AQUATIC ECOSYSTEM RESTORATION PROJECTandrewsforest.oregonstate.edu/research/component/... · land (Rosboro Lumber Company) while the upper reaches of the watershed are public lands

AQUATIC ECOSYSTEM

RESTORATION PROJECT

EFFECTS OF THE FLOODS OF 1996

QUARTZ CREEK

WILLAMETTE NATIONAL FOREST

Submitted by:

Dr. Stan GregoryRandy Wildman

Department of Fisheries and WildlifeOregon State University

Corvallis, Oregon

December, 1998

TABLE OF CONTENTS

I. Introduction....................................................................................................................1

II. Review of the two flood events of 1996.....................................................................2Overview of Quartz Creek restoration project...........................................................4

III. Project site description................................................................................................6

IV. Methods ........................................................................................................................8

V. Results........................................................................................................................ 11Characteristics prior to project installation............................................................. 11

Project installation............................................................................................... 13Installation of wood accumulations.................................................................... 15

Responses after project installation........................................................................ 21Behavior of large wood accumulations............................................................. 24Retention of water and particulate material...................................................... 26Change in channel morphology......................................................................... 45Changes in trout populations ............................................................................. 47

VI. Discussion................................................................................................................. 58Performance of log structures............................................................................ 58Evaluation of log accumulations ........................................................................ 66Ecological responses......................................................................................... 67

VII. Summary.................................................................................................................... 72

VIII. Suggestions.............................................................................................................. 73

IX. Literature Cited.......................................................................................................... 75

1

INTRODUCTION

Quartz Creek is a major tributary on the south side of the McKenzie River in the western

Cascades of Oregon and potentially supports populations of coastal cutthroat trout (Oncorhynchus

clarki), rainbow trout (O. mykiss), chinook salmon (O. tshawytscha), and bull trout (Salvelinus

confluentus). Past forest practices and possibly natural events have resulted in an almost total loss

of wood from the Quartz Creek channel. The upper portion of the watershed is National Forest

System land and the lower portion is private industrial forest. The U.S. Forest Service began

restoration of the existing habitat on public land in 1988 by placing large wood accumulations back

into the stream. From 1988-93, the Department of Fisheries and Wildlife at Oregon State University

conducted an inventory of physical habitat and fish populations to assist the U.S. Forest Service in

developing appropriate wood accumulations to correct habitat deficiencies.

Summer of 1993 marked the end of a five-year study period after ecological restoration of

the stream and a report entitled “Aquatic Ecosystem Restoration Project - Quartz Creek Five-Year

Report” was produced. OSU personnel conducted an abbreviated survey for wood recruitment of the

Quartz Creek restoration site in 1994 and 1995. It was agreed upon that OSU would conduct

detailed monitoring of the channel and ecological features in the event of a major flood. Two major

floods in the 1996 calendar year dramatically altered stream ecosystems and adjacent riparian

areas at Quartz Creek and river basins throughout the Pacific Northwest. Extraordinarily high

stream flows and associated landslides and flows moved boulders, deposited sediment, and shifted

channels along many streams in the McKenzie River basin while other streams in the basin

exhibited little change. Evidence from Quartz Creek and the H.J. Andrews Experimental Forest

indicates that the two major floods of 1996 behaved differently in basins on the south and north

sides of the McKenzie River. The flood that occurred in February resulted in higher stream

discharges on the north side of the McKenzie River. The flood in November resulted in higher

stream flows on the south side of the McKenzie River.

2

DESCRIPTION OF THE TWO FLOOD EVENTS OF 1996

In 1996 the Pacific Northwest experienced not one but two very large storm events. The

first flood event started with a series of intense surges of subtropical moisture during the period of

February 5 – 9, 1996. Storms of this type from the western Pacific are not rare for Oregon but this

storm was unusual in that the surge persisted with strong intensity for 4 days. Record amounts of

precipitation were reported at locations in Oregon (http://www.ocs.orst.edu) with the maximum

occurring at Laurel Mountain in the Coast Range which received 70.8 cm (27.9 in) of rain in the 4-

day period (Figure 1).

A very large snow pack was present in the Cascade Mountain Range when this storm

arrived. As of January 31 the Willamette basin snowpack was 112% of the long-term average for

that date. Very warm temperatures accompanied this moist air mass and snow began to melt

quickly. Throughout this storm event the freezing level remained at about 2,100 – 2,400 m (7,000 to

8,000 ft) in elevation. The combination of record-breaking rain, warm temperatures, and the deep

snowpack in the Cascade Mountains led to severe flooding. This type of flood event is called a

“rain-on-snow” event and occurs when a subtropical storm drops heavy rainfall onto a previously

accumulated snowpack.

During the middle of this 4-day storm event streams rose quickly. For example, the

McKenzie River rose from 113 m3/s (4,000 ft3/s) to 566 m3/s (20,000 ft3/s) in one day at Vida. The

McKenzie River reached a peak flow of 730 m3/s (25,800 ft3/s) at 10:00 P.M. on February 9th. The

crest height for the McKenzie River at Vida is 2.7 m (8.8 ft) but this flood brought the flood stage up

to 3.4 m (11.0 ft). River flood stages were comparable in magnitude to the December 1964 flood,

the largest flood in Oregon since flood control reservoirs were built in the 1940’s and 1950’s.

Examination of discharge records from streams at the H.J. Andrews Experimental Forest indicates

that the 1996 storm was apparently a larger event than the 1964 flood at low elevations and a

smaller event at higher elevations. Peak discharges at small low-elevation basins such as

Watershed 1 in the H.J. Andrews Experimental Forest were up to 40% higher in 1996 than the

3

Figure 1. Total precipitation for Quartz Creek watershed, Oregon and surrounding states,February 5 - 9, 1996.

4

next highest storm, which occurred in December 1964. At small high-elevation basins, peak

discharges were as much as 30% lower than the storm of 1964 (Figure 2)

(http://www.fsl.orst.edu/lter/flood.htm).

There is no discharge gauging station on Quartz Creek so exact flood discharge

measurements are not available for this stream. A USGS gauging station does exist on Lookout

Creek in the H.J. Andrews Experimental Forest, which is approximately 24 km (15 miles) away.

Lookout Creek is a fifth-order stream but is somewhat comparable in size to Quartz Creek. Peak

flows on Lookout Creek crested at 3.1 m (10.1 ft), which corresponds to a flow of 278 m3/s (9,800

ft3/s). Peak flows at the same site during the 1964 flood were 189 m3/s (6,660 ft3/s). Examination

of the USGS gage site after the February 1996 flood revealed at least a meter of gravel deposited in

the control section for the gage, suggesting that the rating curve may have overestimated the

discharge.

November 18-20 brought a second major flood event to Oregon in 1996. The Pacific

Northwest received record-breaking amounts of rainfall in a short period of time resulting in

widespread flooding and numerous landslides. As in the February storm, this storm was created

when a broad upper-air weather system of moist subtropical air originating over the tropical Pacific

swept into Oregon. Heavy rainfall amounts were reported throughout the state with all-time one-day

precipitation records being set at many locations. The City of Corvallis set an all-time one-day

record of 10.9 cm (4.28 in) of precipitation. The main difference in this second storm compared to

the storms of February 1996 and December 1964 was the reduced snowpack at higher elevations

and the precipitation fell as rain onto bare ground in November.

Overview of Quartz Creek Restoration Project

A brief overview on the background of the Quartz Creek restoration project is presented in

this report. For a detailed description of the study, the five-year report should be consulted. This

report focuses on the results of monitoring conducted at the Quartz Creek restoration site in 1996

5

and 1997 and the effects of the two major floods on geomorphology, wood, retention, and fish

populations at the site.

6

Figure 2. Comparison of flood peaks for watershed 1 in the H.J. Andrews Experimental Forest forFebruary 1996 and December 1964.

7

The project objective at Quartz Creek was to reestablish natural volumes of large wood to

provide complex wood accumulations for salmonid habitat. The increase in wood in Quartz Creek

would in turn increase the residence time of water, retention of nutrients, and availability of food

resources, which potentially could increase fish populations.

The project was designed to introduce and recruit large wood to restore the size classes

and volumes that occur in undisturbed streams of similar size and gradient in the McKenzie River

drainage. Larger size classes of wood (generally greater than 5 m (16.4 ft) in length and 0.50 m

(1.64 ft) in diameter) were placed in the stream to create a matrix of large stable wood that would

trap smaller material. This large wood was expected to create the channel structure and wood

accumulations found in old-growth forest streams by forming a “backbone” to retain sediment and

smaller wood.

PROJECT SITE DESCRIPTION

Quartz Creek is a 4th-order stream as defined by Strahler (1957) with a total drainage area

of 10,927 ha (27,000 acres). The lower 14.5 km (9 miles) of the stream flow through private forest

land (Rosboro Lumber Company) while the upper reaches of the watershed are public lands

managed by the U.S. Forest Service. The habitat restoration site was located just upstream from

the National Forest boundary approximately 14.5 km (9 miles) from the confluence with the

McKenzie River (Figure 3). At the habitat restoration site, Quartz Creek is a 3rd-order stream with a

drainage area of 3,440 ha (8,500 acres).

Habitat structure was modified within a 1,100-m (3,609-ft) reach of Quartz Creek in 1988.

Lower and upper sections of the project reach are located in a 400-yr old-growth forest. The middle

section of the project site was clearcut down to the stream banks in 1975. The reach has an

average slope of 4% with a streambed composed predominantly of small and large boulders. Long

cascades with channel gradients of more than 8% occur within the study reach. Relatively low

amounts of wood were present in the channel due to past disturbances and salvage logging

operations.

8

Figure 3. Map of Quartz Creek and it’s location within the Willamette National Forest.

9

METHODS

The 1,100-m (3609-ft) reach of Quartz Creek was mapped in detail prior to log introduction.

Locations of all existing wood and all boulders over 0.5 m (1.64 ft) in diameter were recorded.

Boundaries of geomorphic surfaces (e.g., wetted channel, active channel, and floodplains) were

indicated on the maps. Locations of all large trees (by species), snags, wood accumulations,

undercut banks, and areas of bedrock outcrops along the stream channel also were recorded.

The 1,100 m (3,609 ft) habitat restoration site was divided into discrete habitat units

following the procedures developed by Hankin and Reeves (1988). Width and depth at three

transects, length, maximum depth, slope, and percent bedrock were measured for each habitat

unit. Number of boulders in each channel unit were counted and placed into two size classes 0.5-

2.0 m and >2.0 m (1.64-6.56 ft and >6.56 ft).

Monumented photographic stations were established through the project site.

Photographic stations were installed at 20-m (65.6-ft) intervals along the channel margins and

marked with white PVC stakes. Photographs were taken upstream and downstream of each station

from both the stream margin and a point in the center of the channel. Compass bearing, time of

day, exposure settings, camera and lens type, and film type for each exposure were recorded so

that duplication of each photograph would be possible at future dates. Additional photographs were

taken of all locations where habitat restoration structures were to be constructed.

Three time-lapse cameras were installed at Quartz Creek in December 1988. Exposure

intervals of 15 minutes were set initially on the Super-8 movie cameras at Quartz Creek to

document long-term changes in the stream bed. Exposure intervals were lengthened to 30 minutes

in August 1991 to allow for longer intervals between changing film. These cameras are currently

being maintained to visually record long-term changes at Quartz Creek.

Channel hydraulics were measured using the fluorescent dye tracer rhodamine WT. A dye

solution was injected into the stream at a constant rate until concentrations of dye were uniform

throughout the stream reach. Dye injection was then terminated and the gradual decrease in dye

10

amounts at a downstream sampling station was recorded using a field fluorometer. Relative

hydraulic retention can be calculated from the rate at which dye concentration increases during dye

addition and decreases after termination of dye addition.

Particulate retention was measured by adding known numbers of presoaked, neutrally

buoyant ginkgo leaves (Ginkgo biloba) (Speaker 1985). A total of 4,000 ginkgo leaves were

released at the top of each reach. A seine was placed 50 m (164 ft) downstream, and all leaves

captured in the seine during a 2-hr interval were counted. A retention coefficient was calculated

using the number of leaves added initially and the number recovered in the seine after 2 hr:

Ld = Lo.e-kd

Ld = Percent of leaves in transport at distance d from release pointLo = Percent of leaves released (100%)k = Retention coefficientd = Distance from release point (m)

The project site was divided into six release reaches with distinct geomorphic

characteristics (Table 1). Locations of dye and leaf introductions and fluorometer sampling sites in

these six reaches were located on site maps so that retention measurements can be duplicated in

successive years.

All wood ≥1.0 m (3.28 ft) in length and ≥10 cm (3.94 in) in diameter was measured for

length and diameter (minimum and maximum). Volume of each piece was calculated using the

formula for a frustum of a paraboloid:

V = 3.1416(D1

2 + D

2

2).L

8

V = Volume (m3)D

1 and D

2 = Diameters at each end (m)

L = Length (m)

Each piece was tagged with numbered aluminum tags and location in the channel was recorded.

11

Table 1. Characteristics of reference 50-m reaches used to measure leaf retention in QuartzCreek. Reach location refers to distance along monumented baseline in meters;downstream boundary is designated as 0 meters. Structure numbers are specificaccumulations located in reaches where retention was measured.

ReachType

ReachLocation

StructureNumber Accumulations Forest

Site 1 165 - 215 9 Deflector Old growth10 V-Deflector11 Sill logs12 Lateral deflector

Site 2 300 - 350 18 Lateral deflector Old growth19 Full-channel jam

Site 3 405 - 455 24 Upstream V Clearcut25 Upstream V26 Upstream V

Site 4 580 - 630 35 V-Deflector Clearcut36 Parallel bank log

Site 5 765 - 815 42 Upstream V ClearcutSite 6 995 - 1045 50 Full-channel jam Old growth

Channel cross-sections around log accumulations were not established until after project

completion because of possible disturbance by the excavator (cross-sections are on file at Oregon

State University). A minimum of one cross-section was established through each structure, and

two or three transects were installed at more complex log accumulations, such as upstream V-

shaped accumulations and full jams. Metal fence posts were placed above the active channel to

permanently monument cross-section end points for future use and subsequent measurements.

Notches in the metal posts were used to mark level reference lines for each transect.

Aquatic insects were collected for the Willamette National Forest before and after wood

installation in 1988. Collections of invertebrates have continued each summer since 1988.

Samples were collected with a modified Hess sampler (25-cm diameter, 250-um mesh size) in

riffles with a gravel/cobble substrate. A total of nine samples were taken on each date; three from

the lower old-growth area, three from the clearcut area and three from the upper old-growth area. All

samples were placed in whirl-pack containers and preserved with 95% ethanol. Invertebrate

12

samples are stored at Oregon State University. Invertebrate analysis was not part of this study and

is not described in this report.

In 1988 and 1989, fish abundance and distribution were determined by the snorkeling

method (Hankin and Reeves 1988). Each channel unit was inventoried for fish by one diver and

reinventoried by a second diver approximately 30 minutes later. Species, size, and habitat location

were recorded for each fish observed. The restoration reach and adjacent reference reaches were

snorkeled for direct fish observation in August in 1990-1993, 1996, and 1997 and diver estimates

were calibrated by population estimation by electroshocking (Armour et al. 1983).

RESULTS

Characteristics Prior to Project Installation

Forty-two individual habitat units were identified within the study site. Before structure

installation, cascades were the dominant channel unit type comprising over 46% of the study area

(Table 2). Other relatively high gradient habitat units, rapids and riffles, made up 24% and 14% of

the reach respectively. Pools, an important habitat for fish, comprised only 10% of the entire reach.

Side-channels, important habitat for fry rearing accounted for only 6% of the stream channel.

Prior to the structure installation, 212 pieces of wood were found in the 1,100-m (3,609-ft)

reach. This amount is relatively low compared to natural amounts in similar streams in the

McKenzie River drainage. Mack Creek, a third-order stream in the H.J. Andrews Experimental

Forest, has over 1,666 pieces of wood in a 1,000-m (3,281-ft) reach. Volume of all existing wood at

Quartz Creek was 0.027 m3/m

2 (10.4 ft

3/ft

2) of active stream channel while the volume of wood at

Mack Creek was 0.246 m3/m

2 (93.4 ft

3/ft

2) of active stream channel. Areas above and below the

restoration site contained higher amounts of wood, but all three reaches of Quartz Creek had similar

amounts of wood after log installation in 1988.

13

Table 2. Channel unit distribution before and after wood installation at Quartz Creekrestoration site in 1988.

Pre-Installation Post-Installation

Unit Type # Percent ofLength

# Percent ofLength

Pool 7 10 11 16Riffle 8 14 8 15Rapid 10 24 10 23Cascade 15 46 15 40Side-Channel 3 6 3 6

Of the 212 pieces of pre-existing wood, only 70 pieces had >25% of their volume within the

active channel. A large portion of the pieces of wood was located on the active channel terrace or

perched above the active channel. These pieces of wood had little or no effect on the stream and

provided little or no habitat for fish.

The fish community at Quartz Creek restoration site includes cutthroat trout, rainbow and

steelhead trout, and Paiute sculpins (Cottus beldingi). Cutthroat trout are the dominant salmonid in

the restoration reach, making up 90% of total fish numbers. One adult steelhead was observed in a

pool (Pool-25) located in the upper clearcut reach in August of 1988 and 1989. Bull trout were

observed in lower Quartz Creek near the confluence with the McKenzie River, but none were found

in the habitat restoration site.

In the summer before structure installation, trout densities averaged 66 fish/100 m (20

fish/100 ft) of stream in the restoration reach. Densities of 50-150 fish/100 m (15-46 fish/100 ft) have

been recorded for similar streams in the H. J. Andrews Experimental Forest (Lookout Creek and

Mack Creek). Pool habitats held the greatest densities of trout at 111 fish/100 m (34 fish/100 ft),

while the lowest density of trout occurred in cascade habitats at 59 fish/100 m (18 fish/100 ft).

Riffles and rapids contained intermediate densities with 75 fish /100 m (23 fish/100 ft) and 69

fish/100 m (21 fish/100 ft), respectively.

14

Size frequency distribution of fish in 1988 exhibited reduced proportions of fry and older fish

and was dominated by 10.2 to 12.7 cm (4 to 5 in) fish (Figure 4). Rainbow trout in the system were

slightly larger in size than the cutthroat. The largest individuals observed, other than the one

steelhead, were several 28 cm (11 in) rainbow trout usually in deep pools associated with cover.

The most numerous trout were in the 10.2-12.7 cm (4-5 in) class corresponding to 1+ year age

class.

Project Installation

Log and boulder accumulations were installed in October of 1988. Trees were felled in a

section of old-growth forest (non-riparian) 0.8 km (0.5 miles) from the project site and transported by

a D-8 Caterpillar to locations along the stream. Boulders used to stabilize log accumulations were

obtained from the immediate channel area. Twenty-five root-wads from an adjacent quarry also were

used in structure construction.

A track-driven hydraulic excavator prepared the streambed for log introductions and placed

individual logs in position. A "trash rack" was installed below the project site to minimize possible

downstream movement of logs and potential risks to bridges lower in the system.

Tree species used for log accumulations consisted of western red cedar (Thuja plicata),

Douglas-fir (Pseudotsuga menziesii), western hemlock (Tsuga heterophylla), and bigleaf maple

(Acer macrophyllum). Cedar logs (n = 105) were used extensively because of their slow

decomposition rate and Douglas-fir logs (n = 77) were used when very large diameter logs were

required. Western hemlock (n = 3) and big leaf maple (n = 1) were rarely used because of their

faster decomposition rates.

15

Figure 4. Size distribution of cutthroat and rainbow trout in Quartz Creek restoration site, July1988.

0

1

2

3

4

5

NU

MB

ER

OF

FIS

H(H

undr

eds)

2 4 6 8 10 12 14LENGTH (inches)

QUARTZ CREEK REHABILITATION SITESIZE FREQUENCY OF FISH - JULY 1988

16

Installation of Wood Accumulations

A total of 48 log accumulations were installed in Quartz Creek using 186 pieces of wood.

The volume of wood installed was 0.067 m3/m

2 (35.8 ft

3/ft

2) of active stream channel. Two additional

sites were modified by boulder placement alone. Various types of log accumulations and degrees

of cabling were used to evaluate effectiveness and longevity of different types of material

installations (Figures 5a-d and 6a-c). Seven types of log accumulations, some designed to

resemble natural woody accumulations, were used in the project:

Full-channel dams Sill logsLateral deflectors Cover logsLateral V-shaped deflectors Parallel bank logsUpstream V-shaped accumulations

Three degrees of cabling (full cable, partial cable, and no cable) were applied to each type of

structure in the project reach (Table 3).

Table 3. Number of log accumulations of different types and cabling used in Quartz Creek inOctober 1988.

Structure Full Cable Partial Cable No Cable

Full-channel dam 1 1 1Lateral deflector 4 4 1Lateral V-shaped deflector 3 3 2Sill log 2 0 0Upstream V-shaped accumulation 2 2 2Cover log 2 4 2Parallel bank log 3 0 2Road log 2 0 5

Full-channel dams consisted of accumulations of wood that spanned the entire bankfull

channel. Lateral deflectors were small accumulations anchored on one bank and extending into the

wetted channel. A lateral V-shaped deflector was similar to a lateral deflector but included a

downstream log intersecting at the point of the V. A sill log spanned the channel and lay directly

17

Figure 5a-b. Single log accumulations installed at Quartz Creek restoration site, October 1988.

Top: Sill log structure. Bottom: Pool cover log structure.

18

Figure 5 c-d. Single log accumulations installed at Quartz Creek restoration site, October 1988.

Top: Parallel bank log. Bottom: Lateral deflector.

19

Figure 6 a-b. Multiple log accumulations installed at Quartz Creek restoration site, October 1988.

Top: Upstream “V” accumulation. Bottom Lateral “V” – shaped accumulation.

20

Figure 6 c. Full channel jam accumulation installed at Quartz Creek restoration site, October

1988.

21

on the surface of the streambed, creating a sill. An upstream V-shaped accumulation was two or

more logs that spanned the channel and intersected at a point upstream of their base. Cover logs

were generally small accumulations of logs placed in pools to create overhead cover for fish.

Parallel bank logs were single logs placed on the edge of the wetted channel against the bank to

create small amounts of lateral cover at low flow. Road logs were placed at the intersection of the

temporary skid roads and the active stream channel to prevent encroachment of the stream onto the

roadbed.

Location and position of each structure were added to the maps of Quartz Creek. Changes

in channel geomorphology and movements of boulders and pre-existing wood by the excavator were

also recorded on the existing project maps to provide a final map. Addition of the 48 log

accumulations trapped a large amount of wood within the active channel (Table 4).

Table 4. Large wood characteristics at Quartz Creek before and after structure installation.

Characteristic Prior to ProjectInstalled by

Project After Project

Accumulations 2 48 50Full Channel dams 0 3 3Total Pieces of 212 186 398Logs in Channel (>25%) 70 131 201Logs ≥10 m long and 75 cm wide 6 49 55Logs ≥6 m long and 60 cm wide 23 94 117

Several photographic stations were destroyed by machinery and required careful

replacement. A complete set of photographs was retaken from each photopoint station.

Photographs were taken every year of each specific structure site to document changes in

substrate composition and channel hydraulics. All photographs are 35-mm slides and have been

labeled and archived at Oregon State University.

22

Immediate changes in channel unit composition were observed when the 1,100-m (3,609-ft)

reach was reinventoried in 1988 for habitat unit composition. Four additional pool habitat units were

created in units that previously were cascades. Proportion of pool length over the entire reach

increased from 10% to 16%, and length of stream in cascade habitat units decreased from 46% to

40%. Areas that originally were long, high velocity cascades were converted to a stair-stepped

longitudinal profile by wood placement. Habitat unit lengths of riffles, rapids, and side channels

remained relatively unchanged.

Late installation of logs in 1988 because of fire danger minimized the time available to

remeasure channel composition and fish abundance before high stream flows. Substantial

increases in discharge in November terminated the fish survey and retention studies. Higher

discharges in late fall prevented comparison with data collected at low discharges prior to log

introduction.

Responses after Project Installation (1989-1997)

The Quartz Creek habitat restoration site had detailed monitoring conducted each summer

from 1989 to 1993. In 1994 and 1995 a reduced survey of the restoration reach was conducted

measuring channel units and movement of wood. In the summers of 1996 and 1997 complete

surveys were conducted again. The survey conducted in the summer of 1996 measured changes at

the site as a result of the February 1996 flood and sampling in the summer of 1997 measured

changes from the November 1996 flood. All geomorphic and biological parameters were

remeasured in the same manner as in the pre-introduction data collection. Photographs were taken

from all monumented photopoints.

Time-lapse camera systems have been maintained throughout the period. Influences of

high water discharges on three types of log accumulations have been recorded. Though quantitative

measurements are difficult to derive from these time-lapse films and photopoint photographs,

valuable qualitative information on relative movement of large wood has been obtained.

23

Starting in 1989, we surveyed additional distances of 400 m (1,312 ft) below and 1,500 m

(4,922 ft) above the 1,100-m (3,609 ft) habitat restoration site with the Hankin-Reeves stream survey

methodology. Length of pool habitat in the restoration site increased from 10% before structure

installation to 21% by 1993 (Table 5). Pool habitat remained relatively stable in both 1994 and 1995

at 20% and 18% respectively. After the February 1996 flood, length of habitat in pools decreased to

15% in the summer of 1996 but increased to 16% after the November 1996 flood. Quality of pool

habitat also increased with a mean maximum depth of 0.76 m (2.5 ft) before structure installation to

1.04 m (3.4 ft) in 1993, 0.98 m (3.2 ft) in 1994, and 1.10 m (3.6 ft) in 1995. After the February 1996

flood the mean maximum depth of pools was 0.92 m (3.0 ft) and after the November 1996 flood the

mean maximum depth returned to 1.04 m (3.4 ft).

Length of side-channel habitat changed significantly over the first 5-yr period. Before

structure installation, 6% of channel length in the restoration site was in side-channels; but in 1993,

23% of the total length of stream channel was side-channel habitat. After the February 1996 flood,

34% of the total length of stream channel was side-channel habitat, but in 1997 side-channel habitat

was reduced to 26%. Total area of side-channels accounted for 161 m2 (1,732 ft2) in 1988 (2.0% of

total wetted channel) and 589 m2 (6,338 ft2) in 1993 (6.2% of total wetted channel). In both 1994

and 1995, side-channels accounted for 8.4% of the wetted channel. After the February 1996 flood,

side-channels accounted for 1,331 m2 (14,322 ft2), (13.3% of total wetted channel); but after the

November 1996 flood, side channels accounted for 752 m2 (8,092 ft2), (8.1% of total wetted

channel).

24

Table 5. Total length of channel units (m) for the below restoration reach, restoration reach, andabove restoration reach at Quartz Creek for 1988,1993-1997. Total length is the sum ofmain channel and side channel (SC) lengths. Percentage of total wetted channellength for each habitat unit type is included in parentheses.

BELOW RESTORATION REACH

ChannelUnit 1989 (%) 1993 (%) 1994 (%) 1995 (%) 1996 (%) 1997 (%)

Pool 40 (10) 84 (16) N/A N/A N/A N/A 73 (11) 100 (15)Glide 0 (0) 17 (3) N/A N/A N/A N/A 0 (0) 12 (2)Riffle 57 (15) 129 (25) N/A N/A N/A N/A 232 (36) 224 (33)Rapid 130 (33) 251 (48) N/A N/A N/A N/A 185 (28) 92 (14)Cascade 162 (41) 0 (0) N/A N/A N/A N/A 97 (15) 166 (24)SC 0 (0) 41 (8) N/A N/A N/A N/A 37 (6) 63 (9)Step 2 (1) 4 (<1) N/A N/A N/A N/A 23 (4) 21 (3)Total (m) 391 526 647 678

RESTORATION REACH

ChannelUnit 1988 (%) 1993 (%) 1994 (%) 1995 (%) 1996 (%) 1997 (%)

Pool 116 (10) 280 (21) 273 (20) 251 (18) 237 (15) 221 (16)Glide 0 (0) 17 (1) 16 (1) 12 (1) 17 (1) 0 (0)Riffle 157 (14) 201 (15) 195 (14) 180 (13) 252 (16) 216 (16)Rapid 264 (24) 329 (24) 271 (20) 262 (19) 234 (15) 262 (19)Cascade 509 (46) 197 (14) 249 (19) 289 (21) 259 (17) 275 (20)SC 69 (6) 315 (23) 313 (23) 351 (26) 531 (34) 367 (26)Step 0 (0) 30 (2) 37 (3) (26) (2) 32 (2) 43 (3)Total (m) 1,115 1,369 1,354 1,371 1,562 1,384

ABOVE RESTORATION REACH

ChannelUnit 1989 (%) 1993 (%) 1994 (%) 1995 (%) 1996 (%) 1997 (%)

Pool 264 (17) 220 (13) N/A N/A N/A N/A 343 (18) 256 (15)Glide 0 (0) 39 (2) N/A N/A N/A N/A 0 (0) 0 (0)Riffle 65 (5) 127 (8) N/A N/A N/A N/A 206 (11) 127 (8)Rapid 459 (30) 294 (18) N/A N/A N/A N/A 199 (11) 204 (12)Cascade 725 (47) 965 (58) N/A N/A N/A N/A 1001 (54) 1028 (60)SC 0 (0) 21 (1) N/A N/A N/A N/A 85 (5) 59 (3)Step 15 (15) 9 (<1) N/A N/A N/A N/A 26 (1) 33 (2)Total (m) 1,528 1,675 1,860 1,707

25

Behavior of Large Wood Accumulations

As of 1993 only 21 of the 186 pieces of wood originally installed (11.8%) had been

transported out of the restoration reach. After the November 1996 flood, two additional pieces of

introduced wood were transported out of the restoration reach. Of the 48 instream log

accumulations installed in Quartz Creek, 22 log accumulations "moved" during flood discharges.

Operationally, we defined "movement" of an accumulation as transport of pieces within a structure

one meter or greater downstream. Logs used as road blocks were not included in the analyses but

were reported in Table 6. The relative degree of cabling in the log accumulations did not affect

tendency for structures to move. Of the 20 log accumulations (excluding road block logs) that

moved more than 1 m (3.28 ft), nine were completely cabled, six were partially cabled, and five were

not cabled. If a distance of 10 m (33 ft) or greater is used for classifying a structure as moving, only

eight structures moved: two fully cabled, three partially cabled, and four non-cabled (Table 6).

The distance logs moved downstream differed for the three degrees of cabling applied.

Transported logs from fully cabled structures moved an average distance of 55 m or 180 ft (n = 18

logs; mean length = 10.5 m or 34.5 ft; mean diameter = 0.78 m or 2.6 ft). Logs in partially cabled

structures that were transported moved an average distance of 93 m or 305 ft (n = 11 logs; mean

length = 8.5 m or 27.9 ft; mean diameter = 0.76 m or 2.5 ft). Transported logs that were in

accumulations with no cabling moved an average of 246 m or 807 ft (n = 27; mean length = 5.7 m or

18.7 ft; mean diameter = 0.69 m or 2.3 ft). The maximum distance a fully cabled log moved was

620 m or 2,034 ft (7.4 m or 24.3 ft long, 0.80 m or 2.6 ft diameter). The maximum distance a

partially cabled log moved was 295 m or 968 ft (4.8 m or 15.7 ft long, 0.60 m or 2.0 ft diameter).

The maximum distance an uncabled log moved was 1,000 m or 3,281 ft (2.3 m or 7.5 ft long, 0.45 m

or 1.5 ft diameter).

Most of the accumulations that moved or shifted less than 10 m (33 ft) downstream are still

performing the original objectives they were designed to perform. Logs that moved downstream

greater distances tended to function differently than the original planned objective.

26

The flood of February 1996 deposited an additional log accumulation in the middle of the

restoration reach. A log 10.0 m (32.8 ft) long and 0.26 m (0.85 ft) in diameter was deposited

perpendicular to the stream flow along with several other pieces at the 590 m (1,936 ft) position on

the baseline maps. A large plunge pool was formed behind this new accumulation in 1996 and has

deepened and enlarged in 1997.

Table 6. Characteristics of log accumulations that moved ≥1 meter in Quartz Creek fromSeptember 1988 to 1993, 1996, and 1997. Logs used as road blocks were notincluded in analyses of movement.

Structure Type andNumber

Degree ofCabling

1993 DistanceMoved (m)

1996 DistanceMoved (m)

1997DistanceMoved (m)

Full Jam (#2) Partial 10 10 10Lateral Deflector (#3) Full 10 10 10Upstream V (#5) None 120 120 120Parallel Bank (#6) None 90 90 90Pool Cover (#8) Partial 5 5 5Lateral Deflector (#9) Full 5 5 5Sill Log (#11) Full 2 2 2Pool Cover (#13) None 220 220 220Pool Cover (#20) None 1 1 20V Deflector (#23) None 2 2 2Upstream V (#24) Partial 90 90 90Upstream V (#25) Full 2 5 5Pool Cover (#29) Full 8 8 8V Deflector (#35) Partial 2 2 2Parallel Bank (#36) Full 0 0 2Parallel Bank (#40) Full 85 85 85Upstream V (#42) Partial 12 17 93Lateral Deflector (#46) Partial 4 4 4Upstream V (#48) Full 5 5 5Full Jam (#50) Full 5 5 5

Road Block (#28) None 140 140 140Road Block (#30) None 180 180 180

27

Retention of Water and Particulate Material

Dye releases performed before log introductions showed that hydraulic retention was

relatively low in the high gradient single channel sections of the study site. Particulate retention

was lowest in the bedrock chute area opposite the quarry. Hydraulic and particulate retention were

somewhat higher in those reaches that contained side-channels or in areas where some wood was

present in the channel. In reaches where dye concentrations rapidly approached a maximum

asymptotic concentration, hydraulic retention was low. Hydraulic retention was greater when the

time to reach asymptotic concentrations took longer.

Measurements of channel hydraulics and retention were conducted again in 1996 and 1997

in the same six reaches that were analyzed before structure installation (Figures 7a-f). Though the

same stock concentration of dye and rate of injection were used as in previous years, asymptotic

concentrations varied from year to year due to changes in stream discharge. When constant dye

injection rates are used during lower stream flows, observed concentrations of dye increase.

Stream discharge (Q) is calculated using the rate of injection, the concentration of dye injected, and

the measured concentration of dye in the stream at asymptotic concentration at the downstream

sampling site (Kilpatrick 1967). Discharges in mid-summer ranged from 0.09-0.36 m3/s (3.0-12.7

ft3/s) during the first 5 years of the project, averaging 0.20 m3/s (6.9 ft3/s) (Table 7). In 1996 summer

discharges were low with an average of 0.08 m3/s (2.66 ft3/s). Flows increased in the summer of

1997 with an average discharge of 0.14 m3/s (4.98 ft3/s).

Table 7. Discharge rates (ft3/s) for Quartz Creek from 1988 to 1993, 1996, and 1997.

StreamReach 1988 1989 1990 1991 1992 1993 1996 1997

Site #1 7.62 7.43 5.07 7.02 3.55 11.92 2.83 4.71Site #2 4.97 6.89 7.27 6.37 3.04 12.63 2.71 5.38Site #3 5.42 7.74 6.82 6.93 3.30 12.76 2.68 4.58Site #4 5.31 6.61 5.19 6.37 3.29 11.45 2.66 4.81Site #5 5.71 6.88 4.35 6.60 3.45 12.10 2.41 5.35Site #6 6.60 7.75 6.71 7.29 3.93 12.27 2.66 5.06

Mean 5.94 7.22 5.90 6.76 3.43 12.19 2.66 4.98

28

Figure 7a. Dye release curves for release reach 1 at Quartz Creek restoration site, 1988, 1993,1996, and 1997. Arrow indicates maximum asymptotic concentration for dye release in1997.

0

5

10

15

20

25

DY

E C

ON

C. (

ppb)

0 50 100 150 200 TIME (minutes)

1988

1993

1996

1997

QUARTZ CREEK DYE RELEASESRELEASE REACH #1

29

Figure 7b. Dye release curves for release reach 2 at Quartz Creek restoration site, 1988, 1993,1996, and 1997.

0

5

10

15

20

25

DY

E C

ON

C. (

ppb)

0 50 100 150 200 TIME (minutes)

1988

1993

1996

1997


30

Figure 7c. Dye release curves for release reach 3 at Quartz Creek restoration site, 1988, 1993,1996, and 1997.

0

5

10

15

20

25

30

DY

E C

ON

C. (

ppb)

0 50 100 150 200 TIME (minutes)

1988

1993

1996

1997


31

Figure 7d. Dye release curves for release reach 4 at Quartz Creek restoration site, 1988, 1993,1996, and 1997.

0

5

10

15

20

25

DY

E C

ON

C. (

ppb)

0 50 100 150 200 TIME (minutes)

1988

1993

1996

1997


32

Figure 7e. Dye release curves for release reach 5 at Quartz Creek restoration site, 1988, 1993,1996, and 1997.

0

5

10

15

20

25

30

DY

E C

ON

C. (

ppb)

0 50 100 150 200 TIME (minutes)

1988

1993

1996

1997


33

Figure 7f. Dye release curves for release reach 6 at Quartz Creek restoration site, 1988, 1993,1996, and 1997.

0

5

10

15

20

25

DY

E C

ON

C. (

ppb)

0 50 100 150 200 TIME (minutes)

1988

1993

1996

1997


34

Particulate retention was measured each year by releasing 4,000 ginkgo leaves in the

same reaches as in 1988. Particulate retention generally increased in the six reaches after the

addition of the log accumulations (Table 8). Retention of particulate material is greater when the

value of the retention coefficient (k) increases. Average leaf travel distance (1/k) decreased in all six

reaches between 1988 and 1989 (Table 9). In 1988, the average leaf traveled approximately 83 m

(272 ft); but the travel distances decreased to an average of less than 40 m (131 ft) from 1989 to

1993. In 1996 the average leaf travel distance was 24 m (79 ft) but increased to 33 m (108 ft) in

1997 (Figure 8).

Table 8. Retention coefficient (k) for particulate retention releases at Quartz Creek restorationsite from 1988-1993, 1996, and 1997.

StreamReach 1988 1989 1990 1991 1992 1993 1996 1997


Mean 0.019 0.034 0.024 0.029 0.073 0.030 0.049 0.046

Table 9. Average leaf travel distance (1/k) in meters in reference reaches of Quartz Creekrestoration site from 1988 to 1993, 1996, and 1997.

StreamReach 1988 1989 1990 1991 1992 1993 1996 1997


Mean 82.6 31.9 52.3 38.7 16.9 54.1 23.6 33.1

35

Figure 8. Mean average leaf travel distance (1/k) in meters at Quartz Creek restoration site,1988-1993, 1996, and 1997.

0

20

40

60

80

100

ME

AN

AV

ER

AG

E L

EA

F T

RA

VE

L D

IST

AN

CE

(m

)

1988 1989 1990 1991 1992 1993 1996 1997YEAR

QUARTZ CREEK PARTICULATE RETENTION1988-1997

36

Wood that entered the study site continued to be retained by the log accumulations (Figure 9

and 10). By 1997, log accumulations had retained sufficient amounts of new wood to restore the size

class distribution of wood in the Quartz Creek restoration site to levels observed in streams in old-

growth forests in the basin. Using Mack Creek in the H.J. Andrews Experimental Forest as a reference,

amounts of wood in Quartz Creek in 1997 were similar to the amounts of wood in Mack Creek (Figures

11a-c and 12a-c).

A total of 526 new pieces of wood (mean length = 2.34 m or 7.68 ft; mean diameter = 0.24 m or

0.79 ft) were retained within the restoration site from the February 1996 flood. A total of 93 pieces of

wood left the restoration reach (mean length = 2.29 m or 7.51 ft, mean diameter = 0.24 m or 0.79 ft)

resulting in a net gain of 433 pieces of wood for 1996. In the winter of 1996-1997, with the large

November flood, a total of 427 pieces of wood were deposited (mean length = 2.31 m or 7.60 ft, mean

diameter = 0.26 m or 0.85 ft) within the restoration reach. A total of 379 pieces of wood left the

restoration reach (mean length = 2.37 m or 7.78 ft, mean diameter = 0.24 m or 0.79 ft) resulting in a net

gain of 48 pieces of wood for 1997.

The most efficient structure to date that traps large wood is the non-cabled full jam (Structure

#19) located in the middle of the restoration site. The jam was originally constructed with 20 pieces of

wood. The jam contained 39 pieces in 1989, 97 pieces in 1990, 100 pieces in 1991, 130 pieces in

1992, 163 pieces in 1993, 162 pieces in 1994, 182 pieces in 1995, 280 pieces in 1996, and 311 pieces

of large wood in 1997.

Pieces of wood retained in the restoration reach were more likely to become incorporated into

accumulations rather than to be deposited singly. In 1994, 68 pieces of wood entered the restoration

reach; 50 pieces (74%) were incorporated into accumulations. In 1995, 160 pieces entered the reach

with 121 pieces (76%) occurring in accumulations. In 1996, 526 pieces entered the reach and 455

pieces (87%) occurring stored in accumulations. In 1997, 427 pieces entered the reach and 362 pieces

(85%) were incorporated into accumulations. The volume of wood in 1994 in Quartz Creek was 0.118

m3/m2 (44.83 ft3/ft2) of active stream channel and in 1995, total volume of wood was 0.109 m3/m2 (41.57

ft3/ft2) of active stream channel. In 1996, total volume of wood was 0.126 m3/m2 (48.05 ft3/ft2) of active

37

stream channel, and in 1997 total volume of wood was 0.136 m3/m2 (51.67 ft3/ft2) of active stream

channel.

38

Figure 9. Size class distribution (length) of wood retained in Quartz Creek restoration site,1994-1997.

0

80

160

240

320

400

NU

MB

ER

OF

PIE

CE

S

5 10 15 20 25LENGTH (meters)

19971996

19951994

QUARTZ CREEK RESTORATION SITERETENTION OF WOOD

39

Figure 10. Size class distribution (diameter) of wood retained in Quartz Creek restoration site,1994-1997.

0

80

160

240

320

400

NU

MB

ER

OF

PIE

CE

S

1.0 2.0

DIAMETER (meters)

19971996

19951994

QUARTZ CREEK RESTORATION SITERETENTION OF WOOD

40

Figure 11a. Size class distribution (length) of wood at Mack Creek and Quartz Creek restorationsite before structure installation.

0

1

2

3

4

5

6

NU

MB

ER

OF

LO

GS

/ 10

00 m

(Hun

dred

s)

5 10 15 20 25 30 35 40

LENGTH (m)

PRE-REHAB QUARTZ

MACK CREEK

LARGE WOOD LOADING LEVELSQUARTZ CREEK VS. MACK CREEK

41

Figure 11b. Size class distribution (length) of wood at Mack Creek and Quartz Creek restorationsite immediately after structure installation.

0

1

2

3

4

5

6

NU

MB

ER

OF

LO

GS

/ 10

00 m

(Hun

dred

s)

5 10 15 20 25 30 35 40

LENGTH (m)

QUARTZ CREEKMACK CREEK

LARGE WOOD LOADING LEVELSQUARTZ CREEK (OCT 1988) VS. MACK CREEK

42

Figure 11c. Size class distribution (length) of wood at Mack Creek and Quartz Creek restorationsite, October 1997.

0

2

4

6

8

10

NU

MB

ER

OF

LO

GS

/ 10

00 M

ET

ER

S(H

undr

eds)

5 10 15 20 25 30 35 40

LENGTH (meters)

QUARTZMACK

LARGE WOOD LOADING LEVELSQUARTZ CREEK AND MACK CREEK - 1997

43

Figure 12a. Size class distribution (diameter) of wood at Mack Creek and Quartz Creek restorationsite before structure installation.

0

1

2

3

4

NU

MB

ER

OF

LO

GS

/ 10

00 m

(Hun

dred

s)

0.5 1.0 1.5 2.0 2.5DIAMETER (m)

PRE-REHAB QUARTZ

MACK CREEK

LARGE WOOD LOADING LEVELSQUARTZ CREEK VS. MACK CREEK

44

Figure 12b. Size class distribution (diameter) of wood at Mack Creek and Quartz Creek restorationsite immediately after structure installation.

0

1

2

3

4

NU

MB

ER

OF

LO

GS

/ 10

00 m

(Hun

dred

s)

0.5 1.0 1.5 2.0 2.5

DIAMETER (m)

QUARTZ CREEKMACK CREEK

LARGE WOOD LOADING LEVELSQUARTZ CREEK (OCT 1988) VS. MACK CREEK

45

Figure 12c. Size class distribution (diameter) of wood at Mack Creek and Quartz Creek restorationsite, October 1997.

0

2

4

6

8

10

NU

MB

ER

OF

LO

GS

/ 10

00 m

(Hun

dred

s)

0.5 1.0 1.5 2.0 2.5

DIAMETER (m)

QUARTZMACK

LARGE WOOD LOADING LEVELSQUARTZ CREEK AND MACK CREEK - 1997

46

Change in Channel Morphology

Overall depth and composition of the streambed remained relatively stable, but fine gravel

(smaller than the dominant cobble substrate) was deposited or scoured at several locations.

Various log accumulations, such as upstream "V"s and some lateral deflectors, had deep pools

scoured out below them. Sediments have continued to accumulate above the sill logs in the reach

dominated by bedrock before restoration and above the full channel jam located in the middle of the

restoration reach.

In the 47 channel cross-sections, depth was monitored at 1,818 individual points (Table 10).

In 1996, the maximum scour that occurred at any point was 1.62 m (5.32 ft) at a lateral deflector

and in 1997 the maximum scour of 1.76 m (5.77 ft) occurred at another lateral deflector near the top

of the restoration reach. The greatest amount of deposition in 1996 at any monitored point was 2.12

m (6.96 ft) above a full channel jam and in 1997 the maximum deposition of 2.35 m (7.71 ft)

occurred at the same full channel jam. Maximum net scour in 1996 for an entire transect was 0.61

m (2.00 ft) at a V-deflector, and the greatest net deposition for a transect was 0.70 m (2.30 ft) above

a full channel jam. Maximum net scour in 1997 for an entire transect was 0.42 m (1.38 ft) at a V-

deflector, and the greatest net deposition for a transect was 0.75 m (2.46 ft) above a full channel

jam. In 1996, maximum scour of more than 1.0 m (3.28 ft) occurred at 11 of the 47 total transects,

and maximum deposition of more than 1.0 m occurred at 8 transects. In 1997, maximum scour of

more than 1.0 m occurred at 12 transects, and maximum deposition of more than 1.0 m occurred at

8 transects. More than 10 cm (3.94 in) was scoured (net for entire transect) at 11 transects by

1996, and 12 transects experienced a net deposition of more than 10 cm (3.94 in).

More than 10 cm (3.94 in) was scoured (net for entire transect) at 11 transects by 1997,

and 17 transects experienced a net deposition of more than 10 cm (3.94 in). The average change in

streambed height for all transects by 1996 was a deposition of 0.013 m (0.043 ft). The average

change in streambed height for all transects by 1997 was a deposition of 0.028 m (0.092 ft).

47

Table 10. Scour and deposition of substrates at 47 cross-sections in the restoration reach atQuartz Creek for 1996 and 1997. All values are in meters.

CrossSection

1996Maximum

Scour

1996MaximumDeposition

1996Net

Change

1997Maximum

Scour

1997MaximumDeposition

1997Net

Change n

1-1 -0.82 0.79 -0.23 -0.83 0.80 -0.17 422-1 -0.67 0.24 -0.18 -0.60 0.20 -0.24 382-2 -0.86 0.08 -0.26 -0.79 0.20 -0.27 362-3 -0.62 0.31 -0.09 -0.45 0.35 -0.08 303-1 -1.60 0.00 -0.61 -1.32 0.13 -0.42 435-1 -0.58 0.52 0.22 -0.47 0.82 0.28 415-2 -0.82 0.52 -0.16 -0.68 0.61 -0.07 436-1 -0.95 1.02 -0.04 -0.75 1.10 -0.04 407-1 -1.62 0.32 -0.26 -1.30 0.50 -0.27 438-1 -1.01 0.36 -0.01 -0.39 0.43 0.01 419-1 -1.03 0.36 -0.09 -0.90 0.47 -0.13 3711-1 -0.70 0.57 -0.02 -0.83 0.59 -0.06 3412-1 -0.73 1.60 0.02 -0.71 1.35 0.14 3213-1 -0.97 0.38 0.05 -0.69 0.70 0.16 4515-1 -0.54 0.98 0.20 -0.72 0.86 0.14 4317-1 -0.41 0.65 0.01 -0.61 0.43 -0.01 3018-1 -0.33 0.31 0.02 -0.60 0.62 0.01 4619-1 -0.35 0.95 0.11 -0.53 1.01 0.14 4219-2 -0.75 2.12 0.70 -0.69 2.35 0.46 4319-3 -0.14 1.30 0.58 -0.10 0.62 0.19 4720-1 -0.72 0.68 0.15 -0.57 0.47 0.06 4722-1 -0.19 0.70 0.32 -0.40 0.60 0.17 4323-1 -0.64 0.40 -0.11 -1.18 0.41 -0.16 4824-1 -1.29 0.55 -0.04 -1.47 0.97 0.18 4424-2 -0.96 0.22 -0.14 -0.99 0.52 -0.08 4125-1 -1.50 0.94 0.06 -1.45 0.57 0.05 6025-2 -0.54 1.39 0.38 -0.21 1.76 0.75 5126-1 -0.54 0.25 -0.07 -0.47 0.69 0.04 5129-1 -1.34 0.66 0.05 -1.09 0.80 0.13 2931-1 -0.30 0.78 0.27 -0.74 0.75 0.21 4533-1 -0.95 0.46 -0.17 -0.82 0.56 0.03 3934-1 -0.83 0.71 -0.10 -0.73 1.10 0.07 3535-1 -0.73 0.26 -0.03 -1.00 0.14 -0.31 3337-1 -1.37 0.11 -0.19 -1.65 0.35 -0.21 4438-1 -0.83 0.62 -0.12 -0.99 0.96 -0.19 3339-1 -0.52 0.81 0.01 -0.70 0.48 -0.04 3940-1 -0.96 1.06 -0.10 -1.29 1.00 0.14 3842-1 -0.62 0.40 0.00 -0.23 0.29 0.03 3842-2 -1.09 0.31 -0.02 -0.86 0.61 0.08 4146-1 -0.53 0.35 -0.05 -0.62 0.38 -0.08 1747-1 -0.95 0.23 -0.20 -1.12 0.21 -0.35 3548-1 -0.91 0.97 0.09 -1.02 0.88 0.11 2948-2 -1.49 1.57 0.28 -1.76 2.05 0.48 1449-1 -0.49 1.02 0.09 -0.58 0.81 0.07 2750-1 -0.52 0.53 0.04 -0.56 0.55 0.08 2850-2 -1.26 0.62 0.11 -0.79 0.60 0.12 4950-3 -0.19 0.66 0.16 -0.19 0.61 0.15 24

48

Overall streambed height did not change substantially. However, net changes of more than 10 cm

(3.94 in) occurred at 51% of the transects in 1996, and maximum changes of more than 1.0 m 3.28

ft) were observed at 38% of the monitored transects. Net changes of more than 10 cm (3.94 in)

occurred at 60% of the transects in 1997 with maximum changes of more than 1.0 m (3.28 ft)

observed at 35% of the monitored transects.

Changes in Trout Populations

In both 1996 and 1997 fish abundance and distribution were analyzed in the restoration site.

The 1,500-m (4,922-ft) section immediately above and the 400-m (1,312-ft) section immediately

below the restoration site also were analyzed. Based on snorkel data, average fish densities before

structure installation within the restoration site were 66 fish/100 m (20 fish/100 ft) (Table 11, Figure

13). Fish densities in the restoration reach moderated from 1988 to 1993 with the highest density

occurring in 1991 with 127 fish/100 m (39 fish/100 ft). Fish densities from snorkel data in 1996 were

109 fish/100 m (33 fish/100 ft) and in 1997 fish densities increased to 135 fish/100 m (41 fish/100 ft),

the highest density thus recorded in the restoration site.

Over the first five years since structure installation, fish densities were usually highest in

the 400-m (1312-ft) section below the restoration site. Densities were lowest in the section above

the restoration site for the same time interval. In both 1996 and 1997, fish densities were highest in

the restoration reach, next highest in the reach below the restoration reach, and lowest in the 1,500-

m (4,922-ft) reach above the restoration reach. Fish densities were the highest in pool habitats in

all years for all reaches with the exception of the below restoration reach in 1989 and the above

restoration reach in 1996 (Table 12).

49

Figure 13. Cutthroat and rainbow trout densities based on snorkel counts in the above restorationsite, restoration site, and the below restoration site, 1988-1993, 1996, and 1997.

0

50

100

150

200

250

TR

OU

T/1

00 m

1988 1989 1990 1991 1992 1993 1996 1997YEAR

BELOW RESTORATION RESTORATION ABOVE RESTORATION

QUARTZ CREEKTROUT OBSERVED BY DIVERS

50

Table 11. Number of trout/100 meters of stream (based on snorkel counts) for three sites atQuartz Creek from 1988 to 1993, and 1996 to 1997.

Study Site 1988 1989 1990 1991 1992 1993 1996 1997

BelowRestorationSite

NA 90.2 170.5 208.0 113.9 69.5 71.2 106.8

RestorationSite

66.4 85.7 59.4 126.6 107.0 71.2 109.2 135.4

AboveRestorationSite

NA 63.9 53.2 78.1 81.9 63.1 33.3 72.5

Size frequency distributions were developed from data on visual estimates of fish size

during snorkeling observations. Size frequency of trout in 1993 (Figure 14) resembled those

observed prior to restoration. Larger numbers of fry were observed in 1996 (Figure 15) and fry

numbers increased in 1997 (Figure 16). The largest fish observed by snorkeling was seen in 1997.

Ten fish over 12 inches (30 cm) were observed in the restoration reach in August 1997. Fish of this

size have not been seen in the restoration site in all previous observations.

51

Table 12. Number of cutthroat and rainbow trout/100 m in different habitat types observed bysnorkeling at Quartz Creek from 1988 to 1993, 1996 to 1997.

BELOW RESTORATION REACH

ChannelUnitType

1988 1989 1990 1991 1992 1993 1996 1997

Pool N/A 64.3 294.3 329.8 232.1 144.0 197.1 237.3Glide N/A 261.5 130.4 31.7 83.3 42.7Riffle N/A 113.3 143.6 85.0 74.8 60.6 12.8Rapid N/A 114.3 135.5 238.5 112.6 40.2 62.4 73.0Cascade N/A 69.2 56.3 48.2 71.0 47.1 56.0Side-Channel N/A 4.9Step N/A

RESTORATION REACH

ChannelUnitType

1988 1989 1990 1991 1992 1993 1996 1997

Pool 111.2 177.0 121.4 208.5 157.9 96.9 159.0 185.8Glide 126.5 73.6 40.7 121.4Riffle 75.2 99.0 63.5 167.2 123.9 72.4 124.4 126.0Rapid 68.9 83.0 50.0 135.8 89.5 65.4 89.2 128.1Cascade 59.1 53.0 57.6 98.2 65.1 53.3 72.3 86.1Side-Channel 14.5 20.0 8.6 27.0 21.2 30.5Step 19.0 26.7 57.1 20.0 59.0 22.9

ABOVE RESTORATION REACH

ChannelUnitType

1988 1989 1990 1991 1992 1993 1996 1997

Pool N/A 172.0 111.0 111.6 121.7 127.6 49.0 106.7Glide N/A 33.3 66.7 58.3 37.9Riffle N/A 73.3 135.7 90.5 30.7 56.0 100.0Rapid N/A 89.0 25.6 84.4 82.2 71.4 41.7 79.7Cascade N/A 64.0 41.0 62.8 69.6 51.6 23.7 60.5Side-Channel N/A 10.0 30.0 33.3 13.2Step N/A 22.7 16.8 27.0

52

Figure 14. Size frequency distribution of cutthroat and rainbow trout in Quartz Creek restorationsite based on diver observations, August 1993.

0

1

2

3

4

5

NU

MB

ER

OF

FIS

H(H

undr

eds)

2 3 4 5 6 7 8 9 10 11 12 13 14LENGTH (inches)

QUARTZ CREEK RESTORATION SITESIZE FREQUENCY OF FISH - AUGUST 1993

53


0

1

2

3

4

5

NU

MB

ER

OF

FIS

H(H

undr

eds)

2 3 4 5 6 7 8 9 10 11 12 13 14LENGTH (inches)


54


0

1

2

3

4

5

NU

MB

ER

OF

FIS

H(H

undr

eds)

2 3 4 5 6 7 8 9 10 11 12 13 14LENGTH (inches)


55

The restoration site was electroshocked to validate the accuracy of snorkel counts by

divers in 1990, 1991, 1992, 1993, 1996, and 1997. Pass-removal method was used as the fish

population estimator. The ratio of population estimates from snorkeling to those derived from

electroshocking provided correction factors for each habitat type for each year (Table 13). A

correction factor of <1.0 indicates that divers observed more fish than were estimated by

electroshocking; values >1.0 indicate that electroshocking estimated more fish, and a value of 1.0

indicates that both methods estimated the exact same population. With the exception of cascades

and steps, correction factors for 1996 and 1997 were lower than in 1990.

Table 13. Factors for correcting diver counts to fish populations (as determined by electrofishingestimates) for habitat types in Quartz Creek for 1990-1993, 1996, 1997.

Unit Type 1990 1991 1992 1993 1996 1997

Pool 3.1 1.3 1.7 1.9 1.9 1.6Glide 2.3 2.7 1.9 1.9Riffle 3.4 1.6 1.6 2.2 2.0 2.1Rapid 3.2 2.6 1.8 1.8 1.9 2.1Cascade 3.5 4.7 3.2 2.8 3.6 2.4Side-Channel 10.0 2.0 3.5 3.0Step 2.5 2.5 5.7 3.3 3.0

Total fish populations for the entire restoration reach were estimated by applying the

correction factors to snorkel counts obtained in the three study sites. In 1991, trout populations

were highest in the section immediately below the restoration site, and populations within the

restoration site were only slightly greater than those upstream (Table 14, Figure 17). In 1992, trout

populations declined in all three sites, especially in the site below the restoration reach. In 1993,

trout populations decreased at all three sites but the decline in the restoration site was

proportionately less than in adjacent reaches (6% in the restoration reach versus 20% above and

26% below). In 1996, large increases in trout populations were observed in the restoration site,

56

slight increases in the reach below the restoration site, and decreases in the section immediately

above the restoration site. In 1997, trout populations increased in all three sites with the largest

increase occurring in the section immediately above the restoration reach. The restoration reach

had the highest density of trout in 1992, 1993, 1996, and 1997.

Table 14. Number of fish/100 meters corrected for diver observation efficiencies at Quartz Creekfor 1990, 1991, 1992, 1993, 1996, and 1997.

Study Reach 1990 1991 1992 1993 1996 1997

Below Restoration 519.5 489.8 186.8 149.7 153.9 209.9Restoration Site 203.9 277.1 205.7 192.6 282.8 283.2Above Restoration 177.7 252.4 203.2 149.5 91.0 156.7

The density of fish increased in all habitat types in both 1996 and 1997 from 1993 densities

with the exception of side-channels and steps (Table 15). Pool habitat held the highest density fish

with 330 fish/100 m (101 fish/100 ft) of pool habitat in 1996 and 264 fish/100 m (80 fish/100 ft) in

1997. The next highest density of fish was in riffle habitat, followed by rapids.

Table 15. Numbers of fish/100 meters of each habitat type in Quartz Creek restoration sitecorrected from electroshocking data for 1990, 1991, 1992, 1993, 1996, and 1997.

Habitat Type 1990 1991 1992 1993 1996 1997

Pool 251.0 244.1 300.8 194.9 329.9 263.5Glide 223.5 171.8 110.5 231.2Riffle 213.0 225.4 209.1 138.7 266.3 235.9Rapid 167.0 244.2 184.4 121.6 215.2 175.1Cascade 173.0 246.9 203.2 167.5 194.0 152.0Side-Channel 69.0 72.4 40.0 145.9 82.3 106.8Step 106.0 142.9 125.0 298.0 109.0 157.0

57

Figure 17. Corrected diver estimates of trout densities at Quartz Creek in the above restorationsite, restoration site, and below restoration site, 1988-1993.

*Values for 1988 and 1989 restoration site derived from applying mean correction values obtained in 1990-1993.

0

1.1

2.2

3.3

4.4

5.5

TR

OU

T /

100

m(H

undr

eds)

1988 1989 1990 1991 1992 1993 1996 1997YEAR

BELOW RESTORATION RESTORATION ABOVE RESTORATION

QUARTZ CREEKCORRECTED DIVER ESTIMATES

58

The narrow width of side-channels can make the density of fish appear to be low when

using number of fish/100 m. Density of fish expressed as number/m2 of wetted channel can be very

high in narrow habitats such as side-channels. Side-channels held the highest density of fish in

1991 with 0.38 fish/m2 (4.09 fish/ft2); 0.76 fish/m

2 (8.16 fish/ft2) in 1993; and 0.43 fish/m

2 (4.67

fish/ft2) in 1997.

Table 16. Numbers of fish/m2 of each habitat type in Quartz Creek restoration site corrected from

electroshocking data for 1990, 1991, 1992, 1993, 1996, and 1997.

Habitat Type 1990 1991 1992 1993 1996 1997

Pool 0.443 0.376 0.412 0.244 0.446 0.332Glide 0.304 0.243 0.134 0.274Riffle 0.318 0.316 0.240 0.152 0.353 0.298Rapid 0.161 0.297 0.260 0.148 0.278 0.224Cascade 0.195 0.326 0.288 0.161 0.220 0.165Side-Channel 0.266 0.380 0.117 0.758 0.235 0.434Step 0.186 0.169 0.284 0.191 0.280

59

DISCUSSION

Performance of Log Structures

Time-lapse photography of wood accumulations during high winter flows on Mack Creek

(H.J. Andrews Experimental Forest) shows that natural wood dams rise and fall with changing

stream discharge. During high discharges, these log accumulations float up and the majority of

water passes underneath. On the falling limb of the hydrograph, the pieces fall back into place, and

it is often difficult to discern any changes. Logs inundated by higher flows naturally tend to float,

and any logs that are artificially bound to the streambed are subjected to high flotation forces.

Structures that are not cabled or partially cabled can move and adjust to the directions and intensity

of the force of flowing water.

The upstream-V log accumulations installed at Quartz Creek effectively created a step-pool

profile in long cascades, but they had to take the full force of high winter discharges because of

their design. Five of the 21 log accumulations that moved were of this type. The “V” configuration

focused the force of the flow to the middle of the channel and quickly scoured sediments. In most

cases, this scour cuts back under the structure and caused upstream sediment deposits to give

way under the structure and changed the arrangement of wood in the accumulation. In one

instance a secondary or flood channel formed during high flows around an upstream "V". Flows

down these secondary channel take some pressure off log accumulations in the main channel

during high water events. The structures that the highest tendency to move or shift were the

upstream-V accumulations (5 of 6), followed by full jams (2 of 3), sill logs (1 of 2), and cover logs (4

of 8).

Large amounts of spawning gravel continue to accumulate in association with installed

structures. The upstream-V log accumulations had large amounts of potential spawning gravel

deposited below them on the sides of the stream during winter discharges (Figure 18a-d). Directly

below the tip of the upstream-V log accumulations, deep plunge pools were scoured. The full

channel jam in the middle of the restoration reach had over 2 m (6.56 ft) of sand and gravel

60

Figure 18 a - b. Top: Site of proposed upstream V structure at Quartz Creek, July 1988.Bottom: Same site with upstream V structure installed, October 1988.

61

Figure 18 c - d. Top: Upstream V structure at Quartz Creek, September 1993. Bottom:Upstream V structure at Quartz Creek, September 1997.

62

deposited directly upstream of the jam. Spawning gravel was deposited for a distance of 20 m (66

ft) upstream of this jam. Lateral deflectors had spawning gravel deposited below them for various

distances.

The retention of large amounts of wood by the non-cabled full channel jam (Structure #19) in

the middle of the restoration site continues to be encouraging (Figure 19a-f). The number of logs

increased more than fifteen-fold in nine years. In appropriate reach locations, these types of jams

provide more natural habitat than heavily cabled "trash racks" and still effectively capture floating

wood during high flows. The non-cabled full channel jam grew from 20 logs to 311 logs in nine

years, while the trash rack of nine logs accumulated 38 logs. Accumulations of a few large logs will

not capture wood from transport as effectively and will not create complex habitats as quickly as

more complex accumulation of logs.

The sill log structure (Structure #11) has preformed well in trapping sediment on top of the

bedrock substrate that was present at this location in 1988 (Figure 20a-b). A large deep pool has

been formed behind this sill log structure. In 1988, a total of three trout were present at this

bedrock dominated site but the trout density increased at this site to 67 trout by 1997.

The maximum distance that a piece of wood from the Quartz Creek restoration site has

moved is at least 40 km (25 miles). The Leaburg hatchery manager on the McKenzie River found a

tagged piece of wood (#1013) during a class field trip he was conducting in the summer of 1996.

This log #1013 was 1.20 m (3.94 ft) long and 0.15 m (0.49 ft) in diameter and was deposited in an

alder dominated riparian area directly below Leaburg dam on the McKenzie River. Although this is

the longest documented movement of any piece of tagged wood from the Quartz Creek restoration

project, other pieces may have moved greater distances.

There is evidence that some pieces of wood from the Quartz Creek restoration site have

been removed from the stream area. Aluminum tags used for tagging each log in Quartz Creek

were found in blackened campfire pits along the Quartz Creek road. One log on the “trash-rack”

was removed and presumably used for firewood as well.

63

Figure 19 a - b. Top: Looking downstream at full channel jam (Structure 19) at Quartz Creek,October, 1988. Bottom: Full channel jam (Structure 19) at Quartz Creek, October1989.

64

Figure 19 c - d. Top: Full channel jam (Structure 19) at Quartz Creek, October 1990.Bottom: Full channel jam (Structure 19) at Quartz Creek, October 1992.

65

Figure 19 e - f. Top: Full channel jam (Structure 19) at Quartz Creek, October 1996.Bottom: Full channel jam (Structure 19) at Quartz Creek, October 1997.

66

Figure 20 a - b. Top: Proposed site for sill log structure at Quartz Creek, July 1988.Bottom: Same site with sill log structure installed, September 1997. Upstream silllog was partially moved by flood discharges in 1993.

67

Evaluation of Log Accumulations

Twenty-two of the 48 instream log accumulations have moved more than 1 m (3.28 ft) since

installation in 1988, but most of those moved logs are still performing good instream functions.

Fourteen of the 22 log accumulations moved less than 10 m (32.8 ft) and the few that moved further

were eventually deposited on or within existing log accumulations. Based on simple comparison,

we observed no major differences in the permanence of log structures regardless of the degree of

cabling.

Incorporation of root-wads with no attached bole exhibited mixed results. Eight root-wads

were placed singly along the sides of the stream channel. Six of these single root-wads (75%) have

moved since installation in 1988. Seventeen root-wads were incorporated within log accumulations

with three (18%) having moved since installation. Root-wads incorporated within structures, such

as in the middle of lateral deflectors, provide more complex lateral habitat that potentially serves as

critical winter refuge for fish and salamanders.

For those structures that were fully cabled or partially cabled and still "moved", inadequate

size of attached boulders was one of the factors for movement. Because all boulder material was

obtained from the direct site of structure installation, large boulders were not accessible in some

cases and moderate sized boulders had to be used. A number of the structures that did move

downstream still have boulders attached by cable, which are hanging in unaesthetic positions.

Most of the movement of structures occurred soon after installation. Since the summer of

1990, few of the installed structures have moved or shifted. The two large flood events of 1996

caused one additional accumulation to move. This possibly suggests that as time progresses after

installation, structures become somewhat more stable. In the Quartz Creek project, flows were low

during the first 5-yr period with high flow events equal to or less than a 5-yr-recurrence-interval. In

1996 the recurrence interval for local streams similar in size to Quartz Creek was a 30-100+yr-

recurrence-interval flood. The continued functioning of the accumulations at Quartz Creek after two

such large flood events is evidence of their physical stability.

68

We would like to reemphasize that movement alone should not be considered a failure of a

specific log accumulation or the project as a whole. If the wood is moved by the stream and used

effectively to create functional habitats in the stream, the intent of introducing wood into the channel

is met. In many respects, effective redistribution of wood by the stream is a more desirable

ecological response than remaining in an original fixed position.

Ecological Responses

Hydraulic and particulate retention are extremely important in stream ecosystems because

these processes increase time available for aquatic organisms to process organic matter such as

detritus and leaves which enter from the riparian zone or sources upstream. These aquatic

invertebrates in turn are a major source of food for fish populations.

Hydraulic retention was poor in the 1,100-m (3,281-ft) reach of Quartz Creek before log

introduction. This can be largely attributed to the constrained configuration of the stream channel,

relatively low amounts of large wood, low number of deep pools, and the lack of extensive

backwaters.

Particulate retention increased with the addition of the log accumulations (see Table 9).

Large increases in particulate retention continue to occur in the bedrock chute area where sill logs

were installed. The average leaf travel distance in this bedrock chute area in 1988 was 29.4 m (96.5

ft) and in 1996 was 10.8 m (35.4 ft) and in 1997 was 8.0 m (26.2 ft). The average leaf travel distance

for the six reaches where particulate retention studies were conducted has improved from 82.6 m

(271.0 ft) in 1988 before structure installation to 23.6 m (77.4 ft) in 1996 and 33.1 m (108.6 ft) in

1997. We anticipate that particulate retention will continue to increase as smaller pieces of

material become entrained and incorporated into the log accumulations.

Original large wood, installed structures, and retained wood within the restoration reach

generally moved only short distances during high winter discharges. In 1989, 33 (8.6%) of the 385

total pieces of wood in the restoration reach moved a distance of 5 m (16.4 ft) or greater. In 1990,

50 (10.4%) of the 479 total pieces moved, and in 1991, 32 (3.7%) of the 857 pieces moved. In

69

1992, 53 (5.6%) of the 947 total pieces moved, and in 1993, 46 (4.8%) of the 968 total pieces

moved a distance of 5 m (16.4 ft) or greater. In 1994, 49 (3.1%) of the 1,596 pieces moved, and in

1995, 65 (3.9%) of the 1,652 total pieces moved. In 1996, (8.4%) of the 1,757 total pieces moved

and in 1997, 195 (8.9%) of the 2,190 total pieces moved a distance of 5 m (16.4 ft) or greater.

In contrast, movement of natural wood at Mack Creek averages around one percent

annually for flows of less than 10-yr recurrence intervals. Rates of movement at Quartz Creek

indicate that the wood in the restoration reach increased in stability with time after structure

installation. The size of the pieces that moved were usually small (1.0 – 5.0 m or 3.28-16.4 ft long),

and the pieces moved relatively short distances. Most of the moving pieces eventually were

incorporated into structures downstream. Flood discharges in 1996 doubled the rate of log

movement at Quartz Creek.

Short-term barriers to fish passage may occur in restoration projects where accumulations

cause elevational breaks that are higher than the jumping ability of resident fish species.

Seasonality of fish movement must be considered in assessing barriers. The sill logs (Structure

#11) placed in the bedrock chute area at the 200 m (656 ft) position on baseline maps is of some

concern for movement of fish during low flow conditions. The substrate at the lower end of this

structure is mostly bedrock with very little depth of water for fish to jump from. During base winter

flows this structure posses no barrier to movement. High channel roughness throughout the reach

provides numerous opportunities for both upstream and downstream access for fish.

Snorkeling surveys in 1996 and 1997 (with corrections based on electroshocking

calibration) showed a 47% increase in fish numbers in 1996 in the restoration reach and relatively

no change in 1997. Estimates of trout populations for the 9-yr period after restoration averaged 21%

higher than the population observed in 1988.

The increase in the fish population could be attributed to the installed structures, which

allowed for winter refuge even during the large flood events of 1996. The increase in side-channel

habitat may have allowed for better survival during both low and high discharges. Deposition of large

amounts of spawning gravel behind numerous log accumulations may have allowed for higher

70

spawning success. Increased retention of organic matter may have increased the invertebrate

populations and resulted in more drift organisms for the fish community to consume.

The trout populations in the above restoration reach declined by 39% between 1993 and

1996. In all years surveyed, this reach above the restoration site had the lowest trout population of

the three reaches studied. Although trout populations increased in 1997 in both the above and

below restoration sites, the highest density of trout in 1997 was still in the restoration reach. The

trout populations from 1990 to 1997 varied considerably in the above and below reaches while they

remained relatively consistent in the restoration reach.

Snorkeling and shocking surveys were also performed for the same years at an old-growth

section of Mack Creek and at a control section at North Fork Quartz Creek (a deciduous canopied

third-order stream near the H. J. Andrews Experimental Forest approximately 19 km (12 miles)

north of the restoration site on Quartz Creek). Both of these streams contain relatively undisturbed

populations of cutthroat trout. Mack Creek and N. F. Quartz Creek seem to have the largest yearly

fluctuation in trout populations of the three streams (Fig. 21). Trout populations were low at both

Mack Creek and N.F. Quartz Creek in 1988 and 1989 but were stable at the Quartz restoration site

for the same time period. Large populations of trout were observed in both Quartz Creeks in 1991.

In 1996 and 1997, trout populations increased in Mack Creek and Quartz restoration site

but decreased in N. F. Quartz Creek. The Mack Creek fish sampling site is at 793 m (2,600 ft) in

elevation while both Quartz Creeks are at the lower elevation of 610 m (2,000 ft). As previously

discussed, watershed studies at the H.J. Andrews Experimental Forest indicate that streams in

higher elevations had smaller discharges during the floods of 1996. This may be a factor for the

increase of trout numbers at Mack Creek in 1996 and 1997. Trout numbers declined at the lower

elevation N.F. Quartz Creek but increased at Quartz restoration site for the same time period. In all

7 years surveyed, the trout population at Quartz restoration site was higher than the other two

streams. Interannual variation in resident trout populations in the upper McKenzie River basin are

approximately +/- 25% of mean abundance. Changes in trout numbers in Quartz Creek are well

within that range of variability.

71

Figure 21. Trout densities at Quartz Creek restoration site, Mack Creek, and N. F. Quartz Creek,1988-1997.

0

80

160

240

320

400

TRO

UT

/ 100

m

1988 1989 1990 1991 1992 1993 1994 1995 1996 1997

YEAR

N.F. QUARTZ CRMACK CR

QUARTZ CR RESTORE

THREE STREAM COMPARISON# TROUT/100m (SHOCKING & SNORKEL DATA)

72

SUMMARY

This report is the culmination of the 1996 and 1997 monitoring at Quartz Creek. The

Department of Fisheries and Wildlife (Stream Team) at Oregon State University (104 Nash Hall,

Corvallis, Oregon, 97331) is the repository of all field data, photographs from photopoints, and time-

lapse movie film.

The Aquatic Ecosystem Restoration Project resulted in several major physical and

biological changes in Quartz Creek in a relatively short period of time. The rapid recruitment of

wood by the installed accumulations in Quartz Creek was faster than we expected. In nine years,

the restoration reach of Quartz Creek has nearly developed the amounts and sizes of wood that

would be expected in a similarly sized stream flowing through an old-growth forest in this basin.

Over the short term, the large wood installed by the project has effectively retained the smaller size

classes in transport. Channel scour or deposition has been observed in association with most of

the accumulation. Almost half the accumulations have shifted a meter or more, but little of the

wood has left the restoration reach. Only twenty-one of the 186 pieces (11.3%) of wood originally

installed have been transported out of the restoration reach as of 1993. Most of the transported

pieces have been relatively small in size with a mean length of 4.6 m (15.1 ft) and a mean diameter

of 0.57 m (1.87 ft). Two additional installed pieces of wood have left the restoration reach as a

result of the two floods in 1996.

Retention of potential food resources (as measured by leaves) increased approximately 3.5

times in 1996 compared to pre-introduction levels. This increase in retention of food resources

potentially could increase invertebrate populations, which in turn are food resources for the fish

community.

Trout populations within the restoration reach have increased, particularly in 1996 after the

February flood. Log accumulations may have provided the essential winter hiding refuge necessary

for fish to survive such a large flood event. Side-channels and pools increased after implementing

the restoration plan, and these habitat types support higher densities of fish than rapids and riffles.

73

Monitoring will continue at Quartz Creek as part of the continuing effort of the Long Term

Ecological Research Program at Oregon State University but at a severely reduced level of

intensity. Habitat mapping within the restoration site will continue each year to monitor changes in

the channel structure. Monitoring retention of wood also will continue with the mapping, measuring,

and tagging of all new wood within the restoration site. Three time-lapse camera systems will

continue to be maintained to visually monitor any changes to the structures. Funds are not

available to continue the high level of monitoring of the project every year, but detailed monitoring

will be again conducted in 2008, twenty years after project initiation. Additional monitoring at the

fifteen year period or after major flood events would be advisable if funding was available.

The Aquatic Ecosystem Restoration Project has accomplished many of the physical and

biological objectives since 1988. Short-term changes in wood and habitat created by the project are

favorable. Rapid retention of new wood by the structures has been particular encouraging. The

long-term effectiveness of the project remains to be determined.

SUGGESTIONS

The Willamette National Forest asked the authors of this report to give suggestions on their

perspectives of the project. The placement of logs at the junction of temporary roads used in

structure installation was not necessary. In stream systems such as Quartz Creek with relatively

large sediment particle size and a stable floodplain, road logs are not necessary. These road logs

acted to disconnect the stream from its floodplain. Placement of these road logs may be

necessary however in other systems with finer particle sizes and unstable floodplains, such as in

the coastal areas of Oregon.

This project was an experiment to study the physical and biological affects associated with

the installation of wood and boulder structures and was not a comprehensive effort in restoring an

entire watershed. While the project was able to partially restore a kilometer reach of Quartz Creek

74

by re-establishing normal levels of large wood, the remaining 23 kilometers of Quartz Creek

remaining in need of restoration. Restoration efforts have been placed on a very small percent of the

basin. The watershed contains large areas of both public and private land and restoration efforts will

be necessary on both before the watershed can be successfully restored.

75

LITERATURE CITED

Armour, C.L., K.P. Burnham, and W.S. Platts. 1983. Field methods and statisticalanalyses for monitoring small salmonid streams. U.S. Fish & WildlifeService.

Dryness,T., F. Swanson, G. Grant, S. Gregory, J. Jones, K. Kurosawa, A. Levno, D.Henshaw, H. Hammond. Flood of February, 1996 in the H.J. AndrewsExperimental Forest. http://www.fsl.orst.edu/lter/pubs/spclrpts/flood/floodrpt.html#INTRO (24 February 1998).

Hankin, D.G., and G.H. Reeves. 1989. Estimating total fish abundance and totalhabitat area in small streams based on visual estimation methods. Can. J.Fish Aquat. Sci. 45:834-844.

Kilpatrick, F.A., W.W. Sayre, and E.V. Richardson. 1967. Flow measurements withfluorescent tracers (a discussion). J. Hydraul. Div. Amer. Soc. Civil Eng. 93:298-308.

Speaker, R. 1985. Distribution and retention of particulate organic matter instreams in the Cascade Mountains of Oregon. M.S. Thesis, Oregon StateUniversity, Corvallis, 145 p.

Strahler, A.N. 1957. Quantitative analysis of watershed geomorphology. Am.Geophys. Union Trans. (EOS) 38:913-920.

Taylor, George. H. The Great Flood of 1996. http://www.ocs.orst.edu/gifs/flood_map.GIF (24 February 1998).

Documents

AQUATIC ECOSYSTEM RESTORATION PROJECTandrewsforest.oregonstate.edu/research/component/... · land (Rosboro Lumber Company) while the upper reaches of the watershed are public lands