 1 on

the following page locates Goat Creek within its larger context.

The study area for this project focuses on Goat Creek from Goat Pond to its

confluence with the Spray River. The Creek has always formed part of the Spray

River watershed, and thus a part of the Bow River watershed. The stream

channel now is similar to the pre-developrnent channel. However, before

impoundment Goat Pond, which feeds Goat Creek, was separated fmrn the

headwaters of the Spray River by a sub-watershed boundary. Goat Creek began

at Goat Pond and flowed roughly 15km to the Spray River, which then flowed ten

km further downstream into the Bow River at the Town of Banff. The Creek still

runs this course, but hydroelectric facilities now move water from the Spray

Lakes Reservoir over the historic watershed boundary and into Goat Pond.

Water flows from there through generation facilities into the Bow River at

Canmore, creating an artificial system different from the historic natural loop of

flows in the Spray River watershed.

Alberta

n - Enlarged map area 1 -- I Park Boundary c-- -.- Taw" m Waterbody

w - - 3 0

i 5m

Watershed Boundary Current - Historic - -

Banff National Park . . . . . Boundary

Goat Creek Trail -*'* -*-• - [ - - a I 0

i lkm


Area Climate

Environmental Canada (1 998) climate data for the area recorded at the town of

Banff, illustrates temperature and precipitation patterns (Figure 2). Snowmelt

feeds most streams in the Bow River system, causing discharge peaks in June,

July, and August. augmented by rainfall and glacial meltwater (Schindfer and

Pacas 1996).

Precipitat ion

,." c@ & 99' *& ,** \a +9 &Q g iQJ ',&

M o n t h

Tern perature

J U l Aug Jun - r

Mav n I S ~ P - daily m ('C 1 daily m ('C daily m

aximum temp

inimum temp

ean ('C)

I Month I I I Figure 2: Climate at tho Town of Banff (Environmant Canada 1998)


Goat Creek watershed sits in the Montane Cordillera Ecozone (Lands Directorate

1986) and within this ecozone. in the Eastern Continental Ranges Ecoregion.

Within the emregion. Goat Creek watershed is a subalpine valley ecosystem,

characterized by warm. dry summers and mild, snowy winters (Lands Directorate

1986). Forests are dominated by lodgepole pine (Pinus cuntuda). Engelmann

spruce (Picea Engelmannio and alpine fir (Abies lasiocarpa). Alpine vegetation.

found in cooler sites (adjacent to streams) in the subalpine region are

characterized by mountain avens (Dryas d m o n d i i ) . Colluvial, morainal and

fluvioglacial deposits are typical of the surficial deposits, covered by Regosolic

and Eutric Brunisolic soils (Ecological Stratification Working Group).

HISTORY OF DEVELOPMENT

As part of the Spray River system, Goat Creek came under investigation for

hydroelectric development in 191 1 (Figure 3). Calgary Power Ltd. (now

TransAlta Utilities Corp.) became interested in 1921 when it realized the potential

of a system so close to the Bow Valley with a potential reservoir 341 m (1 120)

feet above the Bow River (Calgary Power Ltd. circa 1950). Then, and until 1930

when new park boundaries were negotiated. Goat Creek and the Spray Lakes

were entirely within BNP and no development permits were issued (Schindler

and Pacas 1996). The new boundaries excised land and it passed from federal

to provincial government control under the Alberta Natural Resources Act.

Around that time. Calgary Power Ltd. began an expansion program and again

sought permission to develop the Spray River system's power potential (Calgary

Power Ltd. c. 1950). In 1947 the province granted approval to Calgary Power for

the development. The project. completed in 1952, dammed the Spray River at

Spray Canyon and diverted it first into Goat Creek Valley, then over Whiteman's

Pass, dropping into the Bow River at Canmore. The power plants associated

with the development produce 66.1 MW (88,600 hp) and, according to a circa

1950 Calgary Power brochure. are 'picturesquely located in a rugged setting

typical of the mountain country south of Canrnore and Banff.

5,OO ~,i'/s (200cfs) flos in Spriiy River Bi,aIT rcq~lircd for ..figl,tilrg forcs~ lircs, . . . i~nd rctc~l~ioli of ~ I C S I I I C I ~ C pro~rt ics i n Spra!, V;~llc!,".

Flow a~~g~ncnt;llion ~hrough Goal Creck to Spray River slopped,

Lcltcr of coni~rriltric~~t frolit TrilnsAlta Utilities to Banm Niitiot~iil Piirk slipl~lalcs nrininrutir flow of 10 cfs past p~iilpi~rg sli~tion.

Ncw Pdrk Policy focllscs on ccologicirl in~cgrilp.

Banff Bow Vallcy Study finds ccological intcgrity compro~niscd in BanfT Nulional Park.

Banff Mani~gcmcnl Plan idcntifics rcmo\ral of non-riirlivc spccics i111d flow augnicnlation for oil mainmining aquatics ccologici~l intcgrity .

I ~ \ \ c l t;LllLldllUll 511 IILIIIIC'S COIIIJJICICU. UOiII k fL'cK \\ i l lCrSIICU

rcduccd J l.6'% illld flo\vs rcg111;11cd.

I:lo\r.s rcq~~ircd lo IIICCI 5.00 111'1s (200) cfs ill JIIIIC. JII~!. ;11rd Augasl in Spri~y River rclciiscd j~ciirly ~l~rougli GO~II Crcck.

Albcrl Fislr i111d Wildlifc stocks brook (rout into Goilt Pond.

Goat Vallcy Dyke fails: pcik flows rcilch I H 11~31s in Goal Crcck. rcsulling in hid~cst flows on rccord for Sprii!. River it1 Banff.

Tho~~ipso~i and Wcibc study cffccls of dykc fnilurc on Goal Crcck ond find i1 pop~lalion of cullhroal lrotll in a SIrcillli Ilrlbitat \\lill\ fc~v pools.

Mudn aud Grccll find tllilt 11si11g Goill Crcck ;IS ;I spilltvi~y lo allgnlcllt flows ill (hc Spray River I~as dil~liagcd fish llirbiti~t i n Goat Crcck.

Court~lcy cl al. find only brook {rout in il surI1cy of tllc fish community in Goirl Crcck.


Development of the Spray system required that Calgary Power and Parks

Canada negotiate an agreement regarding affected flows within the Park. This

agreement required that Calgary Power provide enough flow into the Spray River

to ensure 5.7 m3/s (200 cfs) at the town of Banff during June, July, and August.

This flow was necessary for Yighting forest fires, proper removal of sewage from

Banff Springs Hotel area. and retention of aesthetic properties in Spray Valleyn

(Mudry and Green 1976). Examination of potential effects on fish populations

focused on maintaining angling potential. From mid-July through to September

the flows in the lower Spray River needed augmentation to flow at 5.7 m3!s (200

cfs) but a valve built into Canyon Dam was not used to provide this l ow from the

reservoir. Instead, flows were augmented through Goat Creek since Wle source

of water for flow augmentation was not stipulated by the Order in Council

allowing dam constructionn (Mudry and Green 1976). Mudry and Green (1976)

also concluded that using Goat Creek 'as a spillway" had resulted in

considerable damage to fish habitat. 'Artificially fluctuating water levels and

occasional dike failures" had also affected habitat (Mudry and Green). Mudry

and Green recommended that flows into the lower Spray River not be augmented

by flows through Goat Creek. and, in 1976, the practice stopped (Golder

Associates Ltd. 1996). Dyke failures during construction in the 1950s and in the

1970s resulted in extremely high flows in Goat Creek. In one instance, peak

flows reached 181 m3/s into the Creek (Golder Associates Ltd. 1996), resulting in

the highest flows on record in the Spray River at Banff (Environment Canada

1990a). Such high flows would likely have had an effect on instream habitat,

filling existing pools and washing woody debris downstream.

The power system begins with Canyon dam at the head of the lower Spray River.

the Three Sisters plant at the mouth of the Spray Reservoir. the smallest in the

system, with a generating capacity of 3MW (Figure 4). From there the Three

Sisters Tailrace carries flow into Goat Pond and a dike at the mouth of Goat

Pond guides the flow into Goat Valley canal. Water then flows through the canal

into Whitman's Pond and down through a pressure tunnel to the Spray Power


Plant, the largest on the system, with a generating capacity of 108MW. The

head of 274 meters at this plant is the highest of all TAU'S plants. From there

water flows down the Rundle canal to the Rundle Power plant (capacity 50 MW)

and into the Bow River at Canmore.

Figure 4: Trans Alta's Spray River power generation system From Calgary Power Ltd. circa 1950

P m


HISTORICAL CONDITIONS

Watershed

Information on historical conditions in Goat Creek was drawn from aerial

photographs, Parks Canada and Alberta provincial stocking records, previous

studies, maps, and Environmental Canada flow records. Two topographic maps

(Department of the Interior 1926; Canada Department of Mines 1923) covering

the Spray Lakes area show historical watershed divisions between the

headwaters of Goat Creek and the Spray River (Figure 5). Using these maps,

the Goat Creek historical watershed was outlined on current topographic maps

(Natural Resources Canada 1996). The area of the historic watershed was

calculated by counting one km2 map grid squares. The historic Goat Creek

watershed was approximately 70 km2. Environment Canada (1 990a) now

measures the watershed as 40.9 km2.

Many small tributaries flowing off the slopes of the Three Sisters and Mount

Lawrence De Grassi into Goat Creek are visible on aerial photographs taken in

1948. Goat Creek no longer receives water input from these tributaries, because

the Goat Valley canal now diverts the flow into the power generation system.

These photographs also show a small pond, roughly the size of the current Goat

Pond, at the headwaters of the stream, the outline of which is visible on recent

(1988) air photos lying immediately west of the current Goat Pond (Figure 5).


While the stream is still partially fed by waters from the new pond, through

seepage or water release through pipes, the Goat Valley Dyke has fragmented

the aquatic habitat, making the new pond inaccessible to fish from the creek.

The shape of the stream channel has changed little in the 47 years since flows

were reduced but it is apparent from comparison between pre- and post-dam air

photos that flows were greater and filled more of the channel. On the 1948

photos, areas of exposed gravel in the riparian areas are minimal and vegetated

areas are adjacent to the stream. Recent photos show that gravel and cobble

banks are now common and vegetation is sparse on exposed areas. While this

difference may be due to the time of year in which the photographs were taken

(which is unknown for the 1948 set and September 13 for the 1988 set) flows

have been reduced since regulation and have likely played a part in the changes

to the riparian areas.

Flows

In 1980, TAU provided a letter of commitment to BNP indicating that they would

allow a minimum flow of 0.283 m3/s (10 cfs) past the lower pump. Also, under

normal operations they would not allow flows greater than 30 cfs (0.849 m3/s).

Flows greater than 0.849 m3/s (30 cfs) could result from either natura! flow events

caused by high inflow from storm or snowmelt, or from management actions

requiring flow releases from the Spray Reservoir, Goat Pond, or the Goat Valley

Canal, or a planned or forced outage of the lower pump.

Environment Canada has no discharge information for Goat Creek prior to power

development. Since the impoundment, TAU has provided discharge data to

Environment Canada (1 990a). measured at their lower pumping station roughly

halfway down the stream (Figure 1). To estimate historical discharges for Goat

Creek. Golder Associates (1996) extrapolated from data for the Spray River

watershed. Environment Canada records for the Spray River begin in 191 5 and

are available for three locations: at the town of Banff, at Spray Canyon and on


Spray Creek. From these records, Golder Associates graphed minimum daily

discharge, and smallest and largest recorded annual floods against watershed

size from the three! sites (Appendix I: Determination of historical flows in Goat

Creek). From this graph they extrapolated flow information for Goat Creek.

However, they based their estimate of Goat Creek flows using a watershed of

40.9km2 for Goat Creek: its present size, post-dam. Before impoundment Goat

Creek's watershed covered roughly 70km2. Using this historical watershed size

and Golder's graph, the discharges associated with the largest and smallest

annual floods are nearly double Golder's estimate. with flows of 19m3/s and

3rn3/s respectively. Minimum daily discharge would have been 0.4m3/s. Post-

dam, from 1976 to 1990, the minimum daily discharge was 0.031 m3/s, although

this value is much lower than for all other years, with the next lowest at 0.1 7rn3/s.

The largest and smallest annual floods postdam were 4.03m3/s and 1 .32m3/s

respectively (Environment Canada 1990, data in Appendix ll: Historical flow

data). The changes are summarized in Table 4.

Table 4: Changes in hydrological regime in Goat Creek I Predam I Post-dam I Degree of

(km2) Largest recorded annual flood ( m h ) Smallest recorded annual flood (m31s) Minimum daily discharge (m31s) Mean annual discharge (m3/s)

Watershed area change (96) 41 -6

As Table 4 illustrates, changes in flow have been greater than changes in the

watershed size, with the greatest degree of change in the largest recorded

annual flood at 78.8 %. The other changes have been more related to the

degree of change in watershed size. ( Because the flow of 0.031 m3/s is so

much less than all other minimum daily discharges and likely influenced by ice

(estimated) 70 40.9


conditions (Environment Canada 1990a) I included the values for the next

smallest minimum daily discharge).

In addition to changes in the amount of water flowing down the stream, the

hydrograph is modified under managed flow conditions. To estimate the

historical hydrograph for Goat Creek the mean monthly discharges for the Spray

River at Banff for the years 191 1 to 1929 were calculated. These values were

then divided by 10.7 because the Spray River watershed, at 749 km2

(Environment Canada 1990a). is 10.7 times that of Goat Creek's historic

watershed (70 km2). This method for determining historic flows in the absence of

discharge records is generally accepted (Flosi and Reynolds 1991 ; FISRWG

1998). The calculation may not result in exact discharge amounts, but it does

provide a clear picture of changes to the timing and relative magnitude of flows.

The result is shown in Figure 6 below. The shape of the hydrograph has

changed radically since flow regulation and peak flows that once occurred in

June now occur in August.

Figure 6: Changes to Goat Creek hydrograph following flow regulation

5

4.5

4

3.5 35 € 3 Q)

P 2.5 c6 r 0 2 m

1.5

- - - Current Coat Creek mean monthly flows (1 976-1 990)

- Estimated historical mean monthly flows for Goat Creek

1

0e5 0 e


Fish and Habitat

Parks Canada stocked large numbers (up to 20,000 a year) of cutthroat trout and

rainbow trout into Goat Creek from 1931 to 1 947, every year except 1 938 and

1943 (Pacas, pers. comm.). In June of 1969 Alberta Fish and Wildlife stocked

14,000 brook trout fry into Goat Pond. Then, from 1973 to 1976, they stocked

85.000 rainbow trout (Oncohynchus mykiss). another non-native species. also

into Goat Pond. Before construction of the power generation structures, in 1944.

Alberta Fish and Wildlife stocked rainbow bout into the Spray Lakes. Beginning

in 1953 and continuing until 1987, lake trout (Salvelinus namaycush) were

stocked into the Spray Lakes Reservoir (Stelfox, pers. comm.).

Thompson and Weibe (1974) surveyed the fish community in Goat Creek in the

early 1970s and found a fish population of 94% artthroat trout. They also

describe the low numbers of pools in the stream, adding that the number of pools

decreases dramatically going down the stream, with few inside Banff National

Park boundaries. Miller and MacDonald (in Mudry and Green 1976) studied the

Spray River in 1945 and they also describe a cutthroat population in lower Goat

Creek and the lower Spray River typical of stream resident fish. They were small

and grew slowly. never reaching lengths greater than 250mm. Miller and

MacDonald state that this was a separate population from the one found in the

Spray River upstream of the 16 mile cabin, which was an extension of the fast

growing lake population. By 1992. the fish community had changed. All fish

caught in Goat Creek during a 1992 study by Courtney et al. were brook trout. a

result of provincial stocking in 1969 (Stetfox pers. comm.).


CURRENT HABITAT

The assessment of the current state of habitat in Goat Creek is based upon data

collected in the field in 1998 and 1999.

Representative Reaches

Data for this study was collected from stream reaches that represented broader

characteristics of Goat Creek. since 'classification of reach types and channel

geomorphic units enables investigators to extrapolate results to other areas with

similar featuresn (Bisson 8 Montgomery. 1996). Initial selection of the reaches

was done using topographic maps and air photos to break the stream into

sections based on channel gradient and degree of valley confinement (Newbury

and Gaboury 1993; Bisson and Montgomery 1996). Using this method three

sections were idenbified. Field visits confirmed preliminary divisions and

representative reaches chosen for every section measuring 12 times bankfbll

width were placed to include all habitat features (suggested in Newbury and

Gaboury 1 993).


Vegetation plot

Figure 7: Reach 1

Boulder vegetated ':-

Reach 1 (Figure 7) is 200m downstream of TAU'S upper pumphouse and

upstream of the lower pumphouse. outside of BNP. The slope of the 5.5 km long

stream segment represented in this reach is 0.8%. The slope of the reach, from

the thalweg survey, is 0.7%. This is the furthest upstream reach and would likely

provide much of the spawning habitat to stream resident fish. Inflow to this

section comes from seasonal tributaries flowing off the Goat Range and from

seepage through the Goat Valley Dyke and Goat Valley Canal. Two 1OOm

Hobo location

Rifflehapid -

4

Lw/ IOM 0 I 0-

Flow direct ion

Drawn from measurements taken 07/22/98

o - * d

Goat Creek Reach 1


reaches in this section are channelized with boulder riprap: one at the gravel pit.

the other at the upper pumping station. Historically this section was highly

sinuous. with mostly shrubby riparian vegetation (likely Betula pumila and Salix

spp-) and some patches of dense forest. The relic-ed pond at the headwaters

appeared shallow and the stream immediately below the pond shows evidence of

seasonal flooding. The stream, when it began at the pond, would have been

roughly 1.2km longer. Now, in much of this stream segment. areas of bare or

minimally vegetated cobble separate riparian vegetation from the channel. Some

remnant forest remains on the west side in the upper third of the section.

Shrubby vegetation also remains in a marshy area in the lower quarter of the

section, just above the lower pump house. This area is represented as a marsh

on a 1926 map (Department of the Interior).

The second representative reach (Figure 8) lies just inside the boundary of BNP,

downstream of the pump house. This 1OOm long reach represents a stream

segment of approximately 3.5 km characterized by a slope of 0.5% and wide,

marshy flood plains with sedges and tall coniferous snags. The slope of the

thalweg in this reach is 0.4%. The section represented begins just upstream of

the lower pump house and extends for 3 km into BNP. A channelized section

and a small impoundment created by a weir, both at the pump house, have

altered the original channel. At this pump house. Trans Alta pumps water from

Goat Creek into the Goat Valley Canal to compensate for losses to seepage. As

a result, flows in this section are often slightly lower than in the section upstream.

A tributary stream noted on a 1926 map (Department of the Interior) that flowed

off the end of Mount Rundle is now dammed at the lower pump house.

The pond created by that dam now supports brook trout. Once inside BNP. the

stream channel and vegetation remain similar to historic conditions, except that.

as in the first section, bare, cobbled areas now separate historic riparian

vegetation from the stream channel.


Figure 8: Reach 2

1 1 Vegetation Hobo Log) Flow / 1 Goat Creek Reach 2 1

The third representative reech (Figure 9) lies 5 km down the Goat Creek trail

from the trailhead parking lot. This section of the stream is within BNP and runs

approximately 6 km to Goat Creek's influence on the Spray River. The stream

segment has a slope of 2.6% and the lOOm long representative reach has an

overall slope of 3.8%, reflecting two small chutes. Without these chutes the

thalweg slope is 2.5%. Steep valley walls of either alluvial deposits or bedrock

I plot

1 Non- :. -.. I vegetated :.'. I 07/29/98

I I I

location

slope

/ Boulder D

direction

Rifflelrapid A

IOW - b I On\ ~rawnfiorn measurements taken


confine much of the stream valley. although in some places the flood plain is

200m to 300m wide. This section remains closest to its historic state, with no

structures affecting the channel directly. Both before and after impoundment,

parts of this section have bare cobble banks. up to 4m wide, flanking the stream.

About 1 km upstream of the influence with the Spray River, Goat Creek Trail

crosses the Creek at a bridge. Immediately upstream of the bridge is a waterfall

in a confined bedrock area with a height of roughly five metres.

Figure 9: Reach 3

\ -- Vegetation i Hobo x i Log plot j location ; -

Flow / I / Goat Creek Reach 3 direction 1 4

! I Non- . '. .:: . i Slope 1 Boulder i Riffletrapid I 1Qn~ (2 ICr.1

Drawn from

vegetated -' :; , measurements taken ! 1 07/22/98 I


Data Collection

Data collected in the 1998 and 1999 field seasons describes:

Water velocity and discharge

Water temperature

Substrate

Riparian vegetation

Fish population

Conductivity

pH

Suspended sediment

Water velocity, discharge and temperature were also measured on Healy Creek

for comparison to an unregulated stream. Healy Creek flows into Brewster Creek

three kilometers south of the Trans Canada Highway, eight km west of the town

of Banff. Brewster Creek then flows into the Bow River four km further east.

Healy Creek watershed. at 56km2 is slightly larger than Goat Creek. it is a

second order stream and has the same orientation and channel size, with a width

of 5m. The two drainages are only about 20km apart. Healy Creek was chosen

as a comparison based on its orientation, similar size and proximw to Goat

Creek. Also, Environment Canada has historical streamffow data for Brewster

Creek, which was used as the comparison stream for the Spray River in the

companion study to this one. The road to Sunshine Village provides easy access

to both Healy and Brewster Creeks.

In each reach on Goat Creek, three transects were placed to represent the

variety of pools. riffles, or other habitat characteristics, as well as where the best

evidence existed for bankfull width (Newbury & Gaboury, 1993). In all reaches,

and on Healy Creek, one transed crosses a straight section in which the l o w

appears uniform and parallel to stream banks so that discharge measurements

will be representative (Gore, 1 996).


Discharge

Methods

Stream discharge was calculated from measurement of flow velocity and area.

Velocity, depth and wetted width were measured on each transect in each reach.

Wetted width was measured using surveyors tape stretched across the stream

perpendicular to flow. Each transect was divided into at least five cells, only

creating more than five cells if. at five cells, each cell would exceed 3 metres (m)

in width (Newbury 8 Gaboury 1993; Gore 1996).

Depth and velocity measurements were made at the centre of each cell using a

guriey meter provided by TAU and calibrated by Environment Canada.

Measurements of velocity were taken at 0.4 of the depth (Harrelson et al., 1994;

Gore, 1996) and took 30 seconds each. Results were recorded in the field then

entered into Microsoft Excel for calculation and presentation. To calculate

discharge measurements taken at the straight section of the channel were used.

Discharge was calculated for each cell by multiplying the depth at midpoint by the

width of the cell by the veloclty in metes per second (mls). Total discharge is

the sum of the discharge of each cell.

Results

Figures 10 and I 1 illustrate the summer hydrographs for Goat Creek and Healy

Creek in 1999 and 1998. Environment Canada (1 990a) discharge data for Goat

Creek suggest that the overall decline in discharge over the summer of 1998 is

not usual (see Figure 6). The mean monthly discharge from 1976 to 1990,

measured just upstream of the BNP boundary. shows the discharge increasing to

a peak in August. Work on the power canal in September 1998 caused the

increase at sites 2 and 3, both downstream of the pumping station used to

redirect water from Goat Valley Canal into Goat Creek. Except for that instance,

discharge in reach 2 was lower than in reach 1 due to pumping activity between

reaches at the lower pumphouse.


Discharge peaks occurred later in the season in 1999 (late July and early

August) than in 1998 (June). Cooler spring and summer temperatures in 1999

delayed snowmelt in 1999, leaving the mountain snow pack above average for

June (Alberta Environment 1999a). Flow amounts in reaches 1 and 2 are similar

in 1 999 and 1 998, with peak discharges of 1 .I m31s and 1 -2 m3/s. respectively.

In both seasons, flows in reaches 2 and 3 in the late summer were lower than in

reach 1 , due to TAU pumping activities.

Figure 10: Goat Creek hydrograph, summer 1998 1

Reach Reach Reach Healy

Date

Figure 1 1 : Goat Creek hydrograph, summer 1999


Temperature

Methods

Therrnister dataloggers (Hobo) were installed in each reach to record daily and

seasonal variations in water temperature. The dataloggers were located at the

upstream end of each reach to prevent any disturbance from data collection

activities. To the extent possible, they were placed in the stream so that direct

warming from the sun did not influence temperature readings. Before installing

them in the stream, the dataloggers were wrapped in 0.5 cm foam and slipped

into solid plastic tubing. open on both ends to allow flow through. Wires were

attached to the plastic tube and to solid bank vegetation. Boulders were placed

over and around the tubes to prevent movement during high flows. The boulders

also provided shade. The dataloggers were set to record water temperature

every 72 minutes. Data was down loaded in October of 1998, when the batteries

were replaced. and were reset to record throughout the winter. Winter data from

reaches 1 and 2 was downloaded in July 1999, providing one hrll year of

temperature data for those two sites. The datalogger from reach 3 and from

Healy Creek were lost over the winter or in high spring fiows.

Results

In all reaches the normal range for maximum summer temperatures is between

10°C and 16°C (Figures 12-1 4). In reach 3 water temperatures rose above 16OC

for six days in the summer of 1998. The maximum temperature in reach 1 was

approximately 1 1 OC and in reach 2 it was 13OC. Temperatures in reach 1 were

lower overall, possibly resulting from a cold spring inflow. Also overhanging

banks and riparian vegetation shaded the Hobo at this site for much of the day.

Summer (June to September) minimum daily temperatures fall between 8°C and

2°C in reach 2 and between 10°C and 2°C in reach 1. Healy Creek daily summer

temperatures are more constant than Goat Creek with maximums and minimums

mostly between 5°C and 8°C. Riparian vegetation provides constant shade to

much of the stream throughout the day resulting in the small daily differences in

maximum and minimum temperatures.


Reach1

14

- 12

E 10

5 8 c.

fi 6

2 4

2

0 a O a o a o a o a o a o o , b , o , o , m Q ) ~

o , m Q ) Q ) $ 8 8 8 8 8 8 8 8 o , m a o P F F P

\ \ T F F F

4 - ~ z e a S S ~ ~ ~ s r e k F F F ~ - T r T F F

r r

Date

Figure 12: Reach 1 maximum and minimum temperatures 1 998-1 999

Reach 2 98/99

Date b

Figure 13: Reach 2 maximum and minimum temperatures 1998-1 999


I J u l y 1 t o S e p t e m b e r 3 0 , 1 9 9 8

Figure 14: Reach 3 maximum and minimum temperatures with comparison to Healy Creek

Winter temperature data is only available far reaches 1 and 2. Differences

between daily maximum and minimum temperatures in the winter months

(October to March) were less than in summer. Temperatures fell to -0.2OC in

reach 2 and to 1 OC in reach 1. During winter field visits in January open water

was observed at reach 1. Deep snowdrifts covered much of the channel at reach

2, including the hobo site. Temperatures of 8°C to 10°C that cutthroat trout need

for spawn and embryo incubation (Hickman and Raleigh 1982; Trotter 1987;

Mclntyre and Rieman 1995) and had occurred by July (when dataloggers were

installed) in 1 998 and in May (reach 2) and June (reach I ) in 1 999. Alberta

Environment (1 999a) records indicate that temperatures were below average in

May of 1999, resulting in delayed snow melt.


Survey

Methods

With the help of Paul Godman of TAU and equipment provided by TAU, each

reach was surveyed to provide cross-sectional and longitudinal profiles. All

transects and upper and lower boundaries of the reaches were surveyed, noting

the water surface level, bankfull stage, and terrace elevations (Hanelson et al.,

1994). Data were analyzed using Hec-Ras software (U.S. Army Corp of

Engineers).

Results

As survey data was only collected on five transects per reach, additional

transects were interpolated by Hec-Ras. For this reason scenarios represented

here are general and only serve to graphically illustrate the form of the reaches

and the relative changes in wetted width with various discharges (Figures 15-1 7).


The graduated shaded areas represent water levels at different discharges

(defined in the legend), however, they do not necessarily denote the stream

channel. The shaded areas show water level. which may be lower than ground

level. Channel locations and water levels are indicated in heavy black lines. In

all drawings water flows from bottom to top with a vertical exaggeration of ten.

Water level profiles:

0.66 m3/s

1.1 9 m3/s

3.0 m3/s

rn H

water surface /\r

Figure 15: Goat Creek reach 1



Water level profiles:

0.61 7 m3/s

1.19 m3/s

3.0 m3/s

Water surface

H (L,

Flow direction


Water levei profiles:

1.22 m3/s

3.0 m3/s

5.0 m3/s lIlsl Water surface &


Substrate

Methods

Streambed material composition was characterized using the Wolrnan Pebble

Count method on all transects in each reach (as described in Harrelson et al.,

1994). For each transect 100 randomly grabbed partides were measured on

each axis (x-y-2). These measurements were averaged for each particle.

Results

Table 5 Substrate size categories (Culpin 1986)

Reaches 1 and 2 have higher percentages of finer particles (c76mm) than reach

3 (Figure 18). This change from finer to more coarse substrate is to be expected

(Brookes and Sear 1996). The e2mm category generally describes the substrate

in pools which ranges from silt to sand, depending on water velocity (Table 5).

The fine gravel (2-25mm) category describes the size of spawning gravels for

trout in the stream. Fine and coarse gravels (25-75mm) are the dominant

substrate in all reaches, however, in reach 3, these particles are dispersed

throughout the substrate and do not afford good spawning areas. Small rubble

(77-1 52mm) and larger particles (1 53-305mm) could provide hiding wver and

resting areas for juveniles and adults. Partides of this size class are rare to

absent in Reaches 1 and 2.

Particle size < 2mm 2 - 25mm 26-76 rnrn 77-1 52 mm 153-305 mm > 305 mm

Category Sand. silt

- -

Fine gravel Coarse gravel Small rubble Large rubble Boulder .

CKAPTER 4 GOAT CREEK

Reach 1 Reach 2 Reach 3

Figure 1 8: Goat Creek percent substrate compositii by reach

Fish population

Methods

With the assistance of Charlie Pacas and Elaine O'Neil from Parks Canada, and

use of Smith-Root backpack electrofishing equipment from Parks Canada each

reach was electrofished to determine species presence and size classes. All fish

were identified, weighed and fork length measured (Table 6).

Results

Table 6: Results of elecbofishing activities

Total fish (#)

I Average fork length (mm) Effort

Reach 1 38

62.5

( s ) Catch per unit

2076

Reach 2 38

79.4

0.018 I I effort (#/s)

2376

I

Reach 3 21

94 -9

0.016

Total 97

78.9

1605 6057

0.013 0.016


With the exception of one Rocky Mountain whitefish (Pmsopium williamson~

130mm long found in reach 3, all fish captured were brook trout and perhaps

Lake trout (Pacas pers. comm.). Field identification did not differentiate between

brook and lake trout, however neither is native to the Creek. Sizes of fish caught

are represented in Figure 19. The dominant size class. comprising roughly half

the fish caught, was < 55mm in reaches 7 and 2. Medium sized fish (55-90 and

90-1 20mm) found in all reaches was the next largest group, with only one or two

large fish (120-250mm) found in reaches 1 and 3.

Reach 1 Reach 2 Reach 3

Figure 19: Percent composition by size category (fork length) of Goat Creek brook trout population

lnstream Cover

Methods

Along each transect in an area of 2 m long by the width of the stream. with the

transect bisecting the area, percent cover of both instream and ex-stream cover

types were recorded. lnstream cover included instream vegetation. boulders,

large woody debris (LWD). and small woody debris (SWD). Ex-stream cover

included bank overhang and riparian vegetation.


Results

I Undercut Banks lnstream Vegetation

25 0

20 0 L Q) > 0 U u C 150 Q 0, a9 Q

g 100

I 4) r

5 0

0 0 1 2 3

Roach

Figure 20: Percent instream cover by reach

Figure 20 illustrates that, with the exception of boulders in reach 3, there is very

little instream cover in Goat Creek. Other types of instream cover provide less

than 5% cover as for fish.

Riparian Vegetation

Methods

The riparian vegetation community of each reach was characterized by

identifying all species present in each level (herbs, shrubs, tall shrubs, and

trees). Ten estimates were made of: percent cover of each species, total canopy

cover, and soil moisture and drainage. Alberta Vegetation Index (AVI) and Banff

National Park ecological land classification maps and information provided

preliminary community type identification. Detailed surveys of the riparian

vegetation community were conducted on both sides of the stream at all

transects. The size of the detailed study areas depended on the size of the


vegetation community: 10 m by 10 m for forested areas, and 1 m by 2 m for

shrub and forb communities.

Results

Figures 21 and 22 illustrate the shrub and herb species present. Tree results are

not illustrated since the two species found (Engelman spruce and lodgepole pine)

occurred only in two sites.

R ipar ian s h r u b s

Ye l low m ounta in -avens

T w i n f l o w e r

W illow

E n g e I m a n s p r u c e

B uffaloberry

Prickly r o s e

B a l s a m p o p l a r

S h r u b b y c inquefoi l

B e a r b e r r y

Corn m o n J u n i p e r

D w a r f birch

Trembl ing a s p e n

L o d g e p o l e p i n e

R e d raspberry

r -

- I 1 -

B 1 -

- e 1 I - I I 1 A v e . %

T - I

r e s e n c e

I f -

1 i - I

1 i i .(

0 2 0 4 0 6 0 8 0 100 1 2 0

P e r c e n t

Figure 21 : Shrub species on Goat Creek


S e d g e

F i r e w e e d

C o m m o n h o r s e t a i l

T h o m p s o n ' s p a i n t b r u s h

S t r e a m b a n k b u t t e r w e e d

P ink w i n t e r g r e e n

G r e e n - f l o w e r e d b o g - o r c h i d

D w a r f scouring r u s h

L e a f y a s t e r

Y a r r o w

C o m m o n d a n d e l i o n

Ye l low H e d y s a r u m

E l e p h a n t ' s h e a d l o u s e w o r t

E v e r g r e e n s a x i f r a g e

F r i n g e d G r a s s o f P a r n a s s u s

N o r t h e r n g o l d e n r o d

8 r o a d - l e a v e d wi l lowherb

0 I 0 2 0 3 0 4 0 5 0 6 0 7 0

p e r c e n t

I

Figure 22: Forb species on Goat Creek

The east side of Goat creek (west-facing slope of Mount Rundle) is classified as

Pine/Buffaloberry, while SprucelFir forests cover the east slope of Goat Range.

However. forest stands only make up riparian vegetation in a few areas. In 19

vegetation plots on Goat Creek only two were forested. Shrubs, usually willow

(Salix spp.) or small spruce (Picea englemannii), sedges (Carex spp.). or bare

cobbly areas with some mountain avens make up most of the riparian

environment. In most cases riparian vegetation provides little or no shade or

streamside cover.


Water characteristics

Methods

Water conductivity and pH were measured in the lab using samples collected

from the stream.

Results

Conductivity in Goat Creek ranges h m 0.262msIs to ,290msIs at room

temperature (21 OC). with most measurements tending toward the higher end of

the range. Healy Creek averages 0.254mds. pH values ranged from 7.78 to

8.34, with an average of 8.0. Healy Creek average is slightly lower at 7.93.

Benthic Invertebrates

Methods

To obtain a stratified random sample, five samples of benthic invertebrates were

collected along the transect representing riffle habitat in each reach. Using a

Surber sampler, samples were collected across the stream by disturbing the

substrate and rubbing large cobbles and boulders for one minute. The current

swept the invertebrates into a jar attached to the open, downstream end of the

Surber net. Invertebrates were then killed by addition of formaldehyde.

Results

Results of a comparison between benthic invertebrates collected in studies in

1973 and 1992 found that the benthic invertebrate population has remained

relatively stable, with similar numbers and species collected with similar methods

in two studies (Courtney et al. 1992). Samples cdlected in 1999 have not been

identified. These samples could provide base line information on the benthic

invertebrate communQ. If a restoration plan for Goat Creek involves using

chemical piscicides, the benthic invertebrate populations may be harmed.

Information on the current community composition could provide information for

reintroduction of benthic invertebrates.


HABITAT SUITABILITY FOR TARGET SPECIES

Cutthroat Trout

To assess the suitability of Goat Creek for the cutthroat trout I used the Habitat

Suitability Index (HSI) developed by Hickman and Raleigh (1982). This method

is widely used in the United States (Hunter 1991) and uses preference curves

developed for habitat features that affect suitability for the target species (see

Appendix 111: Habitat suitability curves). These habitat variables are presented in

Table 7, along with the data and corresponding indices for each study reach of

Goat Creek. The suitability indices are unitless numbers between 0 and 1. Data

collected in the field seasons provided a base for an assessment of the habitat in

Goat Creek.


The HSi then requires calculation to determine habitat suitability for each life

stage: adult, juvenile, fry, embryo, and other. Each life stage calculation requires

,

only some of the variables.

based on the size of substrate suitable for spawning.

I

Table 7: Goat Variable

V1

V2

V3 V4

V5

V6

V7

V8

V9

V10

V11

V12

V13 V14

V15 V16

No spawning

Creek Habitat Suitability Values Description

Ave. max. water temp - summer Ave max water temp - embryo Ave min DO Ave thalweg depth - low water period Ave velocity (cmfs) over spawning areas % cover - low water period Ave substrate size 0.3- 8cm in spawning areas % substrate size 10-40cm for winter and escape cover Dominant substrate in riffle run areas % pools in late growing season Ave % vegetation along bank for allochthonous input Ave % rooted veg and stable rocky cover on bank Ave pH Ave annual base flow as % of ave annual daily flow Pool class rating % fines in riffle run areas

was obselved in Goat

for cutthroat trout , Reach

10°C

9.2OC

- 50 cm

0.5

5 %

8

1.3 an

A

10 %

48 %

30 %

8 - C 4 % Creek.

1 HSI 0.98

1

- 1

1

0.5

1

0.1

1

0.3

0.8

0.9

1 1

0.3 1 The HSI

I

13°C

12.3" C - 3 4 m

0.5

10%

t

0

A

25%

110 %

70 %

8 63%

C 1%

values

Reach 2 HSI 1

1

- 1

1

0.7

1

0

t

0.4

0.8

0.9

1 1

0.3 1 assigned

I

13.2" C 13.4" C - 33 cm

-

10 %

t

25cm

B

10 %

97 %

50 %

8 -

C 10%

are

Reach 3 HSI 1

1

- 1

1

0.7

- 1

0.6

0.3

0.8

0.9

1 1

0.3 0.9


Adult (CA)

The calculation for this component uses variables V4, V6, V10, and V15

(average thalweg depth, percent cover during low water period, percent pools in

late growing season, and pool class rating). To calculate the component score

for the adult life stage the following equation is used:

This equation is only used if V4 and 0110 x V1 5)IR are greater than 0.4. If this

test for use of the equation is not passed, the score for the adult component is

the value of the lowest variable in the equation for CA. None of the reaches in

Goat Creek pass the test for use of the equation so all reaches have a value of

0.3, the value for V15 (pool dass rating). This requirement that certain or all

variables exceed a defined threshold occurs in the calculation for each

component, based on the assumption that good quality habitat features can

compensate for some poor ones, but not when too many features are poor, or

one feature is very poor. The limiting element for adult trout is pools: the percent

of pool cover and the quality of the pools are both low.

Juvenile (CJ)

The juvenile component uses variables V6, V1 0, and V15 (percent cover during

low water period, percent pods in late growing season, and pool class rating).

Here the calculation instructions state that if any variable is less than or equal to

0.4, then the component value is the lowest variable score. Therefore the

juvenile component score is the same as the adult score and for the same

reason: poor pool habitat.

Fly (CF) Variables V8, V10. and V16 (percent of substrate size 1040 cm for winter and

escape cover, percent pools in late growing season, and percent fines in riffle run

areas) are used to calculate values for fry. Once again the values are for the


lowest variable, which in this case varies among the reaches. Reaches 1 and 2

have very low values of 0.1 and 0, respectively. based on the value for V8 (%

substrate 1040cm for winter cover). Reach 3 has a value of 0.3 based on the

low value for V10 (% pools).

Embryo (CE)

No spawning was observed in Goat creek during the field seasons. Values for

velocity and substrate size in spawning areas are assigned based on data

collected for sites in which trout of the size found in Goat Creek could spawn.

The calculation for this life stage indudes a rating of dissolved oxygen 013).

Data collected in the 1999 field season found DO levels of 13 mg/L. which

returns a value of 1 for this element. All other variables (V2, V5, '17. and V16:

average maximum water temperature during embryo development, average

velocity over spawning areas. average substrate size in spawning areas. and

percent fines in riffle run areas) used in the calculation for this component have a

value of one for reaches 1 and 2. Reach 3 has no potential spawning sites ('an

area > 0.5 m2 of gravel 0.3-8.0 cm in size covered by flowing water 15cm deep"

(Hickman and Raleigh 1982)) so it receives a value of 0.

Other (CO)

This component returns a value for water quality and food supply which affect all

life stages. The water quality subcomponent includes maximum temperature

(V1 ), DO 013). pH (V13). and base flow (V14). The food subcomponent covers

substrate size (V9). percent vegetation for allochthonous input (V1 1 ), and

percent fines in riffle run areas 0116). Those relating to substrate are included

because abundance of benthic invertebrates is correlated with substrate type.

Variables for percent streamside vegetation (V12) and the relationship of

average daily flow to average annual base flow are also included as important

habitat maintenance features. The equation for this component is:


Component = [[0/9 x ~ 1 6 ) ' ~ + V I I]'~] x [(Vl x V3 x V12 x V13 x V14 x 1IN 112

V16) I

Where N = the number of variables within the parentheses

The values for the overall habitat component are 0.89 for reaches 1 and 2. and

0.76 for reach 3.

An overall value for the stream can be calculated for each life stage separately.

or using any combination of life stages. This value is calculated using the

equation:

HSI = (CAx CJ x CFxCE X C O ) ' ~

But if any value is < or = 0.4, then the result is the lowest value. Therefore the

overall HSI for each reach matches the values for each life stage. Table 8

presents the results for habitat suitability for cutthroat trout.

Table 8: Habitat suitability results for cutthroat trout IReach IReach IReach 1

Adult Component Juvenile Component Fry Component Embryo Component Other Component

" Since cutthroat trout and bull trout would spawn in the upper reaches of Goat Creek. where suitable substrate exists, the value of 0 for the embryo stage is removed from the assessment of over habitat suitability for reach 3.

1 0.3 0.3

Overall HSI

0.1 1

0.89

2 13

0.3

0.3 ' 0.3

0 7

0.89

0.3 0.3

0.3 0'

0.76

0.3 0.3


Bull Trout

To assess habitat for bull trout in Goat Creek I used preference curves

developed by Femet and Bjomson (1 997). This method does not include a full

suitability index, and provides values for a smaller number of habitat features, but

it provides a general picture of the suitability for bull trout. The preference curves

are presented in Appendix Ill (Habitat Suitability Curves). Data collected in the

field seasons are used in the assessment of bull trout habitat.

Table 9: Habitat suitability results for bull trout

Because of the range of velocities and depths along and across the stream, all

reaches provide some habitat for each life stage. except Reach 3, which has no

potential spawning sites for small fish due to many boulders. Cover values are

difficult to judge because the preference curves point to which type of cover bull

trout associate with, but not how much is required of each type. Goat Creek has

limited cover of all types in each reach so I assigned low to median values for

cover.

Variable

Depth (m) Velocity (m/s) Substrate for spawning (mm) Cover Fry Juvenile Adult Cover at Spawning sites

LIMITING FACTORS

Rating each habitat feature allows identification of those features that limit habitat

suitability; those with low value scores (less than or equal to 0.4). Many habitat

features in Goat Creek rate as good to excellent and thus are not identified as

0.6 0.8 0.5 0.2

Reach 1

0.1-1.0 O.f-0.6 26-76

0.8 0.5 0.6 0.2

Index 1 1 1

Reach 2

- 0.5 0.6 -

0.1-1.0 0.1-0.7 26-7

Reach 3 Index 1 1 1

0.1-1.0 0.1-1.2 26-7

Index 1 1 -


limiting suitability. Temperature, thalweg depth, water velocity, % cover,

substrate in riffle run areas for food production, bank vegetation, and pH all are

suitable for cutthroat trout. The rating for base flows is also high since flows are

relatively constant throughout the year. Those elements that l iml suitability for

cutthroat trout are: substrate 104Ocm for winter escape cover and pools, percent

pool cover and pool class rating. The ideal percentage of pools for cutthroat trout

habitat is 50%. None of the study reaches in Goat Creek approach that amount.

lnstream cover in the form of pools, especially those created by large woody

debris (LWD), and undercut banks may be a limiting factor for both bull trout and

cutthroat trout. Also, since no spawning was observed, cover for spawning sites

is based on an assessment of potential spawning sites based on substrate size.

Temperature is not included in the preference data for bull trout, but other

sources (Pratt 1985; Shepard 1985; McPhail and Baxter 1996; USFWS 1998)

point to temperatures under 12OC as favoured, and find that bull trout may avoid

water with suitable habitat but warmer waters. Summer daytime maximum

temperatures in Goat Creek often exceed this threshold, limiting habitat suitability

for bull trout.

It is important to note, however, that the suitability values for Goat Creek do not

mean that cutthroat trout cannot be suppolted by available habitat. When Mudry

and Green (1974) conducted their study of Goat Creek in the 19709, the dam

had been in place for twenty years. Changes to habitat and flows would have

already altered the stream from its original state. Therefore, it is likely that when

Mudry and Green found a population of cutthroat trout, the habitat was very close

to what exists today. So, while habitat is not optimum it can support a cutthroat

trout community, but will limit numbers and size of fish.

The methods of habitat assessment used for both species only take into account

physical habitat. They can not be used to predict standing crop of fish since

other factors may also affect the success of a stream population. In Goat Creek,


the major limiting factor on reestablishing populations of bull and cutthroat trout is

the presence

GOAT CREEK RESTORATION POTENTIAL

Restoration of Goat Creek focuses on the length of stream from Goat Pond to

just above the bridge on Goat Creek Trail. The waterfall there limits upstream

movement of brook trout from the Spray River and the Bow River. The last

kilometer of Goat Creek, from the bridge to the Spray River is excluded from the

restoration to take advantage of the natural barrier to fish movement. If this

lower section were included, a bamer at the Spray River would be required,

unless non-native species in that River were also extirpated.

Removal of non-native species

Since BNP did not stock brwk trout into Goat Creek (Pacas pen. comm.), the

population of brook trout originated from the stocks introduced into Goat Pond in

1969 by provincial fisheries managen (Stelfox pen. comm.), or migrated through

spillway channels from the Spray lakes Resewoir. Restoration of a population of

native fish would involve removal of non-native fish and creation of barriers to

access from up and downstream sources of non-native fish.

Goat Creek presents a possibilw for native species reintroduction because it

could be made into a closed system. Investigation of the potential to restore a

native fish population in Goat Creek focuses on the length of stream from Goat

Pond to just above the bridge on Goat Creek Trail. The waterfall at the bridge

limits upstream movement of brook trout from the Spray River and the Bow River

(Courtney et al. 1992). The last kilometer of Goat Creek, from the bridge to the

Spray River could be excluded from the stream restoration to tske advantage of

the natural bamer to fish movement provided by the waterfall. If this lower

section were included, a barrier at the Spray River would be required, unless

non-native species in that River were also extirpated. Studies to determine the


effectiveness of the waterfall as a barrier to upstream movement would be

necessary. Higher flows and water velocity and lower summer water

temperatures as a result of moddying water flow releases in Goat Creek could

favour cutthroat trout over brook trout (Griffiths 1972; Behnke 1992; De Staso

and Rahel 1994). However, a population of only two brook trout can reproduce

quickly enough to replace a flourishing population of cutthroat trout in five years

(Behnke 1992).

For this reason, access to the Creek from upstream sources, in Goat Pond and

the small impoundment at the lower pumping station must also be blocked. In

the summer of 1998, anglers identified b m k trout in the small impoundment

pond. Coarse screens block trash and debris between the Spray Reservoir and

the Three Sisters power plant, but do not impede fish passage. The are no

screens or barriers to fish passage from Goat Pond through the culverts (Drury

pers. comm.).

A native cutthroat trout population exists in Marvel Lake and could be used for

stocking (Earle 1995).

Flow Modification

Restoring Goat Creek and environs would involve not only the fish community, it

would require recreating natural or naturalistic conditions in the habitat and

watershed to meet the goals of the BNP Management Plan. The main factor

affecting the stream habitat is the stabilization of flows from impoundment.

Recreating a more natural hydrograph would mean higher flows than currently

during the historic high flow period, from May to August.

Effects of higher flows on the instream habitat were examined in 1992, when

TAU diverted flows through Goat Creek to perform work on Whiteman's Dam

(Courtney et al. 1992). Flows increased fivefold above normals for the period,


from 0.5 m3/s to almost 3.0 m3/s. Depth increased, but not linearly with

discharge. The wide channel means that increases in discharge will result in

small increases in depth. The study found that the five-fold increase in discharge

resulted in only a 7 cm increase in depth in a study site immediately above the

lower pumping station, and an increase of 20 cm in a more confined channel

between reach 2 and reach 3. The site (Courtney et al. 1992) above the lower

pumping station was similar to reach 1. The stream channel is wide and shallow

with gently sloping banks so increases in flow create little change in depth.

During the study, Courtney et al. (1992) observed the movement of pea-sized

gravel and coarse sand at flows of approximately 2.83 m3/s. These particles

accumulated on the downstream side of instream velocity baniers such as log

and boulders. The study suggested that, since cobbles make up much of the

substrate in the stream, deposits of the smaller particles could provide suitable

spawning substrate. As higher flows raised the water surface elevation, fine

sediments from the shoreline were eroded and turbidity appeared higher,

resulting in milky waters. However, tests for suspended sediment showed no

change in levels of TSS between high and low flow periods. Another study

(Golder Associates 1 996) found that higher discharges (up to 5.42 m3/s) had not

resulted in deleteriously high levels of TSS. Even at the highest flows tested,

TSS levels were under h e 25mgR limit set by DFO. Both studies found that

sedimentation would not affect habitat in the stream because high gradient and

low numbers of pools allow few opportunities for water to slow and allow

sediment to settle out. Both studies concluded that there were no adverse

effects on fish from the increased water flows.

lnstream temperatures at higher flows would be lower for two reasons. First, the

hypolimnion water released from the reservoir would be cool. When Mudry and

Green (1 974) conducted their investigation on the fish in the Spray River, they

found that temperatures in the lower Spray River were depressed by cooler water

flowing in from Goat Creek. At that time oat Creek was used as a spillway for


augmenting flows in the lower Spray River, thus the water was cooler, at least in

part, due to its source in the reservoir. Secondly, higher Rows would also result

in faster moving, deeper water that would remain cooler than slower moving

water exposed to more solar radiation (Armitage 1984; Ward and Stanford 1985).

Goat Creek is now essentially removed from the River and Reservoir system

used in hydroelectric generation. Aside from occasional flow releases from Goat

Pond or Goat Valley Canal to allow repairs to various structures, the effects of

impoundment on Goat Creek result in stable flow; the daily and seasonal flow

fluctuations associated with run of the river power generation do not exist.

Comparing estimated historic flows to current fbws suggests that current low

flow discharges. from late August through to late April (eight months) are close to

historic flows (Figure 18). From November to April current flows are greater than

estimated historic flows. Therefore they would not need to be modified to restore

a more natural hydrograph. Current flows from May through August (four

months), the historic season of high flows, are substantially lower since

impoundment. Augmenting flows during these months would mimic the natural

hyd rograph.

To determine flow amounts and associated costs for recreating a natural

hydrograph in Goat Creek, two possible flow management scenarios were

examined. The first (scenario one) creates a hydrograph with peak flows from

May to August (the historic high flow period). The peak flow amount is within the

limits of what power generation structures allow, without modification. Capacrty

at the outlets from Goat Pond is 21 8 cfs (6.1 7 m3/s). Limits to flow increases

occur at the weir at the lower pump, where flows greater than 100 cfs (2.83 m3/s)

can subject the pump to flooding (Drury pers. comm.). Scenario one uses 2.83

m3/s (1 00cfs) as the peak flow for June and July.


Estimated historic peak flows occurred in June and July at approximately 4.5

m3/s (1 58.8 cfs). Scenario one involves no structural changes to the weir or flow

outlet capabilities at Goat Pond so lost revenue from diverted flows represents all

monetary cost to TAU.

0.0283 m3/s (1 cfs) of water flowing for one full day through the Spray and

Rundle power plants produces 2 megawatthoun (MWh) of energy (Drury pers.

comm.).

Costs (lost opportunity) are calculated using values of 1 cfs-day = 2MWh and

$40.00 per MWh, in the equation:

Cost = flow (cfs) x number of days x 2MWhIcfsday x $40.00 per MWh

Since TAU is required to release a 0.283 m3/s (10 cfs) baseflow, these ffows are

subtracted from the target flows before calarlation of revenue lost. Flow levels

and costs are shown in Table 10. Figure 23 shows the hydrographs from each

scenario.

In scenario two. flows during high flow season (May to August) are augmented to

their historic levels. To achieve these flows structural changes to the weir at the

lower pump house would be required. Costs for modifying the weir are not

included in the cost summary in Table 11. The hydragraphs for both scenarios

are represented in Figure 23.


Table 10 Cost for scenario one (no structural changes) Month

May June July August Totals

Table 11 Cost for scenario two (involving structural changes to weir) Month

May

June

July

August

Average flows 19761990 in m31s (cfs) 0.739 (26.1 ) 1 -02 (36) 1 . I4 (40.2) 1.34 (47.3) 4.23 (149.61

1.14 (40.2)

Totals

Figure 23: Hydrographs for scenarios one and two with comparison to current flows

Target flows in m31s (a) 1.42 (50) 2.83(100) 2.83 (1 00) 1.42 (50) 300 18.49)

Difference in m31s (cfs)

0.68 (23.9) 1.81 (64) 1.69 (59.8) 0.08 (2.7) 4.26 11 50.4)

Average flows 1976- 1990 in m31s (&)

0.739 (26.1)

1.02 (36)

1.34 (47.3)

5 h

m 2 4 € 3 a 2' 2 tu c 2 - 0 1

0 a 0 '3 4 co -.

A

This examination of restoration potential for Goat Creek does not consider

removal of the power generation system so the Goat creek watershed will remain

at 41 -6% of its historic size. Therefore, restoring flows to their historic levels may

not be appropriate. Flow releases possible within the existing structural

constraints (scenario one) allow peak flows of 60% of estimated historic peak

Cost in lost revenue($)

59.272 I 53,600 148,304 6,696 367.872

Target flows in m31s (a) 1 -66 (58.63) 4.43

Difference in m31s (cfs)

0.92 (32.53)

3.41 (1 56.48) 3.52

4.23 (149.6)

- - - -Scenario one flows

- - Historical mean monthly flows approxim ated by scenario two Current Goat Creek mean monthly flows

Cost in lost revenue())

80,674.40

289,152

(1 24.40) 1 -99

(1 20.48) 2.33 (84.2)

(70.46) 11 -60 (409.97)

208,816

1.99 (23.1 6) 57,436.80

7.37 (260.37)

636,079-20


flows. Because of the relationship between watershed size and discharge (Flosi

and Reynolds 1991 ; FISRWG 1998), flows amounts reflecting the new, reduced

watershed size may be appropriate.

The target flows in Tables 9 and 10 are averages for the months and could be

designed to be flexible. as in the concept of a water budget, as used by BCHydro

(BCHydro 1996). A water budget would allow BNP and TAU flexibility to modify

agreed-to flows for adaptive management. An annual amount could be set at

total amount of discharge for the year or four month high flow period (May to

August) or at an agreed-to monetary amount so that average annual cost to TAU

remains constant. For example, in scenario one, if an annual flow increase of

4.26 m3ls (1 50.4 d s ) over four months was agreed upon over a four year cycle,

fisheries managers could design peak releases to respond to yearly precipitation

variations (Wieringa and Morton 1996). In a year with high snowmelt and rainfall

amounts, full flow releases could be combined with higher natural inputs to

create flushing flows. Alternatively, a yearly cost to TAU, set at $367,872 (the

cost for increasing flows in scenario one), would allow similar flexibility, but flow

changes would be assessed on the value at the time the flows are released and

would allow more certainty for TAU. In either case, BNP could 'purchase' flows

by reducing flow requirements in low flow periods.

Removal of non-native fish would be aided by lower flows, so during the years in

which removal occurs, the agreement for the 0.283 m3/s (1 0 cfs) that TAU now

allows past the lower pumping station could be waived. If so, in one year TAU

would gain $292.000 by benefiting from the power generated by the 0.283 m3/s

(1 0 cfs) over 365 days.


lnstream Techniques

lnstream structures. used in combination with flow management would

accelerate channel change and create more diverse instream habitat with

increased pools and cover. The high flows released into Goat Creek during

failures of the Goat Valley Dyke likely caused changes in instream habitat,

washing LWD downstream and filling pools with sediment. These high flow

events could have acderated changes or caused changes in instream habitat

that would not otherwise have occurred.

l nstream restoration techniques for Goat Creek should be aimed at mitigating

limiting factors identified in the assessment of habitat suitability. These limiting

factors are: lack of and poor quality of pools. high maximum temperatures in the

summer for bull trout, little instream or streamside cover, and limited suitable

substrate for juvenile winter cover. High summer temperatures could be

addressed through high water floes in summer months. The instream techniques

reviewed in Table 3 are suitable for Goat Creek. Those techniques that address

limiting factors in Goat Creek are outlined in Table 12. All instream techniques

work in concert with flows to create and diversify instream habitat.

Physically. Goat Creek is a suitable candidate for instream structures to improve

habitat. Flows are managed. the overall stream gradient is within the ranges for

instream structures, and sediment sources are limited. While riparian sources of

LWD would need years to decades to naturally affect instream habitat. sources

for LWD exists all along the length of Goat Creek for use in a managed

Table 12: Limiting factors and restoration techniques Limiting factor High summer temperatures Low number and poor quality of pools Little instream or streamside cover

Little substrate for juvenile winter cover

Potential restoration tools Riparian planting Increase instream objects, large woody debris (LWD) and boulders Increase instream objects, large woody debris (LWD) and boulders Boulder placement


introduction of LWD. Because of the low amount of LWD in Goat Creek, high

discharges could simply scour and remove sediments and amour the channel,

rather than create more diverse habitat. lnstream structures would address this

factor.

Riparian areas

In the 50 years since flow regulation on Goat Creek, little riparian vegetation has

emerged. Many streamside areas are unvegetated cobble. some have growths

of mountain avens (Dryas dmmondii), and willow (Salix spp.) shrubs cover

other areas. In a few places there has been limited regrowth of spruce (Picea

englemannii), that. over decades, will develop into well-forested riparian areas.

The large areas of bare cobbly deposits, having remained unvegetated since

1950, show little sign of revegetation since no soil deposition takes, as it would

with periodic flooding with high flows. Flows suggested in the two scenarios

would not flood the banks and there is little sediment available for deposition.

Plantings of native willow species, or dwarf birch (Betula pumila) native to the

area could hurry reestablishment of the riparian community. Since BNP has a

large community of volunteers interested in working in the Park, a revegetation

program could be done relatively inexpensively..

CHAPTER 5

SU'MMARY AND RECOMMENDATIONS

SUMMARY

Cutthroat and bull trout were selected as target species for this investigation of

restoration potential because they are native to Alberta and their populations are

in decline there as well as over much of their historic ranges. They are also

vulnerable to human-induced habitat changes and competition from introduced

fish species. Restoration efforts in Canada and the United States are focussed

on re-establishing viable populations of these native species by managing two

types of effects: flow regulation and the presence of non-native species.

The two native trout have similar h a b i t needs. requiring cool. dear. flowing

water. in habitat that provides hiding cover, food, and opportunities for

reproduction. Flow regulation directly affects this habitat by creating barriers to

movement, by changing the nature of the aquatic habitat from flowing to still, and

by reducing flows and thereby reducing area of available habitat. Indirect effects

from lowered flows and lowered sediment levels lead to changes to instream

habitat, reducing habitat diversity. Lowered flows also affect water temperature.

which can make habitat unsuitable for some species and can interfere with

reproduction stimuli and food availability. Absence of flooding flows leads to

degradation of riparian habitats. as replenishing soils and nutrients are no longer

seasonally deposited on the stream banks.

Lower flows also affect interactions between native and non-native species.

Non-native trout species introduced into western North American waters over the

last century have decimated native populations in many cases. Non-native fish

compete with native species for temtory and resources. often more successfully

in an altered environment to which they are better adapted. They can also

CHAPTER 5 SUMMARY AND RECOMMENDATIONS

hybridize with native populations, reducing those species abillty to reproduce and

altering native genetic strains.

Stream restoration projects now adopt a broader-scale perspective than in the

past. Historically, restoration projects that focused solely on instream habitat

were unsuccessful. Projects now focus on watershed structure and functions

and address causes of habitat degradation rather than simply the effects. In

cases where streams are affected by flow regulation this means including fish

habitat needs as well as power generation requirements in flow management

decisions. Flow management for fish habitat can be either in the form of

minimum flows or as mimicking a natural hydrograph. Water budgets. in which

flow releases are set for a year, but timing of releases may be varied according

to habitat management needs, have been used with success in cases where

uncertainty of results would otherwise limit decision-making. Water budgets

allow for flexibility in habitat management while providing economic certainty for

the power generator.

Methods to remove unwanted fish species include poison, electmfishing, and

angling, all in use now in North America with varying success rates. Poisons

work well at removing fish populations, but affect all instream organisms and thus

require restocking of benthic invertebrates after treatment. Electrofishing does

not kill native fish or benthic invertebrates, but has limited potential to remove all

non-native fish. as does angling. Brook trout are especially difficult to remove by

any method other than poison, since it is difficult to remove all young of the year,

yet those fish will mature and reproduce in the next year.

Projects using instream structures for habitat restoration have low success rates,

unless used in combination with watershed management. Such structures can

be used with flow management, to accelerate habitat creation in degraded

streams. They should only be used, though, when an analysis of limiting factors

indicates that such structures would address habitat shortcomings.

CHAPTER 5: SUMMARY AND RECOMMENDATIONS

Both flow regulation and introduction of non-native fish species have affected

Goat Creek, in Banff National Park. The fish community changed after

introduction of brook trout. from one composed of native species to one

dominated by non-native fish. Impoundment structures and extreme flow events

changed instream habitat. reducing habitat area and instream diversity, and

thereby limiting its suitability for native fish.

Parks Canada's legal mandate to maintain ecological integrity in the National

Parks supports restoration of the fish community and habitat in Goat Creek.

Management of Goat Creek, however, falls not only to BNP, but to the Province

of Alberta, and to TransAlta Utilities. Each organization's management activities

have affected the fish communw and habitat in Goat Creek over the last 47

years.

Restoration of Goat Creek would involve removing non-native fish species,

stocking native cutthroat trout, managing flows for fish habitat, and creating

instream habitat. Structural constraints associated with power generation

facilities allow for augmentation opportunities to mimic natural flow patterns and

create water velocities high enough to move substrate and create instrearn

habitat. Current flow outlets, though. also allow fish passage from upstream

areas that support non-native fish populations. Successful eradication of non-

native species depends on such access point being closed. Upstream fish

movement from the Spray River and the Bow River is blocked by natural

structures. Goat Creek is a suitable candidate for instream structures for habitat

creation. The size, topography, and flow levels would not limit the choice of

types of structures. In table 1 3 the issues and restoration opportunities for Goat

Creek are summarized.

Table 13: Summary of issues, effects and restoration techniques

Issue

Impoundment

Dam failures

Stocking of non-native species

Effects on Goat Creek Reduced discharge

Stable annual discharge

Homogenous instream habitat

Fish community changed from a diverse native population to a population of brook trout

Potential Restoration Methods Increase minimum flow requirements lncrease flows in natural high flow season Increase flows in natural high flow season

Increase instream woody debris and increase flows in natural high flow season

Chemical poisoning

Electrofishing

' Bkdting re-entry of non- native fish

Restock native fish

Comments

Does not address BNP Management Plan objective to create more natural flows in the Spray River system. Within current structural framework, flows can be increased to 2.83 m3/s, or 60% of historic flows. Watershed area is reduced from historic size by 41 % so correspondingly reduced peak flows may be appropriate. A water budgets with a set annual amount for flow releases allows flexibility in flow management when effects of increased flows are not known. High flows released during dam failure likely washed instream debris downstream and filled pools in the 1970s. Materials for placement in stream are available along stream.

6 Increasing flows may not create diverse instream habitat, since little debris exists in the stream. Good record of success in eradicating non-native fish species. May kill benthic invertebrates, requiring reintroduction of aquatic insects. Currently not permitted for use in National Parks, but altowed by the Federal Fisheries Act.

Poor record of eradication of brook trout,

Potential natural barrier at waterfall one km upstream of Spray River. Fish can c u ~ t l y access Goat Creek from the Spray Lakes Reservoir and Goat Pond. Saesns to block access through culvert at Goat Pond would be needed for a successful restoration. Stocks of native cutthroat and bull trout exist in the Bow River watershed.


RECOMMENDATIONS

Management recommendations were developed to meet the goal of maintaining

and enhancing the structural and functional integrity of the Goat Creek

ecosystem, as determined by the laws, policies and management plan for Banff

national Park. If Parks Canada decides to restore Goat Creek as a means to

achieving its mandate for ecological integrity, the management recommendations

would provide a framework within which to guide restoration planning.

The recommendations are divided into two types: organizational and specific.

Organization recommendations refer to broad scale management activities that,

if not addressed, will limit the success of any restoration activities for Goat Creek.

These recommendations are based on an understanding of the current legal and

management framework governing this area, and on information derived from a

review of literature addressing stream restoration. Organizational

recommendations create the management framework within which specific

restoration activities take place. Specific recommendations focus on Goat Creek

and are drawn from analysis of current and past habitat conditions, from an

understanding of engineering opportunities and constraints associated with TAU

dam structures, and from analysis of research into restoration methods. These

recommendations propose actions needed to restore ecological integrity in Goat

Creek.

Organizational Recommendations

The first two organizational recommendations arise from a review of literature

and from discussions with fish habitat managers. The review of stream

restoration literature pointed to failures in restoration projects with narrow scopes

that emphasized habitat creation rather than watershed-scale planning. Current

wisdom suggests managing from a broader perspective that addresses causes of

degradation. The National Parks Act, Parks Policies, and the Banff National Park

Management Plan all support managing for ecological integrity.

CHAPTER 5 SUMMARY AM) RECOMMENDATIONS

Using the Parks Canada definition of ecological integrity would mean focussing

on restoring structures and functions that allow habitat and the communities it

supports to be self-sustaining. Therefore:

1. It is recommended that any restoration plans for Goat Creek focus on

restoring natural structure and functions by addressing the effects of

flow impoundment and the presence of non-native species-

Removal of fish from streams has met with resistance in other areas, no matter

what the method. but using piscicides to accomplish the task would generate

additional controversy. Goat Creek is not currently a destination for anglers. so

resistance to projects focussing on that stream may not be controversial, but if

plans for restoring streams in BNP are not made clear, resistance may arise from

misunderstanding of future plans. Other jurisdictions have successfully

communicated with the public and have won support from groups originally

opposed to restoration of native fish populations. Therefore:

2. It is recommended that Psrks Canada create a public infomation

program inform and include the publk in any plans to restore aquatic

ecosystems and to encourage support for such programs-

The third and fourth organizational recommendations are drawn from my

understanding of the current organizational and jurisdictional setting within which

Goat Creek sits. Past projects on Cascade Creek (McCleary 1996; Godman

1999) and a current project on the Spray River (Eaton in prep.) investigate the

restoration potential for those streams. Parks Canada has developed preliminary

restoration plans for Cascade Creek. A restoration of Cascade Creek provides

an excellent opportunity for public education, since Lake Minnewanka and the

creek are easily accessible to Park visitors and are already a destination for a

large percentage of Park visitors. Restoration potential for the Spray River is not


yet known. Goat Creek, although less accessible to the public than Cascade

Creek, is physically a good candidate for restoration and presents some

opportunities for interpretive programs at the Goat Creek Trailhead and at the

bridge on Goat Creek Trail. Therefore:

3. It is recommended that. in determining restoration pn'on'ty Goat Creek, it

be reviewed in context with other pmjects investigating restoration

potential on the Spray River and on Cascade Creek.

Since Goat Creek originates and runs almost half its length through the Province

of Alberta, actions by provincial fisheries managers and by public visitors to

provincial lands have the potential to affect any restoration plan for Goat Creek.

Past actions by provincial fisheries managers resulted in the current community

of brook trout in Goat Creek. Current provincial projects involving removal of

non-native species from provincial waters could help in any efforts by BNP. Also.

the Spray Lakes Reservoir, Goat Pond. Goat Creek Trailhead, and the most

accessible section of Goat Creek are on provincial land and provide interpretive

opportunities to inform the public of both restoration efforts and collaborative

projects. Therefore:

4. It is recommended that Parks Canada collaborate with provincial

fisheries managers on any restoration plan fbr Goat C m k .

Specific Recommendations

The following recommendations apply to Goat Creek and would be a guide to

restoring Goat Creek, if it were selected as a potential site for restoration.

The historical analysis of Goat Creek shows that, in its natural state, Goat Creek

supported a population of native cutthroat trout in a stream regulated by


snowmelt and rainfall. Analysis of historic flows illustrates that Goat Creek flows

peaked from May to August, like the majority of unregulated streams in BNP.

The information on its past state can guide the goal setting process for restoring

Goat Creek. My review of literature suggests that an understanding of past

biological capacity and historic habitat conditions provides a realistic framework

within which to plan restoration efforts. Therefore:

5. It is recommended that Parks Canada use the infbnnation in this report

on historic conditions in Goat Creek as a guidb in defining restontion

goals.

Based on knowledge of historical and present conditions of the habitat and the

fish community in Goat Creek, restoring natural structure and function would

require:

a) Reestablishing a population of native fish

Closing fish access through culverts at Goat Pond and lower pumping

station, and from pond above lower pumping station (l access exists)

Removing brooknake trout from Goat Creek

Stocking Goat Creek with cutthroat trout from stocks in Marvel Lake

b) Recreating a natural hydrograph

Increase flows in historic high flow season, from May to August

c) Encouraging instream habitat creation

Fish populations

Discussions with provincial fisheries managers indicated that the current

population of brook and lake trout in Goat Creek originated in the Spray Lakes

and Goat Pond, so fish in those water bodies have access to Goat Creek.

Populations of non-native fish still exist in Goat Pond and the Spray Lakes, so

success of restoration of native species in Goat Creek requires blocking that

access.


To prevent recolonization of brook and lake trout, structures to block fish

passage from Goat Pond would be needed prior to any removal process.

Therefore:

6. !f is recommended that Parks Canada work with liansAIta Utilities to

defermine feasibility of building stmctures to block fish passage-

Analysis of information from a literature review and from fisheries managers

revealed that, of the methods available to remove fish from streams, piscicide

appears the only choice to successfully eliminate fish in a stream such as Goat

Creek. Therefore:

7. It is recommended that Parks Canada investigate the possibility of

using piscicides in Banff Naffonal Park. This includes detetmining

potential effects on adjacent wafers and fish popula0ions-

FIo ws

Scenarios for flow alteration developed fmm an understanding of historical flow

patterns in Goat Creek combined with information on the costs and constraints

on flow augmentation from a hydroelectric generation view. show the costs and

results (in terms of recreating a natural hydrograph) for TransAlta and Goat

Creek. It is possible, under current structural constraints, to increase peak flows

to ten times the amount currently released as a minimum flow by TransAlta.

From a literature review of projects in other jurisdictions working on managing

Rows for fish habitat and power generation, uncertainty regarding results has

lead to use of water budgets that allow for adaptive management. Since the

effects of flow increases are not completely understood for Goat Creek. a water

budget would be a valuable tool for managing flow releases.


Water budgets provide both flexibility for Parks Canada fisheries managers and

certainty to TransAlta regarding costs. Therefore:

8. It is recommended that Parks Canada and TransAIta Utilities work

together to define a water budget and detemine desired flow amounts.

Under current structural constraints. it is possible to increase flows in Goat Creek

to approximately 60% of historic peak flow levels. Since the Goat Creek

watershed would remain at its present reduced size (41 % of historic size), and

because of the relationship between watershed size and discharge, discharges

lower than historic levels may be appropriate.

lnstream habitat management

Analysis of current instream habitat conditions and the forces that created them

illustrated that instream habitat diversity in Goat Creek is low. likely as a result of

extreme flow events that filled pools and removed woody debris. Assessment of

habitat suitability for native trout in Goat Creek pointed out that the low number

and poor quality of pools is a main limiting factor for habitat quality. Information

gained from the literature review tells that instream structures are best used in

concert with broad-scale watershed management that addresses causes of

ha bitat degradation. Such structures can accelerate instream ha bitat formation.

Taking this information in the context of the Goat Creek environment, this means

combining instream structures with flow management. In a natural state, Goat

Creek would have large woody debris from fallen riparian vegetation shaping and

creating instream habitat. Riparian areas now are either bare gravel or beginning

to regenerate with willow and small spruce. These plants will require decades to

mature and fall and play a rde in habitat creation. Mature vegetation does exist.

though, close enough to the stream all along the length, as a potential source for

managed placement. Flow augmentation will move substrate. but velocity

shadows are required for sediment to settle out of the current. and areas of

higher velocity are needed for scouring effects. Instream objects that would

CHAPTER 5: SUMMARY AND RJXOMMENDATIONS

direct flow and accomplish these tasks are limited to non-existent in Goat Creek.

Therefore:

9. It is recommended that Parks Canada include use of large woody debris

in the stream to work in concert with increased flows to accelerate

habitat formation.

REFERENCES

REFERENCES

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Culpin, Paul. 1089. Streams. lnventorv and Monitorina of Wildlife Habitat, Allen Y. Cooperrider, Raymond J. Boyd, and Hanson R. Stuart (eds.) United States Department of the Interior, Bureau of Land management.

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De Staso, James and Frank J. Rahel. 1994- Influence of water temperature on interactions between juvenile Colorado River cutthroat trout and brook trout in a laboratory stream. Transactions of the American Fisheries Society 123:289-297-

Earle, Jenny. 1995. A Po~ulation Studv of Westslow Cutthroat Trout (Oncortrvnchus clarki lewisi) in Marvel Lake. Banff National Park. With lm~lications for Manaaement. Masters Degree Project, Faculty of Environmental Design, University of Calgary.

Ebersole, J.L., Liss, W.J., & Frissell, C.A. 1997. Restoration of stream habitat in the western United States: Restoration as a reexpression of habitat capacity. Environmental Manaaement, 21.1, pp.-14.

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Fausch, Kurt D. 1988. Tests of competition between native and introduced salmonids in streams: what have we learned? Canadian Journal of Fisheries and Aauatic Sciences 45: 223892246.

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Godman, P.G. 1999. Fisherv Habitat Modelina of Cascade Creek. Banff National Park, An Abandoned Mountain Channel. MSc. Thesis, University of Calgary.

Golder Associates. 1996. Effects of Increased Levels of Turbiditv and Susmnded Sediments in Goat Creek Assodated with a S ~ i l l Event from Goat Pond durina the summer of 1995. Calgary, Alberta: TmnsAlta Utilities Corporation.

Gore, James A., Franklin L. Bryant, and Dina J. Crawford. 1995. River and stream restoration. Rehabilitatina Damaaed - Ecosvstems, John Cairns, Jr. ed. Boca Raton: Lewis Publishers.

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REFERENCES

Griff~th, J.S., Jr. 1972- Comparative behavior and habitat utilization of brook trout (Salvelinus fontinalis) and cutthroat trout (Salmo cIarkr] in small streams in northern Idaho. Journal of the Fisheries Resources Board Canada 29: 265-273.

Hamelson, C.C-, Rawlins, C.L., & Potyondy, J.P. 1994. Stream Channel Reference Sites: An Illustrated Guide to Field Techniaue. General Technical Report RM-245. Fort Collins, CO: U.S. Dept of Agriculture, Forest Service, Rocky Mountain Forest and Range Experiment Station.

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Henricson, Jan and Goran Sjoberg. 1984. Reaulated - Rivers, Albert Lillehammer and Svein Jakob Saltveit (eds.) New York: Columbia University Press.

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Kondolf, G. Mathias and Peter W. Downs. 1996. Catchment approach to planning channel restoration. River Channel Restoration: Guidina Princi~les for Sustainable Proiects, Andrew Brookes and F. Douglas Shields Jr. (eds.) Chichester: John Wiley and Sons.

Koning, C. Wendell and Pat A. Slaney. 1996. Techniques to assess and restore fish habitat in stream impacted by logging activities. Proceedinas of the Canadian Water Resources Association (CWRAI Conference. Watercourses. Gettina on Stream with Current Thinkina. October 22-25. Vancouver. B.C., pp. 181 -1 87.

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REFERENCES

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McCleary, R. 1996. lm~acts Of Water Diversion on Floodplain Structure. Hvdrolw~, and Rioarian Veaetation. - and Possible Mitiaation. Cascade River. Banff National Park. MSc Thesis, University of Montana.

Mclntyre, John D. and Bruce E, Rieman. 1995. Westslope cutthroat trout. Conservation Assessment for Inland Cutthroat Trout, Michael K. Young ed. USDA Forest Service General Technical Report RM-Gm-256.

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Meyer, Kevin. 1998. Native Salrnonids Assessment Summaw. Idaho Department of Fish and Game.

Ministry of Canadian Heritage. 1994. Parks Canada Guidina Princides and Omrational Policies.

Mudry, Dwight R. and Roderick B. Green. 1976. Fisheries lnvestiaations on the Smay River. Banff National Park. 1 975-1 976.

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Newbury, R.N. 8 Gaboury, M.N. 1993. Stream Analvsis and Fish Habitat Desian: a Field Manual. Winnipeg: Newbury Hydraulics Ltd., The Manitoba Habitat Heritage Corporation, Manitoba Fisheries Branch

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REFERENCES

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United States National Park Service. National Park Service Park Manaaement Policies.

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REFERENCES

Personal communications

Drury, Roger Water Management Planner TransAlta Utilities 1 1 0-1 zrn Ave SW, Calgary, Alberta

Homer, Ned Fisheries Biologist Idaho Fish and Game, 5750 Kathleen Ave., Coeur d'Alene, Idaho

Lutch, Jeff Aquatic biologist PO Box 168, Yellowstone National Park, Wyoming

Pacas. Charlie Aquatics Specialist, Banff Warden Service, PO Box 900, Banff National Park, Alberta

Paul, Andrew Ph.0. candidate Department of Biological Sciences, University of Calgary 2500 University Drive NW, Calgary, Alberta

Stelfox, Jim Alberta Environment 2938 1 1" St NE, Calgary, Alberta.

Maps

Canada Department of Mines. 1923. Palliser - Kananaskis Area: British Columbia and Alberta. Geological Survey 82J N.W. 1 :126.720, 1' = 2 miles. contour interval 200'.

Canada Department of the Interior. 1926. Banff and vicinity. Topographical Survey 82 014. 1 :63,360, 1" = 1 mile, contour interval 100'.

Natural Resources Canada. 1996. Canmore Alberta. 82 0/4. 1 :50,000 contour interval 40 metres.

Aerial Photographs

820, Line 24B 381 0- 3, September 13, 1988, 1 :40,000 820, Line 24A 381 9-283, September 13, 1988, 1 :40,000

APPENDICES

Determination of historical flows in Goat Creek based on historical data (1 91 5-1 929) for the Spray River watershed

Based on graph From Golder Associates 1996.

The dotted line represents an estimation of historic flows in Goat Creek based on its current watershed size (40.9 km2). The thick black line represents the estimation based on the size of the historic watershed (70km2).

Drainage areas (krn')

APPENDIX 11: HISTOIUCAL FLOW DATA

SORAY AT BWIPT - SPAR- IO. 05BC001

ANNUAL mM DIscmRcEs m CUBIC Prn SEaJllD 21311 m E'mIaD cf Rxmm APR I U Y JlRl JUL AUG S&? OCT m3V DEC HW(

GPPENDLX 11: WSTORICAL n o w DATA

From Historical Streamflow Summary - Alberta. 1990. Environment Canada Water Resources Branch, Water Survey Branch. Water Survey of Canada.

COAT QCePE AT BAWFF PARK H X W D M Y - SPATfCH NO. OSBCOO8

.?lOITITCf AND lWMlAL GXSCHARQS M CUBIC HZTRES PER SECOCID FDR T I E ZERXW Q RECURD

YEAR JAN FEB MhR APR UAY JVPI 3UL AUG SEP CCT HOV DEC .SAN

GOAT LtS[ AT BANFF P A ! - STmCN K). 358C008

ANKJAL OF DiSSARGE AND ANMTAL DISCBARGZ iT)R TAE PEitTCC OF =CORD

lEAR nAXU.IVn I N 7 U . S DISQPlRTr .WHfM;)( DAnfY 3ISCEAl'GE Z m A L DISCBARGE - Wf )Dxs-- (m3 5) (ma s) (bJ) 3.26 OH AUG 22 3.96 ON AUC 07 1.50 ON AUG 20 3.34 ON sn 09

--- -- 1.59 OR JUN 19 --- 1.96 ON OCl' 29

3.82 CW A f f i 22 1.53 a W S E P 2 3 . 4.03 ON SEP 19 ' 2.04 AT 14:OO MST Q( APR 16 1.38 OW APR fi

--- 2.14 CN JLM 01 0.1688 QI 14

9 - ICE -I'XOCCS ' - EIflZIPe REa)I(DED FOR ZBE PERIOD OF

APPENDIX 111: HABITAT SUITABJLITY CURVES

Cutthroat Trout Habitat Preference Curves for Habitat Suitability Index Source: Hickman and Raleigh 1982

(V1 ) Avg. max water temp. - summer 012) Avg. max temp during embryo development

(V3) Avg- minumum DO (V4) Avg. thalweg depth in low flow

3 4 5 6 7 8 9

Otuolved Oxygen (mgll)

(V5) Avg. velocrty over spawning areas

(V7) Avg. substrate size 0.3-8cm in spawning areas

(V6) % cover in late growing season

(V8) % substrate 1040 cm for winter cover

(V9) Dominant substrate in riffle run areas

A: Rubble or small boulders dominant B: Rubble, gravel and fines in equal amounts C: Fines, bedrockor large boulders dominant

(V11) Avg. %vegetation for allochtonous output

1 0.8 0.6 0.4 0.2 0 0 25 50 h 1 0 0 1 2 5 150

Streanbank wqdatkm cover (Y

(V13) Avg. pH

(V16) % fines in riffle run and spawning areas

(VlO) %pools in late growing season

(V12) Avg. % rooted vegetation for erosion controi

Stmanbank vcqctatkn cover Cn)

(V14) Base flow as percent of average annual daily flow

Base k a v g annual daily tow Cn)

(V15) Pool class ratjng

A: > 30% large, deep pools 6: 10-30% large, deep pools. >SO%Medium C: 10% large deep pools, 4 0 % moderate

APPENDIX 111: HABITAT SUITABILITY CURVES

Bull Trout Habitat Prebrence Curves Source: Fernet and Bjomson 1997

Cover Cover code definitions: 1 : No cover 2: l nstream object for velocity sheiter (Substrate. boulders, debris) 3: Instream/offstream visual isolation (undercut bank, log lams, overhanging canopy -

---- Adult Spawning Sites

0 1 2 3

Cover code

1

0.8

0.6

0.4

0.2

0 1 2

Cover cock

Substrate suitability for spawning bull trout

Substrate suitability for spawning

: I 1

0 10 2033 40 50 80 7 0 8 0 90100110120130

Substrate particle size (mm)

APPENDIX UI: HABITAT SUITABILITY CURVES

8ull trout preference curves Source: Golder Associates - 1997

Bull 1 rout depth preference curves

. - -- - - -

- -- -. --

Bull Trout velocity preference curves

1 -1 -

an investigation of the potential to restore native trout

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