BLM LIBRARY

88058687

iviuiuiuiiug on cam Channels
and Riparian Vegetation-
Multiple Indicators

Idaho Technical Bulletin 2007-01
April 2007

Timothy A. Burton
Ervin R. Cowley
Steven J. Smith

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Monitoring Stream Channels and
Riparian Vegetation - Multiple Indicators

Version 3.0 -2007

Timothy A. Burton, Ervin R. Cowley, and Steven J. Smith

TABLE OF CONTENTS

INTRODUCTION 1

Selecting Designated Monitoring Areas (DMAS) 4

Selecting Appropriate Indicators 5

Establishing the Line Transect 7

Skills, Training, Collection, Time, and Equipment 7

Systematic Procedure 8

A. Procedure: Locating the greenline (Modified from Winward 2000) 10

B. Procedure: Measuring and Recording Streambank and Vegetation
Indicators 13

1. Greenline Vegetation Composition 14

2. Streambank Alteration 16

3. Streambank Stability and Cover 19

4. Residual Vegetation Measurement (Stubble Height) 21

5. Woody Species Regeneration 22

6. Woody Species Use (Modified Landscape Appearance Method) 25

C. In-Channel Indicators 27

7. Greenline-to-Greenline Channel Width (GGW) __ 27

8. Maximum Water Depth as measured at the deepest point in the stream
(Thalweg depth): 30

9. Water width: 31

10. Substrate composition: 31

DATA INTERPRETATION 32

1. Successional Status - Ecological Status 33

2. Vegetation Erosion Resistance Rating (Greenline Stability Rating) 34

3. Wetland Rating 34

4. Streambank Stability (percent streambanks stable and percent streambanks
covered) 36

5. Residual Vegetation (Mean and Median Stubble Height) 37

6. Woody Species Regeneration 38

7. Greenline-to-Greenline Channel Width (GGW) 39

8. Woody Species Use 39

9. Thalweg Depth Variation Index 39

10. Water Width-Maximum Depth Ratio 40

11. Percent Substrate Fines (<6mm) 40

12. Median Substrate Particle Size Diameter (D50) 40

13. Discharge 41

14. Roughness coefficient 41

15. Pool Quality Index 41

16. Photographs 42

17. PFC Calibration 42

18. Winward Greenline Calibration (Winward 2000) 43

REFERENCES 44

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INTRODUCTION

The purpose of Monitoring Stream Channels and Riparian Vegetation —
Multiple Indicators (or Multiple Indictor Method - MIM) is to provide an
efficient and effective approach to monitoring streams and riparian
vegetation. This protocol is designed to meet the recommendations in the
University of Idaho Stubble Height Study Report to integrate annual grazing
use and long-term trend indicators. The monitoring procedures described in
this document can be used to evaluate current livestock grazing
management practices, i.e., timing, frequency, and duration of grazing, and
to determine whether the vegetation, stream channels, and streambanks are
responding to livestock grazing management as anticipated. While the
MIM protocol was initiated as a result of grazing management concerns, the
long-term monitoring techniques described herein will provide useful data
regarding the general condition and trend of streams and riparian vegetation
regardless the kind of management activities occurring on the site.

Adaptive livestock grazing management, as described by the University of
Idaho Stubble Height Study Team (2004) requires developing specific
riparian and stream channel management objectives, a grazing management
plan designed to meet those objectives, and long-term monitoring criteria
used to evaluate success. Annual monitoring of livestock use helps
determine if grazing management is being implemented as planned and if
the plan is helping to achieve resource objectives. This includes
monitoring annual trigger and endpoint indicators, assessing the effects of
these impacts on resource objectives, and then evaluating whether or not the
grazing plan needs to be adjusted.

Trigger indicators of livestock use (e.g., residual stubble height, woody
species use, streambank alteration, use compliance, changes in species
preference) are monitored to determine when to move the animals to
another grazing area. Endpoint indicators of livestock use (residual stubble
height, woody species use, streambank alteration) are monitored after the
end of the growing and grazing season to determine if the use or disturbance
was within allowable levels. Endpoint monitoring data provides information
necessary to evaluate the effect of grazing on long-term trend.

Single indicators of condition or trend are usually not adequate to make
good decisions (University of Idaho Stubble Height Study Team 2004).
Data on the condition and trend of vegetation and streambanks, combined
with the knowledge of current management practices helps establish "cause-
and-effect" relationships important for making well-informed decisions.

Appropriate vegetative cover, stream channel geometry (width and depth),
and streambank stability is essential for achieving good water quality and

aquatic habitat. Monitoring the current year's grazing impacts (short-term
monitoring of livestock use) along with long-term indicators of riparian
vegetation, streambank, and stream channel conditions at the same location,
provides the basis for making grazing adjustments needed to achieve
desired conditions. Livestock use indicators (e.g., stubble height,
streambank alteration, and woody species use) alone do not provide the data
needed to determine condition and trend.

Previous approaches have been relatively inefficient partly due to the fact
that separate protocols were required for each indicator. This protocol
combines observations of up to ten indicators along the same transect, using
simple refinements of existing protocols. Since travel time to field sites
represents a considerable time commitment, collecting multiple indicators at
one location, using one protocol, is more efficient.

A critical component of understanding and detecting trends through time,
despite natural variability in channel and riparian condition, is limiting the
selection of monitoring indicators to those that are sensitive to disturbance
and that can be measured objectively, precisely, and efficiently. This
monitoring protocol is designed to maximize objectivity by emphasizing
precision and accuracy. This is accomplished by selecting indicators that
are measurable; by locating observation points along the greenline
according to strictly defined rules; and by making class determinations
using systematic procedures and classification keys.

This monitoring protocol addresses ten procedures that can be used to
monitor streams and associated riparian vegetation. Seven procedures
provide indicators for long-term (trend) monitoring:

1. Modified greenline (Winward 2000),

2. Modified woody species regeneration (Winward 2000),

3. Streambank stability (Henderson et al. 2003),

4. Greenline-to-greenline channel width (Burton et al. 2006)

5. Maximum water depth (Henderson et al. 2003),

6. Water width (Henderson et al. 2003),

7. Substrate composition (Bunte and Apt 2002)

These indicators provide data to assess the current condition and trend of
the streambanks, channels, and vegetation. They help determine if local
livestock grazing management strategies and actions are achieving the long-
term goals and objectives for stream riparian vegetation and aquatic
resources. Monitoring procedures for vegetation include modifications of
greenline vegetation composition and woody species regeneration described
by Winward (2000) and Coles-Ritchie et «/.(2003). Streambank stability is
a modification of the PIBO method described by Henderson et al. (2003).
The authors devised greenline-to-greenline width measurement. Stream

thalweg depth, width, and substrate parameters are measured at transects
according to the PIBO method (Henderson et al. 2003).

Permanent photo points provide a long-term visual record of streambank
and riparian conditions and trend. The protocol described in this document
recommends a minimum number of photographs needed for an acceptable
visual record. More detailed photos may be added if required to document
or answer management questions.

Three indicators provide data to help determine whether current season's
livestock grazing is meeting the criteria established to make progress
toward meeting resource objectives. The protocol includes:

1 . Modified landscape appearance for livestock use on woody
plants [formerly the Key Forage Plant Method] (Interagency
Technical References, 1996),

2. Modified residual vegetation (stubble height) Interagency
Technical Reference (1996) and Challis Resource Area (1999), and

3. Streambank alteration (Cowley 2004).

These monitoring procedures facilitate adaptive management by providing
data needed to refine and make annual changes to livestock grazing
management practices in order to meet long-term management objectives.

Procedures were modified to allow the use of a prescribed plot size, which
will be described later, to allow collecting data from all ten monitoring
protocols in a single pass. Specific rules were developed to facilitate the
use of the plot and to maintain consistency, precision, and accuracy of the
data.

In addition to documenting stream conditions and trend, photos should also
be used to document annual grazing use at the monitoring site. This helps
those interpreting the data at a later time to visualize the results of the data
being analyzed.

Methods described in this protocol were selected because of their direct
relationships to livestock management on streambanks and riparian
vegetation. The amount of residual vegetation (stubble height) left at the
end of the season has a direct relationship to the long-term productivity of
herbaceous riparian plants and ultimately on the composition of vegetation
along the greenline (measured using the greenline vegetation composition
procedure). Streambank alteration evaluates the amount of disturbance
caused by livestock that may have a direct relationship to streambank
stability and the recovery of vegetation along the greenline. Shrub use
along the greenline, as measured by woody species use, directly affects the

long-term productivity of woody plants on the streambanks. For example,
research has shown that heavy to extreme use by grazing animals every year
is detrimental to plant health, while light to moderate use maintains overall
plant health (Thorne et al. 2005). In addition, continued heavy to extreme
use of woody species can limit the plant's ability to regenerate. Greenline-
to-greenline width is the non-vegetated width of the stream channel
between the greenlines on each side of the stream. As stream channels
recover from disturbance, the width between greenlines often decreases.
This is because channel narrowing usually reflects increasing streambank
stability and vegetative encroachment.

Selecting Designated Monitoring Areas (DMAS)

A designated monitoring area (DMA) is the location, or stream reach, where
monitoring occurs. DMAs should be selected to represent a riparian
complex as defined by Winward (2000), and should be located in areas
representative of grazing use (or other use) specific to the riparian area
being assessed. DMAs should not reflect an average amount of use in all
riparian areas of the stream reaches in the pasture. Instead, they should
reflect typical livestock use where they impact streambanks and riparian
vegetation. DMAs may be selected where livestock use exceeds the
apparent average use of riparian areas in the pasture. For example, the
assumption is made that since the DMA reflects higher use than other
stream segments within the pasture and is meeting resource objectives, then
the rest of the stream in that pasture is also meeting objectives. While the
term "DMA" was initially established for grazing management applications,
DMAs may be located in areas to monitor recreation impacts, the effects of
roads, and other activities. A DMA may also be selected to serve as a
reference reach to help determine the potential and capability of a stream.

The following criteria are used to select DMAs (see Appendix A):

• DMAs represent riparian areas used by livestock (or other use). Select the
site based on the premise that if proper management occurs on the DMA,
the remainder of the riparian areas within a pasture or use area will also be
managed within requirements.

• Select sites that are representative of use, not an average for the stream
within the pasture or allotment. For example, if livestock use one-half
mile of a stream reach in the pasture and one mile is not used because it is
protected by vegetation, rock, debris, or topography, the DMA location
should represent the stream reach that livestock actually use.

• Monitoring sites should have the potential to respond to and demonstrate
measurable trends in condition resulting from changes in grazing

management. Livestock trails associated with livestock use of the riparian
area may be included in the DMA.

• Avoid selecting sites where vegetation is not a controlling factor, such as
cobble, boulder, and bedrock-armored channels.

• Do not place DMAs in streams over four percent gradient unless they have
distinctly developed flood plains and vegetation heavily influences
channel stability.

• Avoid putting DMAs at water gaps or locations intended for livestock
concentration, or areas where riparian vegetation and streambank impacts
are the result of site specific conditions (such as along fences where
livestock grazing use is not representative of the riparian area). These
local areas of concentration may be monitored to address highly localized
issues, but they should not be considered as representative of livestock
grazing management over the entire riparian area within the grazing unit,
and are therefore not generally chosen as DMAs.

Selecting Appropriate Indicators

After the DMA has been located, it is important to select the appropriate
objectives and indicators for the site and management strategy. Site
potential or capability (vegetation and stream type), management objectives
for vegetation, streambanks, and stream channel, timing, duration, and
frequency of the grazing strategy, and monitoring questions must all be
considered when selecting the indicators that are to be monitored (see
Appendix B).

• General goals and/or broad objectives are usually established in the
agency land use plans, i.e., forest resource plans, resource management
plans (RMP), management framework plans (MFP), allotment
management plans, ranch plans, and other management plans.

• An understanding of the basic geomorphic processes and vegetation
responses are important to interpreting the potential of the stream, and
therefore the desired future condition. Streams with substrate and banks
dominated by gravel, with limited fine sediment loads, are likely to be
dominated by woody vegetation. In such instances, herbaceous vegetation
is likely to be slow to develop, as these types require more fine soils to
become established.

• Riparian Management Objectives should reflect the attainable condition.
For example, incised stream channels may not likely fill with sediment
under current climatic regimes. Miller et al. (2004) states "The dominant
process operating within the upland stream systems today is channel
incision." Therefore, it is likely that incised channels will widen, develop
a new floodplain, and stabilize the channel near the current elevation. In

some rare instances, however, incised ehannels will fill with sediment and
move toward a stable state at the elevation of the channel prior to incision.

• Appendix A, page A-5: Key to Grcenline Capability Groups (Winward
2000) describes general vegetation capabilities. When better information
is not available, this may be used to help develop objectives for the
amount and kind of vegetation necessary to achieve proper functioning
condition.

Appropriate indicators may change over time. For example, the DMA is
dominated by graminoid species with no willows or woody species present.
Since there are no woody species found along the transect, woody species
regeneration and woody species use were not selected as indicators.
However, there is a potential for willows and other woody species on most
streams with a gradient of 0.05 percent or more and periodic over bank
flooding with deposition (Winward 2000). Woody species reproduction is
episodic, as they require a seed source, freshly deposited soil, and moisture
for a sufficient time to develop a root system adequate to support the
seedling until it is established. When these conditions occur, it is
appropriate to add woody species regeneration and woody species use to
track the changes.

• Pastures that are in a rest period may only need validation that livestock
use has not occurred. Stubble height, streambank alteration, and woody
use monitoring may not be done during that year if it is not answering a
specific question.

• Another situation that may be common is finding that one of the annual
indicator thresholds is reached consistently before other, e.g., streambank
alteration reaches threshold levels before woody species use or stubble
height criteria are met. The decision may be to discontinue the stubble
height and woody species use procedures and monitor only streambank
alteration each year. However, caution must be exercised since the annual
indicators can be affected differently based on the season of use. For
example, maximum allowable willow use may be the first indicator met in
a riparian zone used late in the fall (well before streambank alteration or
stubble height). When the same pasture is used in the spring it is unlikely
that willow use will occur first - stubble height or streambank alteration
would likely be affected first and therefore be the most appropriate
indicator to monitor.

Establishing the Line Transect

After the DMA is selected, a permanently marked line transect is
established on both sides of the stream.

• The line transect at the DMA extends at least 1 10 meters (361 feet) along
the stream. Longer reaches may be needed on larger streams (over 5.5
meters orl 8 feet bankfull width), or those with extreme variability or site
complexity.

• Permanently mark the lower and upper end of the reach. Place the lower
marker, rebar or other suitable material, on the left-hand side (looking-up
stream). Steel t-posts are not recommended for this since they attract
livestock and will lead to concentrated impacts on the reach. Streamside
markers should be made of securely capped or bent over larger-diameter
rebar or similar material. Straight, jagged, rebar stakes that are not capped
or bent-over present a serious hazard to horses and other animals. Pace

1 10 meters (361 feet) up the stream along the thalweg or stream channel
and place the upstream marker on the right-hand side (looking up stream).
Markers should be placed a sufficient distance from eroding banks to
reduce the risk of losing the marker (see Appendix C, Figure 1).

• It is recommended that a reference marker (e.g., steel post, marked post in
a fence line, tree with a marker, unique rock, or other natural feature) is
located at least 30 meters (100 feet) away from the plot location or
described to assist locating the transect in the future. Record the distance
and compass bearing from the reference marker to the lower plot location
marker. Provide a geographic positioning system (GPS) location (UTM or
Latitude-Longitude) for the reference marker, lower, and upper transect
markers. Sketch the monitoring set-up to make sure future visits use the
same starting side of the stream.

Skills, Training, Collection, Time, and Equipment

Skills

Individuals must have a basic understanding of riparian ecology and stream
function. This requires knowledge of riparian species identification, erosion,
and deposition processes.

Training

Training is required to successfully apply this monitoring protocol. At
minimum, observers should receive the basic 2-day training module, including
the overview, data analysis, field presentation, and field-testing. Ideally, field
practitioners would also apply the protocol for several field days in the

presence of trainers to gain proficiency in the methodology. For example,

bank alteration measurement variability among observers was reduced from

about 30 percent variability without training to about 12 percent with training. ^

Collection Time •

If all ten indicators are monitored in the same year, sample time is w

approximately 2 to 4 hours per site. Normally a subset of the indicators is

chosen in a given year, and sampling is typically about 2 hours per site.

Depending upon travel time, from 2 to 4 sites are sampled per day. ^

Equipment •

See Appendix O W

DURES

Systematic Procedure *

1 . After the line transect markers are placed, photographs should be taken
before data is collected since the monitoring process will result in some

visible disturbance on the site. As a minimum, take photographs at the ^

following locations:

a. From the lower marker looking up-stream;

b. Across the stream from the lower marker; •

c. Downstream from the up-stream marker; and

d. Across the stream from the up-stream marker.

e. Take additional photographs as needed and describe the location ^
of each photo in relation to the down-stream marker.

2. Monitoring usually begins at the lower left-hand side of the stream

(looking upstream). Sketch the monitoring set-up, including markers and w

locations to ensure future monitoring data is collected in the same reach.

3. Use only the appropriate indicators for the site (see Appendix). If the site +
does not have the potential for woody species with appropriate

management, do not include the woody species regeneration and woody w

species use as part of the monitoring for the site. However, if the site

objectives include woody species, but no woody species are present, ™

woody species regeneration should be included to determine if ^

management is making progress toward meeting the objectives. Woody

species utilization data cannot be gathered until woody species begin ^

reestablishing along the greenline.

Beginning at the lower transect marker on the left hand side (looking
upstream) determine a random number between 1 and 1 0, take that
number of steps along the thalweg (deepest part of the channel) or along
the stream channel to the first plot location. Place the monitoring frame
(see Appendix D) down at the toe of the boot with the center bar along the

•

greenline. Continue the procedure at predetermined intervals (usually 2,
3, or 4 steps, or short enough to obtain 40 plots on each side of the stream)
until the upper transect marker is reached. If the required number of plots
is obtained prior to reaching the upper marker, continue reading plots
until the marker is reached. Once the upper marker is reached, cross the
stream and repeat the procedure down the other side to the end marker.
The entire length of the transect on both sides of the stream is sampled.
Individuals should determine the length of their steps and adjust the
interval between plots so that an adequate sample size can be obtained.
Mark a distance, usually 100 feet, and count the number of steps it takes
for that distance. Determine the average step length by pacing the
distance three or four times and calculating the average. For example, if
an individual takes an average of 66 steps in 100 feet, then the average
step length is 18 inches. Table 1 indicates the number of steps needed to
obtain at least 40 plots on a side of the stream.

Table 1 - Determining the Number of
steps between plots

Average Step
length

To obtain at least 40 Plots per
110 meter (361 feet)Transect

Steps between
plots

Spacing between plots
(Feet)

15 inch

7

9

18 inch

6

9

21 inch

5

9

24 inch

4.5

9

27 inch

4

9

30 inch

3.5

9

5. Do not use these monitoring procedures immediately following a flood or
high flow event resulting in sediment deposition and scour. Sediment
deposition and scour makes it difficult, if not impossible, to determine the
effects of the current season livestock use, and some vegetation may be
temporarily buried.

6. Long-term (trend) monitoring data should be gathered at three to five-year
intervals. This allows vegetation and streambanks to respond to the
effects of grazing management. In some cases, the period may be
extended be cause of slower recovery rates. Ten years should be the
longest interval used on any site.

Short-term annual indicator data may be collected at a different season
than the trend data; however, short-term data should be collected when it
is appropriate, typically right after livestock use. If the management
prescription requires a certain amount of residual vegetation remaining to
protect streambanks during high winter or spring flows, monitoring should
be done after the growing season has ended and livestock have been
removed from the area.

Use handheld computers to record data (see Appendix E). These devices
save about one hour per transect. However, the data may be recorded on
the Riparian Monitoring Data Sheet if a handheld computer is not
available (sec Appendices F).

A. Procedure: Locating the greenline (Modified from Winward

2000)

The Greenline is "The first perennial vegetation that forms a lineal grouping
of community types on or near the water's edge. Most often occurs at or
slightly below the bankfull stage" (Winward 2000). It is found only along
streams with defined channels.

The greenline often forms a continuous line of vegetation adjacent to the
stream, but can also be patches of vegetation on sand bars and other areas
where vegetation is colonizing or being eroded. Individual lineal
groupings are considered part of the greenline when they meet the criteria
described below. Review Appendices C and G for explanations and
examples of many greenline locations.

Criteria and Limits

1) "Most often the greenline is located at or near the bankfull stage. . . .At times
when the banks are freshly eroding or, especially when a stream has become
entrenched, the greenline may be located several feet above bankfull stage. "
(Winward 2000). In these cases, the greenline may be non-hydric species, i.e.,
upland species.

2) The location of the greenline should be determined when the stream is at the
summer low flow. Usually, the edge of the perennial vegetation, not the waters
edge at low summer flow, is the greenline (Winward, 2000). Some perennial
vegetation (e.g., spike rush, Eleocharis spp.) may grow in the margins of
streams and in slow backwaters. When this occurs, the greenline used in this
protocol is at the water's edge during summer low flow.

Vegetation

The lineal grouping of perennial vegetation must have at least 25 percent foliar
cover for the entire length of one quadrat (50 cm or 19.6 inches). If the
vegetation is not continuous within the plot, move the plot up the bank,
perpendicular to the direction of streamflow, until the cover requirement is met.

1) Colonizer species at or near the water's edge which meet the appropriate
criteria (i.e., 25 percent foliar cover, 50 cm (19.6 inches) long, and
establish a distinct lineal grouping of perennial vegetation) are considered
greenline, except as described in number 2. For example, short-awned

10

foxtail (Alopecwus aequalis), spike-rush [Eleocharis palustrus), arroyo
willow (Salix lasiolepis) and coyote willow (Salix exigua) on the
streambank (above the summer low flow) should be recorded as part of
the greenline (see Appendix G, Figures 2 and 16). These species have
moderately deep roots and the ability to stabilize streambanks.

2) Colonizers that commonly float on or submerge in the water, such as
brookgrass (Catabrosia aquatica), watercress (Rorippa nasturtium-
aquaticum), seep spring monkey flower (Mimulas guttatus), American
speedwell (Veronica amehcana), and smartweed {Polygonum
amphibium), may form grouping in the water or near the water's edge, but
are not considered part of the greenline (see Appendix G, Figures 5, 6, 7,
and 8).

3) Non-vascular plants such as mosses and lichens are not considered as part
of the greenline. The quadrat is moved away from the stream,
perpendicular to the water flow, until the minimum vegetation, rock,
and/or wood meet the criteria for greenlines.

4) Under some conditions, particularly in back waters where the current is
slow, Carex spp., Juncus spp., Eleocahs spp., and Scirpus spp. may
establish in the still shallow water along the stream during the summer
low flow periods. This condition occurs most frequently during low water
in a drought period. When this occurs, the greenline is along the edge of
the water at low summer flow (see Appendix E, Figures 2, 3, 4, 8, and 9).

5) The greenline runs approximately parallel to the stream channel. When
the streambank or the vegetation line becomes approximately
perpendicular (75 degrees or more) to the flow of the stream, the greenline
ends. Then the transect moves away from the stream perpendicular to the
stream flow and begins at the next lineal grouping of perennial vegetation
continuing along the greenline (see Appendix C, Figures 3 and 4).

6) The greenline is at the rooted base of perennial plants, whether herbaceous
or woody (see Appendix C, Figures 7 and 8).

7) Woody vegetation overhanging the stream is not considered a greenline.
The greenline is located at the edge of the lineal grouping of vegetation
nearest the water's edge, including anchored rock and wood (see
Appendix C, Figure 8).

8) When shrubs or trees have no understory (or less than 25% foliar cover),
the greenline is along a line connecting the streamside edges of the rooted
base of the plants, thus not at the drip line (see Appendix C, Figure 6).

9) If there is an overstory tree with a shrub understory, the greenline is at the
base of the shrub. For example, if there were a narrow-leaf cottonwood
tree over red osier dogwood, the greenline would be at the base of the
dogwood. When shrubs such as willows are over herbaceous vegetation

11

such as sedges, the greenlinc is at the edge of the sedges or the lower layer
of vegetation.

10) Only canopy cover from plants rooted on the streambank on the same side
of the stream is recorded. Overhanging canopy from plants on the
opposite side of the stream is not recorded as canopy cover, even if it
overhangs the plot. This condition often occurs on small streams.

Rock as part of the greenline

Rocks, boulders, talus slopes, and bedrock that are part of the streambank
must be of sufficient size (at least 15 cm or 6 inches in diameter) to protect
that portion of the streambank from erosion during high stream flows and
be exposed along the greenline. The rock or boulder must be at least
partially embedded/anchored in the streambank, with no evidence of active
movement by water. Appendix G, Figures 33, 37, 38, 41, and 42 provide
examples of rock along the greenline.

Anchored and Downed Wood as part of the greenline

Anchored wood consists of logs or root wads that are anchored in or along
the streambank in such a way that high flows are not likely to move them.
The anchoring may be embedded in the streambank or wedged between
rocks, trees, or other debris. Anchored wood must currently exert a
hydrologic influence on the stream. There should be no evidence of active
erosion that would destabilize the woody material. When logs are anchored
and somewhat perpendicular to the stream, count the amount of anchored
wood that joins the vegetation greenline on each side of the log (See
Appendix G, Figures 33 through 36).

Detached Blocks of Vegetation

Blocks of vegetation obviously detached from the streambanks are not
recorded as greenline. When deep-rooted hydric vegetation covers the block
from the water's edge to the terrace wall creating a new floodplain (false
bank), the greenline is the edge of the vegetation along the stream (see
Appendix G, Figures 24 through 32).

Islands

Islands are defined as those areas that are surrounded by water at summer
low flow or have a channel that is scoured frequently enough to keep
perennial vegetation from growing. The greenline follows the main banks
of the stream and not islands (see Appendix C, Figure 3 and Appendix G,
Figures 17 through 19).

12

No Greenline Present

In some instances a greenline may not be present within proximity to the
stream. This may be annual vegetation, such as cheatgrass, occupying the
upland. In other cases, the area in proximity to the stream may be barren.

A terrace is a relatively flat area adjacent to a stream or lake with an abrupt
steeper face adjoining the edge of the stream. The first terrace is the first
relatively flat area adjacent to and above the edge of the water. It may be an
active floodplain or an area too high for the water to reach under the current
climate and channel conditions. The second terrace is the next elevated area
above the first terrace, with a distinctly steeper slope facing the stream (see
Appendix G, Figures 21 and 22).

Record "NG" or no greenline present when any of these conditions exist:

1 . Lineal grouping of perennial vegetation is not present on the first terrace or the

second terrace and the first lineal grouping is further than 6 meters (20 feet) of
the edge of the stream (see Appendix G, Figure 46).

2. If no obvious terraces are present and lineal grouping vegetation is more than 6

meters (20 feet slope distance) from the edge of the water.

3. If sharp meander bends with a narrow peninsula exist with no lineal grouping of

vegetation between the streambanks (see Appendix G, Figures 47 and 48).

Specific Instructions

1 . Observers should look ahead and determine the greenline. This provides
continuity for pacing in the appropriate location. The center of the
monitoring frame is placed along the greenline.

2. Evaluate the vegetation within the monitoring quadrat on the floodplain
side of the greenline (see Appendix C, Figure2).

3. When there is less than 25 percent perennial foliar vegetation cover,
including shrub and tree overstory, move up the bank, perpendicular to the
stream flow, until the quadrat has the appropriate amount of vegetation.
The frame is adjusted along the actual edge of the greenline.

4. Record all other pertinent data at the plot location (e.g., streambank stability,

woody species regeneration, streambank alteration, and woody species use,
etc.).

B. Procedure: Measuring and Recording Streambank and
Vegetation Indicators

13

/. Greenline Vegetation Composition

Vegetation Classification

Two classification systems are commonly used to describe and record the
vegetation occurring on the greenline, i.e., riparian community types and
dominant plant species. Document the vegetation classification method
used on the field sheet or handheld computer.

Recording vegetation using dominant plant species

Dominant plants are the species having the largest portion of the
vegetation composition by cover in the quadrat. To be considered
dominant, the plant must represent at least 25 percent of the plant
composition by cover within the quadrat. The exception is where a
mature tree or mature shrub overstory occurs. Mature trees or shrubs
with any portion of the canopy covering the quadrat are considered
dominant. This exception applies only to mature trees and shrubs;
seedlings and young plants that overhang the plot are not counted as
dominant unless they are rooted within the plot and have 25% vegetation
composition by cover.

When only a single species is found in or over the quadrat, it is recorded
as the dominant species. When two or more species make up a majority
of the composition in or over the quadrat and are of approximately equal
proportions, each is recorded as dominant.

Sub-dominant plants occur when the composition of a particular plant
species or group of plants, e.g., mesic forbs, are less than the dominant
species. Sub-dominant plants do not have to exhibit 25 percent
vegetative composition by cover within the quadrat (although it is
possible). An example of this would be if the quadrat contained 75
percent water sedge (Carex aquatilis) and 10-25 percent Kentucky
bluegrass (Poapratensis). In this case, the sedge would be recorded as
dominant and the bluegrass as sub-dominant. See Appendix H for a list
of common dominant species in the intermountain area.

1. How to address overstory vegetation: Riparian vegetation structure may
occur in three layers: trees, shrubs, and herbaceous. Mature plants, with
any part overhanging the plot (e.g. willows) are always recorded as
dominant vegetation. Seedlings and young plants must be rooted within
the plot to be counted, and are treated the same as understory vegetation.
When quaking aspen {Populus tremuloides) occurs with an understory of
red-osier dogwood (Cornus sericea), both the taller plant layers of
quaking aspen and the red-osier dogwood are recorded as dominant plants.
A third dominant plant may be listed if an herbaceous understory is

14

present and makes up at least 25 percent of the understory composition of
plants in the plot (anchored rock and wood are also part of the cover).
Another example: yellow willow (Salix lutea) occurs in the overstory
with a dense mat of Nebraska sedge (Carex nebraskensis) in the
understory within the plot. In this case, yellow willow would be recorded
as dominant and the Nebraska sedge would also be recorded as dominant.

2. When to include Sub-dominant plants: Users should record important
plants having less than 25 percent of the vegetative composition. Plant
species that indicate potential, trend, or invaders may also be included.
For example, Kentucky bluegrass (Poa pratensis) dominates a plot with a
minor component of Nebraska sedge {Carex nebraskensis). The Kentucky
bluegrass would be listed as the dominant plant and even though the
Nebraska sedge is only a minor portion of the vegetation composition, it is
recorded as sub-dominant to track composition trends through time.

3. Plants with equal composition: When two or more plant species,
including rock and wood, have about the same amount of plant cover in
the plot, and each is over 25 percent of the composition, record each as
dominant. Dominant plants are recorded on separate lines under the same
plot number. These transition vegetation communities are important in
describing the ecological processes occurring along the stream. When this
occurs, list the most dominant species first and the second species on the
next row.

4. Rock and Wood: Rock and/or wood making up at least 25 percent of
the length of the greenline within the quadrat is considered either dominant,
or sub-dominant depending on the vegetation in the remainder of the >
quadrat. Rock is recorded as part of the greenline when it is at least 25
percent of the length of the quadrat. If rock is at least 50 percent of the
quadrat length, record "rock" as dominant. If rock is 25-49% of the plot, it
is recorded as sub-dominant. Wood is recorded as part of the greenline
when it is at least 25 percent of the length of the quadrat. If wood is at least
50 percent of the quadrat length, record "wood" as dominant or co-
dominant. If wood is 25-49% of the plot, it is recorded as sub-dominant. For
example, anchored rock is 25 percent of the length the quadrat and beaked
sedge is 75 percent. Beaked sedge would be the dominant and rock the sub-
dominant. If rock made up 50 percent of the length and beaked sedge the
remainder, rock and beaked sedge are both dominant.

5. Recording the data: Record data either on a handheld computer or on
the Riparian Monitoring Data Sheet (see Appendix F) by dominant
vegetation species or community type that has the majority within
monitoring frame on the field form or in a computer.

15

Recording vegetation using riparian community types

Riparian Community Types may be used when riparian vegetation in the
area has been classified. When riparian community types are used, record
the riparian community type publication that is being used to classify the
vegetation. Riparian Community Type Classification of Utah and
Southeastern Idaho is a typical publication. When using riparian
community type classification, it is very important to use the keys provided
in the publication for consistency.

Rock and/or wood making up at least 25 percent of the length of the
greenline within the quadrat is classified as a distinct community type. For
example, anchored rock is 25 percent of the length the quadrat and beaked
sedge CT is 75 percent. Beaked sedge would be listed as the dominant and
rock the sub-dominant on the data sheet. If rock made up 50 percent of the
length and beaked sedge the remainder, rock and beaked sedge are both
dominant.

Record riparian community types exactly the same as those listed in the
tables in Appendix I or in the tables in the handheld computer. For
example, Booths willow (Salix 6oor/?/7)-Kentucky bluegrass (Poa pratensis)
is recorded "SABO/POPR" in the appropriate column.

2. Streambank Alteration

General Description

The procedure describes a method for measuring the percent of the linear
length of streambank that has been altered by large herbivores (e.g., cattle,
horses, sheep, bison, elk, and moose) walking along or crossing the stream
during the current grazing season.

The part of the streambank that is measured using this protocol is an area 20
cm on each side of the greenline. This focuses on that portion of the
streambank most directly affected by the erosive effects of water (see
Appendix J).

Streambank Alteration Definitions

Streambank alteration occurs when large herbivores, e.g., elk, moose, deer,
cattle, sheep, goats, and horses walk along streambanks or across streams.
The animals' weight can cause shearing that results in a breakdown of the
streambank and subsequent widening of the stream channel. It also exposes
bare soil, increasing the risk of erosion of the streambank. Animals walking

16

along the streambank may increase the amount of soil exposed to the
erosive affects of water by breaking or cutting through the vegetation and
exposing roots and/or soil. Excessive trampling causes soil compaction
resulting in decreased vegetative cover, less vigorous root systems, and
more exposure of the soil surface to erosion.

Hoof shearing is the most obvious form of streambank alteration. It is
common for the shearing action of the hoof to break off a large portion of
the streambank. Include as alteration the total length of broken streambank
directly associated with an occurrence of shearing, not just the width of the
hoof mark (see Appendix J).

Trampling impacts must be the obvious result of current season use and is
considered streambank alteration when:

• Streambanks are covered with vegetation and have hoof prints that expose
at least 12 mm (about V% inch) of bare soil;

• Streambanks exhibit broken vegetation cover resulting from large
herbivores walking along the streambank and have a hoof print at least 12
mm ('/2 inch) deep. Measure the total depression from the top of the
displaced soil to the bottom of the hoof impression; and/or

• Streambanks have compacted soil caused by large herbivores repeatedly
walking over the same area even though the animal's hoofs sink into
and/or displace the soil less than 12 mm (Vi inch).

Large herbivores trampling and trailing on top of terraces, above the active
floodplain, is not considered streambank alteration. Hoof marks within the
plot with shearing on the streambank and/or terrace wall and/or trampling at
the base of the streambank or terrace wall are considered streambank
alteration (see Appendix J, Figure 5).

Procedure

The procedure uses the entire 42 cm by 50 cm monitoring frame. Five lines
are projected across the frame perpendicular to the center pipe (see
Appendix D, Figure 1).

1 . Looking down at the entire frame, determine the number of lines within
the plot that intersect streambank alteration (see Appendix J). Record the
number of lines (0 - 5) that intersect streambank alteration. Record only
one occurrence of alteration, trampling, or shearing per line. This process
is repeated at the predetermined interval so that 80 to 1 00 samples are
taken (depending upon the length of the step) on each side of the stream.
It is important that the observer determine only the current year's
streambank disturbance.

17

2. Place the center of the frame along the grcenline at the end of the toe.
Record only direct alteration occurring on the terrace wall or the
streambank (see Appendix J, Figure 5).

3. Hoof prints or trampling on streambanks with fully developed, deep-
rooted hydric vegetation {e.g., Carex spp., Juncus spp., and Salix spp.) is
not recorded as alteration unless plant roots or bare soil are exposed.
Hoof shearing along the streambank is alteration.

4. Compacted livestock trails on or crossing the greenline that are the
obvious result of current season use are counted as trampling (see
Appendix J, Figures 3 and 4).

5. Roads and tributary streams are not counted. Continue to pace directly
across the area until the greenline is reached. Record separately on the
form any samples that are on the road or water. Leave the cell blank in
the handheld computer or on the form.

6. When obstructions such as trees, shrubs, or other physical impediments
are encountered, sidestep at 90-degrees from the transect line and
continue pacing parallel to the transect to avoid the obstruction. Project
the lines from the end frame to the streambank and record the hits.
Record the amount of alteration on the streambank. Most of the time it
will be "0." Return to the original transect as soon as possible by
sidestepping back to the transect line and continuing.

7. When the greenline is away from the stream channel or the edge of the
first terrace, pacing should continue along the edge of the first terrace (see
Appendix G, Figure 45). If there is no vegetation meeting the definition
(see pages 10 - 15) record "NG" (no greenline) and all appropriate data
for the other indicators at each plot location.

8. The procedure should not be used if a high flow (flood) event occurs prior
to monitoring. In that situation, the water's energy and sediment will
make it very difficult to determine if the effects are a result of the current
grazing season or past grazing seasons.

IS

3. Streambank Stability and Cover

General Description

Streambank stability is observed on the bank associated with the quadrat,
and is recorded using one of six stability classes (see Streambank Stability
Classification descriptions below and Appendix K).

Procedure

At each plot location, evaluate the condition of the streambank within the
plot and record the stability class. If the plot along the greenline does not
include the streambank, project the length of the plot, 50 cm (19.6 in.) to the
streambank and record the stability class (see Appendix K, Streambank
Stability Key). The following are steps that are useful in determining the
stability class.

1 . What kind of bank? Is the bank depositional (inside of channel bends
and bars are usually present) or erosional (outside of bends/straight
channel)? [See Appendix K]

2. Where is the bank? The length of frame (50 cm) between scour line
and the top of the first terrace. Typical scour line indicators are the
elevation of the ceiling of undercut banks, at or slightly above the summer
low flow elevation, or on depositional banks, the scour line is the lower
limit of sod-forming or perennial vegetation (see Appendix K).

3. Is it Covered? At least 50% aerial cover of perennial vegetation, cobbles
six inches or larger, anchored large woody debris (L WD) with a diameter
of four inches or greater, or a combination of the vegetation, rock, and/or
LWD is at least 50 percent.

4. Is it stable? It is stable if none of the following exist: Either a fracture
(crack is visibly obvious on the bank), slump (portion of bank has
obviously slipped down, been pushed down by trampling or shearing,
etc.), or slough (soil is breaking or crumbling and falling away and is
entering the active stream channel) or the bank is steep (within 10 degrees
of vertical), and/or bare, and eroding (including bare depositional bars).

Streambank Stability Classification

Appendix K provides definitions, key, illustrations, and photographs. After
assessing the plot, record the data on the Riparian Monitoring Data Sheet
shown in Appendix F or in the handheld computer by one of the following
six-streambank stability classes:

CS - Covered and stable (non-erosional). Streambanks are covered with
perennial vegetation, and/or cobble (6 inches or bigger), boulders,

19

bedrock, or anchored wood (4 inches in diameter or larger) to protect
them from the erosive effects of water. Streambanks do not have
indications of erosion, breakdown, shearing, or trampling that exposes
plant roots. Banks associated with gravel bars having perennial deep-
rooted vegetation along the edge of the floodplain line are in this category
(see Appendix K, Illustrations and Figures)

CU - Covered and unstable (vulnerable). These streambanks are covered
with perennial vegetation and occur where undercutting by water may
cause breakdown, slumping, nicks, bank shearing, and/or fracturing along
the bank (see Appendix K, Illustrations and Figures)

US - Uncovered and stable (vulnerable). Streambanks having
consolidated soils high in clay, particularly in the lower part of the
streambank, may be uncovered and stable. These banks are vulnerable to
high flows, particularly winter flows with floating ice. Uncovered and
stable banks may also be compacted streambanks trampled by
concentrations of ungulates, human trails, vehicle crossings, or other
activities that cause compaction. Such disturbance flattens the bank so
that slumping and breakdown does not occur even though vegetative
cover is significantly reduced or eliminated (see Appendix K, Illustrations
and Figures).

UU - Uncovered and unstable (erosional & depositional). These are bare,
eroding streambanks and include all mostly uncovered banks that are at a
steep angle to the water surface When the bank is not present due to
excessive bar deposition or to streamside trampling, the bank will be
classified "uncovered/unstable." (See Appendix K, Illustrations and
Figures)

FB - False bank (stable). Streambanks have slumped in the past but have
been stabilized by vegetation. These banks are usually at a lower level
than the terrace and are covered/stable (CS). (See Appendix K,
Illustrations and Figures).

UN - Unclassified. Side-channels, tributaries, springs, road crossings,
etc., cause a break in a streambank. Livestock or wildlife trails are not
included in this category, but are included as uncovered/stable (see "US"
above).

Streambank Cover

Streambanks are considered covered if they show any of the following
features:

1 . Perennial herbaceous and/or woody vegetation provide more than 50
percent ground cover of the vertical height of the streambank (Bauer
and Burton, 1993).

2. Roots of vegetation cover more than 50 percent of the bank. (Deep
rooted plants such as willows and sedges provide such cover.)

20

3. Cobble size rocks (at least 6 inches in diameter), boulders, or bedrock
cover more than 50 percent of the streambank surfaces.

4. Logs, at least four inches in diameter, cover more than 50 percent of
the bank surfaces.

5. At least 50 percent of the bank surfaces are protected by a
combination of the above.

Streambank Stability

Streambanks are considered stable if they do not show indications of any of
the following features:

1 . Breakdown: Obvious blocks of streambanks have broken away and
lying adjacent to the bank breakage.

2. Slumping Bank: Bank that has obviously slipped down. Cracks may
or may not be obvious, but the slump feature is obvious.

3. Bank Shearing: Occurs when animals walk along the streambank or
cross the stream and shear or break off portions of the streambank.
Bank shearing is recognized by a shear plane with obvious hoof
marks on the streambank. Include the total length of bank
disturbance associated with the shearing.

4. Fracture: A crack is visibly obvious on the bank indicating that the
block of bank is about to slump or move into the stream.

5. Vertical and Eroding: The bank is mostly uncovered, and the bank
angle is steeper than 80 degrees (178 % slope) from the horizontal.

6. Bare Depositional Bar: A depositional bar without adequate ground
cover (50%).

4. Residual Vegetation Measurement (Stubble Height)

General Description

The objective of residual vegetation (stubble height) measurement is to
determine the height of key vegetation species remaining following a period
of grazing. The measurement may be used in two ways: first, to determine
when livestock should be moved from the riparian area, and second, at the
end of the grazing season to determine whether livestock grazing
management changes are needed the following year.

Procedure

Prior to recording stubble height, one or more key specie(s) must be
selected. For this protocol, at least one of the key species selected must be a
relatively abundant herbaceous forage plant that is commonly used by
livestock, (preferably hydric species), and able to help address some aspect
of streamside conditions and grazing management. In other words, the
observer must establish what the species is "key" to and why it is important

21

to measure. It is acceptable to use more than one key species if desired to
help address other important issues. For example, where hydric species are
missing or lacking, species such as Kentucky bluegrass or red top can be
(and should in some instances) measured if it helps answer grazing-related
questions. Normally key species are chosen to assess livestock use on the
desired riparian plants, therefore palatable hydric species are preferred.
Record the measurements by species.

Most riparian key species grow tightly together, forming dense mats with
little distinct separation of individual plants. As a result, the sampling
method uses a 3-inch diameter circle of vegetation rather than attempting to
separate the mats into individual plants. If the plants are distinct and not
mat forming, select a 3-inch circle of vegetation nearest the handle of the
frame that includes the key species (see Figure 1).

Figure 1 — Residual vegetation height is measured within a
3-inch diameter circle at the back right-hand corner of the
greenline quadrat nearest the frame handle.

Using the frame handle with one-inch
increments, (or a ruler) measure within
the circle to determine an "average"
leaf length (rounded to the nearest Vi
inch), as shown in Figure 2. Grazed
and ungrazed plants are measured
from the ground surface to the top of
the remaining leaves. Account for
very short leaves as well as the tall
leaves. Do not measure seed culms.
Determining the "average" residual
vegetation height will take some
practice. Be sure to include all of the
key hydric graminoid species' leaves
within the sample. The easiest method
of doing this is to grasp the sample in the sampler's hand, stand the leaves
upright, and then measure the average height (see Figure 2).

Figure 2 — Form hand into an
approximate 3-inch circle, grasp the
vegetation and determine the average
leaf height.

22

When the key graminoid species does not occur in a mat near the handle of
the quadrat, but as individual plant or several individual plants, the 3-inch
plot is placed over the key species plants nearest the handle (see Figure 3).
Measure the leaves of all the key graminoid species rooted within the 3-inch
diameter plot.

Figure 3 — When key species plants are not in the corner by the
frame handle, select the key species plant(s) nearest the handle.
Identify the 3 -inch circle and measure the average leaf height of
all key species plants rooted within the circle.

When a key graminoid species does not occur within the quadrat, leave the
cell blank and proceed to the next plot location.

Once the samples are collected, both the median and the mean (average)
height are calculated and presented in the Data Analysis Module for the
riparian key specie(s). The median is the single mid-point for an odd
number of samples and the average of the two co-midpoints for an even
number of samples (USDI, BLM, 1999). For example, if the middle two
numbers for an even number of samples are 5 and 6 inches, the median is
5.5 inches.

5. Woody Species Regeneration (Modified from winward 2000)

General Description

Woody species regeneration is modified from Winward (2000). The
original procedure developed by Winward, is a six-foot wide by 1 10-meter
belt transect with the center of the six-foot belt being over the greenline.
Woody plants are counted by species and age classed. This modification to
facilitate collecting multiple indicators in a more efficient

23

Streamside of ereenline

Floodplain

Greenline

- -fe+H

»*

Figure 4 — Woody species regeneration plot is 0.42 meters by 2.0
meters. The plot is defined by placing the monitoring frame
perpendicular to the greenline. The frame is placed end-to-end on
each side of the greenline.

manner uses a 0.42 meter by 2 meter plot, 1 meter either side of the
greenline (Figure 4), providing a sample of woody species along the
transect.

Procedure

Identify the plant by species; count the number of plants rooted in the plot,
and age class (described below) of each woody plant within the plot.

1 . The woody species regeneration plot is 0.42 meter wide by 2 meters long (one
meter on each side of the greenline), as shown in Figure 4.

3.

Place the end of the monitoring frame on and perpendicular to the greenline,
and count the number of woody plants by species rooted within the monitoring
frame. If one stem at ground level is within the plot and several other stems are
immediately outside the plot, determine if the stem within the plot is actually
connected to those outside the plot. If it is, record the age of the entire plant to
which the stem is connected. If it is not connected, consider the stem as an
individual plant and record the age class appropriately. Record by species and
age class. (Do not count woody species canopy cover as woody species.)

Move the monitoring frame away from the greenline, and place it at the end of
the first monitoring frame, and repeat the procedure (see Figure 4). Tables 2
and 3 provide descriptions of woody species age classes.

Table 2 - Woody Species Age Classes for Multiple Stem Species

Includes clumped willow (Salix spp.) species and shrubby forms of mountain alder
(Alnus incana), and water birch (Betula occidentalis)

Number of stems at
the ground surface

Age class

1 stem

Seedling

2 to 10 stems

Young

>10 stems

Mature

0 stems alive

Dead

Modified from Winward 2000

24

Table 3 - Woody Species Age Class for Single Stemmed Species.

Single stemmed species such as birch (Betula spp.), alder (Alnus spp.
and cottonwood or aspen (Populus spp.)

Age
Class

Cottonwood

Other Broadleaf Species

Seedling

Stem is < 4.5 ft. tall or < 1
in. diameter breast height
(dbh)

Stem is < 3 ft. tall and the stem
is less than 1 in. diameter at the
base

Young

Stem is > 4.5 ft. tall and 1
to < 5 in. dbh or stem is <
4.5 ft. tall and is 1 to < 5
in. dbh

Stem is > 3 ft. tall and < 3 in. dbh
or < 3 ft. tall and the stem is 1 to
3 in. dbh

Mature

>5 in. dbh

Stem is > 6 ft. tall and > 3 in. dbh
or < 6 ft. tall and > 3 in. dbh or
stems < 3 ft. tall with multiple
branching (hedged) near the top
of the stem

Dead

Entire canopy is dead

Entire canopy is dead

4. It is difficult to age class rhizomatous species such as wolf willow (Salix
wolfii), planeleaf willow (S. plcmifolia), coyote willow (S. exigua), wild rose
(Rosa spp.), and golden current (Ribes aureum), and they are not recommended
for inclusion in the woody species regeneration. When these species need to be
monitored, use the greenline or a line transect.

6. Woody Species Use (Modified Landscape Appearance
Method)

General Description

This method is modified from the Qualitative Assessments - Landscape
Appearance Method (also called the Key Forage Plant Method) described in
Utilization Studies and Residual Measurements, Interagency Technical
Reference, 1996. Winward (2000) recommends a similar method based on
estimated utilization ranges.

The technique is an ocular estimate of woody species (e.g., willow, alder,
birch, dogwood, aspen, and cottonwood) use based on the general
appearance of the woody species rooted within a plot along the greenline.
Estimates are based on a range or class of use of the available current year's
growth on the plants. Examiners must be trained to recognize the various
use classes according to written class descriptions described below.

25

Procedure

The plot size (see Figure 8) for obtaining woody species use is 2 meters
wide (1 meter either side of the greenline), and the length is determined by
the interval

between plots. For example, if the distance between plots is two steps,
observe all of the shrubs rooted within 1 meter either side of the greenline
for a distance of two steps forward and record the mid-point value (see
Table 4) of each key woody species use class. Or, if the plot interval is four
steps (two paces), observe all of the shrubs rooted within 1 meter either side
of the greenline and within four steps forward and record the mid-point
value of each key woody species.

For cattle, only shrubs with at least 50 percent of the current year's leader
growth below 5 feet (see Table 5) should be considered. When shrubs have
over 50 percent of the active leader growth above 5 feet, the leaders are not
generally available to cattle, and the plant usually has adequate leaf area for
photosynthesis to maintain plant health. If no shrubs are encountered
within the plot, leave the space on the field data sheet blank.

Observers examine the woody plants rooted within plot (see Appendix M)
and classify the use based on the descriptors. The five utilization classes
(see Table 4) describe the relative degree of use of the available current
year's leader growth for riparian shrubs and trees. Available current year's
leader growth (see Table 5) is that portion of shrubs or trees that are within
reach of the grazing animal.

Table 4 - Woody Species Use Classes and Descriptions.

Class

Percent

Utilization

Range

Description

None to
Slight

0- 10
(mid-point = 5)

Browse plants appear to have little or no
use. Less than 10% of the available current
year's leader growth is disturbed.

Light

11-40
(mid-point = 25)

There is obvious evidence of leader use.
The available leaders appear cropped or
browsed in patches and 60 - 89% of the
available leader growth of browse plants
remains intact.

Moderate

41-60
(mid-point = 50)

Browse plants appear rather uniformly used
and 40 - 60% of available annual leader
growth of the plants remains intact.

26

Class

Percent

Utilization

Range

Description

Heavy to
Severe

61-90
(mid-point = 75)

The use of the browse gives the appearance
of complete search by grazing animals. The
preferred browse plants are hedged and
some clumps may be slightly broken. Only
between 10 and 40% of the available leader
growth remains intact.

Extreme

90-100
(mid-point = 95)

There are indications of repeated grazing.
There is no evidence of terminal buds.
Some patches of second and third years'
growth may be grazed. Hedging is readily
apparent and browse plants are frequently
broken. Repeated use at this level will
produce a definitely hedged or armored
growth form. Ten to 40% of the more
accessible second and third years' growth of
browse plants have been utilized. All
browse plants have major portions broken.

Table 5 - Available Current Year's Growth: Height of Grazing (USDI,
BLM, 1992)

Kind of Animal

Height of Available Leader
Growth (feet)

Cattle

5

Sheep, antelope, big horn sheep

3.5

Horses, elk, and moose

7

Deer

4.5

Use the appropriate "Height of Available Leader Growth" for the kind of
animals that are of concern in the area. It is difficult, if not impossible, to
discern between shrub use by domestic livestock and wildlife during
periods of common use. Therefore, attempts to determine the kind of
animal that use the browse should not be made.

C. IN-CHANNEL INDICATORS

The following in-channel measures have been included because they are
reasonably objective, are strongly associated with livestock grazing
influences to stream habitat, and have been found predictive of aquatic
health.

7. Greenline-to-Greenline Channel Width (GGW)

General Description

27

Many stream channels are over-widened as a result of vegetative changes
and physical disturbance to streambanks over time. Improper livestock
grazing can alter stream habitats by channel widening and/or incision (Clary
et al. 1996, Clary 1999, Clary and Kinney 2002, Kaufman and Krueger
1984). Under improper grazing, protective vegetation is weakened or
removed, and trampling may induce a sloping streambank profile (Clary
and Kinney 2002). Subsequent erosion of weakened streambanks during
floods results in a wider, shallower stream channel. These changes to
stream habitats can be detrimental to biota (Bohn 1986). Clary's (1999)
observations at research sites indicated that the stream width of previously
over-grazed streams decreases with improved grazing management of
riparian zones. The average amount of narrowing was inversely associated
with the level of grazing intensity. Between 1990 and 1994, width changes
as a proportion of the original measurement were: No grazing - 41%
reduction, light grazing - 34% reduction, and medium grazing - 1 8%
reduction. Stream depth, on the other hand, was variable through time and
appeared to change primarily in response to climatic events. After a flood
event in 1996, channel depth at the ungrazed site increased to 2.33 times the
original depth. This vertical scour likely resulted from the longer-term
effect of channel narrowing.

Commonly the width of stream channels is determined by measuring
channel width at the bankfull level. Detailed measurements of width and
depth are accomplished by surveying channel cross-section profiles. This
method is not useful at a large number of positions along the stream because
it is time-consuming and expensive. Too few cross-section measurements
do not adequately estimate mean channel geometry, due to site variability.

As summarized by Bauer and Ralph (2001), the major concern with use of
width measurements at bankfull level is the reliability of the method.
Bankfull width is determined by using field characteristics such as sediment
surfaces and profile breaks to identify the elevation of the active floodplain
surface. These definitions are vague and the actual selection of bankfull
level is, at best, subjective.

Other field methods have measured the "wetted width" of the stream.
Although this level in the channel is easily identifiable, unfortunately,
wetted width varies dramatically by stream flow. Because it is normally
measured during low or intermediate streamflows, it provides little
information about the overall channel characteristics of the measured
stream.

Greenline-to-greenline width (GGW) is the non-vegetated distance between
the greenlines on each side of the stream. As stated by Winward (2000):

28

"Most often the greenline is located at or near the
bankfull stage. As flows recede and the vegetation
continues to develop summer growth, it may be
located part way out on a gravel or sandbar. At times
when banks are freshly eroding or, especially when a
stream has become entrenched, the greenline may be
located several feet above bank-full stage."

Though related to the bankfull stage, the greenline is easier to identify. In a
recent meeting of scientists working to achieve greater consistency in
riparian monitoring, it was determined that the greenline can be even more
objectively determined if a set of rules or criteria could be identified. A
sub-group was identified and a product developed early in 2005. These
criteria are contained within this monitoring protocol (page 6), and they
build on the original definition of Winward (2000).

To achieve an adequate sample for estimating the mean width (GGW), take
measurements at each plot location. The results are a mean width of the
non-vegetated stream channel. As streambanks recover, the stream channel
typically narrows and the average non-vegetated GGW is reduced.

This indicator helps document stream channel recovery over time. Since
the recovery process may be relatively slow, it is recommended that the
procedure be repeated every three to five years. The procedure is relatively
easy and does not consume a lot of time.

Procedure

At each plot location (see Appendix C, Figure 1), measure the distance
between the greenlines on each side of the stream and perpendicular to the
water flow direction. A laser range finder is the most expedient way of
measuring the distance. It reduces the time required to do the
measurements by about two-thirds. However, these instruments capable
of a measuring accuracy of ±0.3 meter are about $700.00, while those
accurate to ±0.03 meter are $2,400.00. Other less expensive options
include measuring rods and tape measures.

Measure from the greenline associated with the center bar on the quadrat
frame (near the toe of the boot (see Appendix C, Figures 2), to the
greenline on the opposite side of the stream. The measurement is usually
taken from only one side of the stream. If there are an inadequate number
of samples, measurements may be taken from the opposite side of the
steam. Measure to the nearest 0.25 feet or 0. 1 meter.

The measured distance is from the edge of the rooted base of the plants on
the greenline, not the overhanging or overstory vegetation (see Appendix
K, Figures 1 and 2).

29

4. When a vegetated island (at least 25% foliar cover) is encountered along
the line, determine the total distance between the greenlines and deduct
the length of the vegetated island to determine the non-vegetated GGW 4
(see Appendix K, Figures 3, 4, 5, and 6).

f

5. Non- vegetated islands are considered part of the non-vegetated GGW (see
Appendix K, Figure 5). •

t

8. Maximum Water Depth as measured at the deepest point

in the stream (Thalweg depth): *

General description

The nature of the bed profile in a longitudinal direction has been found to P

be a way to measure overall habitat structure and quality (Madej 1999). ^

Increases in the variation of channel depths increases the complexity of

aquatic habitat. Channel depth variations are created by in-stream and #

streamside elements that resist the erosion energies of the stream. Thus, as

streams are subject to greater amounts of erosion-resisting streamside

vegetation, habitat complexity increases. Recent research by the Pacific <f

Northwest Research Station of the Forest Service concluded that

"... measures of channel geometry, pool frequency, and pool size are viable

indicator variables for effectiveness monitoring, " (Woodsmith et al. 2005) «

Thalweg depth profiles allow for objective determination of pool frequency

and quality. Past methods that rely upon observers to define pool

boundaries has been too subjective and not reasonably repeatable. Recent ^

research assessed the relation between fish abundance and thalweg metrics

(Mossop and Bradford 2006). In that study Chinook salmon densities 1

varied greatly among stream reaches, and thalweg metrics explained 57% of

the variation. An excellent metric, the "variation index" (calculated by the

standard deviation of population residual depths along the reach) was found #

to be significant. It will also be possible to objectively estimate pool

quality from maximum depth values and substrate sizes (described in

indicator 10). #

Procedure

0

*

•

#

«

The Thalweg profile is constructed by measuring the depth of water over
the channel bed at spaced intervals along the channel's thalweg (or thread of
maximum depth/velocity). Thus at each plot location, normally while the t

observer(s) is measuring greenline-to-greenline width, a measurement of the
maximum water depth along that transect is measured. The maximum *

depth represents the deepest point in the cross section, and is found by
probing with a depth rod until the deepest point is located. All 80+ plots
should include a maximum thalweg water depth to acquire the sample size I

needed to objectively estimate the habitat metrics. It is important that the

*

30

plot spacing be recorded in the "Header" form of the Data Analysis Module
for proper calculation of the metrics.

9. Water width:

General description

Water width is easy to measure and reasonably precise. As greenline-to-greenline
width is sensitive to changes in streamside vegetation through time, so water widths
would also reflect vegetation changes. However, water width is influenced by
streamflow and will vary according to climatic conditions and season of year. For
this reason, water width alone will likely not represent a good monitoring indicator.
However, in combination with maximum depth, the ratio: Max Depth to Water
Width is influenced more by channel cross-section profile than by streamflow. Thus
changes in channel morphology, through time, can be reflective of this parameter
(Henderson et al. 2003).

Procedure

Measure widths between waterlines, with the tape or rod oriented perpendicular to
the channel. If islands are present, subtract the width of the island from the total
width of both channels. Measure only to the edge of the bank when an undercut
exists. Do not measure beneath the undercut. Measure water widths at all 80+ plot
locations and in the same transect as the thalweg depth measure.

10. Substrate composition:

General description

There is a sizeable literature that supports the contention that excess
substrate fines are adverse to salmonids (Bauer and Ralphs 2001, McHugh
and Budy 2005). The Literature also supports use of Pebble Counts to
estimate substrate composition (Bunte and Apt 2001). With respect to
riparian vegetation, the literature suggests that loss of bank stability is
related to increases in substrate fines. Tests of the pebble counting
technique indicate that there is operator bias against the fines fraction in the
substrate (Bunte and Apt 2001). However, this bias is presumably
consistent, therefore trends through time should theoretically be detectable.
Streams with complex substrate size distributions need more samples than
those with simple substrates (Bundt and Apt 2001). The authors suggest a
minimum of 200 particles from evenly spaced collection points across the
scoured channel (the non-vegetated portion of the channel). Thus the
sample size estimator used in the MIM Data Entry Module includes an
estimator for this variable. The user should make sure that the 200+
sample size is adequate to confidently predict percent fines and average
particle sizes. Substrate metrics include: Percent finer than 6mm (1/4 inch
in diameter), median particle size (D50), and an estimate of the Mannings
roughness coefficient. The latter is used in calculations of estimated

31

discharge, as part of the pool quality index, and as an indicator of the
channel's ability to dissipate stream energy.

Procedure

Beginning with the second plot in the survey, samples are collected at every
other water-width/depth transect (or 20 total transects) evenly spaced along
the entire length of the DMA. Collect and measure the diameter of 1 0
pebbles at each transect.

1. Visually estimate the number of heel-to-toe steps across the wetted width
totaling 10 (5 heel and 5 toe samples) and pace accordingly. For very
small streams, cross once then return and collect 5 samples on each
crossing of the channel. Sample the entire streambed width at each
transect starting with the heel of the boot at the greeline. Never sample a
particle on the streambank above the greenline or on slump blocks.
Depositional features (e.g. point bars) are considered streambed material.

2. End the count at the greenline on the opposite side of the stream.

Sample the particle at the toe (or heel) of the foot. Reach down with the
forefinger (without looking at the sample point) and pick up the first particle
touched. Measure the middle width (Intermediate or "B" axis) of the particle
in mm. Visualize the B axis as the smallest width of a hole that the particle
could pass through. A gravelometer is an excellent tool for objectively
measuring particle sizes and is highly recommended to avoid subjectivity.

A complete description of the device is available in the Stream Systems
Technology Center - Stream Notes for April, 1996 (on-line at:
http://stream.fs.fed.us/news/streamnt/pdf/SN 4-96.pdf). Commercial
sources are available for purchasing this instrument at approximately $50.00
each.

DATA INTERPRETATION

Data must be interpreted within the precision and accuracy for each
monitoring indicator. Precision denotes the amount of agreement between
repeated measurements by the same observer and/or different observes. It
reflects both the expertise of the observers and the rigor of the procedure.
Accuracy is the amount of agreement between the estimate and the true
mean value, usually reflecting the number of samples collected and the
variability of the site. Sample size estimates are used to evaluate each
monitoring indicator to estimate accuracy. See Appendix N for statistical
analysis of testing of monitoring results ranges of precision, and sample
sizes needed to accurately predict means. Electronic data entry may be used
to assess sample size levels using an EXCEL workbook, the Data Entry
Module, which is designed for use with PDA's (including conversion to
Micro EXCEL). See appendix E for details.

32

Seventeen metrics were created to evaluate and summarize the data. These
metrics are calculated using an EXCEL workbook, the Data Analysis
Module. A description of the module is contained in appendix E. Refer to
the Module for a description of each metric and how it is calculated.

Since all of the measures contain variability, both in accuracy and precision,
conclusions reached must take into account this factor. Each indicator
measured has a different level of precision and accuracy. Known levels are
presented in the following discussion.

Discussion and Interpretation of Metrics

Vegetation along the greenline is usually the first indicator of change along
streambanks. It can indicate increases or decreases in the desired species
and is closely associated with streambank stability, residual vegetation
height, woody species use, woody species regeneration, and greenline-to-
greenline width. Greenline vegetation composition is expressed as percent
dominant vegetation or community types, including anchored rock and
wood, along the greenline. Additional information includes co-dominant
and sub-dominant species. From this data and species data contained in
Appendices H and I the ecological status, vegetation erosion resistance
rating (Winward 2000) and wetland rating (Coles-Ritchie 2005) may be
calculated.

1. Successional Status - Ecological Status

Successional status (Winward 2000) is weighted by the percentage of plants
by serai state along greenline (see Table 6). Anchored rock and anchored
wood are considered as late serai. Serai state vegetation data must be
included for any new species added to the dominant or community type list
for the analysis module to operate correctly. Local riparian plant
association or community publications usually provide that type of
information. The following table summarizes class ratings for ranges of
ecological status as reflected by the serai status of the plant or community
type, substrate, stream gradient, and presence/absence of the woody
vegetation component (see Winward 2000).

Table 6- Greenline Ecological Status (Winward 2000)

Summary Value

Descriptor Class Rating

0-15

Very Early

16-40

Early

41-60

Mid

61-85

Late

85+

PNC

33

Ranges of variability between observers produced an average difference of
1 3. However when samples are repeated by the same observer, the
difference between repeat samples averages 8 (on a scale of 0 to 100).

2. Vegetation Erosion Resistance Rating (Greeniine stability

Rating)

The vegetation erosion resistance rating (synonymous with "Greeniine
Stability Rating" Winward 2000) is based on the relative root strength of
various plant species and combination of plant species along with rock and
wood. Computations result in a weighted average for the transect.
Generally an average over 7 is considered adequate to protect the
streambank and allow streams to function properly (see Table 7). Some
early serai species such as Eleocharis spp. and arroyo willow (Salix
lasiolepisis) growing together along the greeniine provide a higher erosion
resistance rating of 7 (see Appendices H and I).

Table 7- Vegetation Erosion Resistance Index

(referred to as the "Greeniine Stability Rating" in Winward 2000)

Summary Value

Descriptor Class Rating

0-2

Very Poor (very low)

3-4

Poor (low)

5-6

Moderate

7-8

Good (high)

9-10

Excellent (very high)

Ranges of variability between observers produced an average difference of
1 .29. However when samples are repeated by the same observer, the
difference between repeat samples averages .75 (on a scale of 1 to 10).

3. Wetland Rating

The wetland rating (Coles-Ritchie 2005) is a weighted number (see Table 8)
based on the wetland indicator status (Reed 1988 and USDI, Fish and
Wildlife Service 1993). The wetland indicator status (Table 8) is the
frequency that individual plant species occurs in saturated (hydric) soils.
For descriptive purposes only, these have been categorized according to
Table 9.

Depending only on the values generated by the procedures described above
may not give an adequate depiction of the condition of a vegetation
community (including anchored rock and anchored wood). Careful review
of all species described is important and should be considered in every data
interpretation.

Vegetation communities in transition may be deceptive if only dominant
vegetation is considered. Those interpreting the data must also consider

34

sub-dominant species as these species frequently provide valuable
indicators of potential change. For example, if Nebraska sedge (C.
nebraskensis) is present in a site dominated by Kentucky bluegrass (P.
pratensis) and/or red top {Agrostis stolonifera), it indicates the potential for
deep-rooted species to dominate the site. Vigorous Nebraska sedge in the
site described above is usually an indicator of an improving trend. Another
example is undesirable plants such and noxious weeds as a sub-dominant
species may be an indicators of a trend away from the desired condition or
an intermediate step toward the desired condition. It is common for noxious
weeds such as thistles (Circium spp.) to quickly manifest themselves after
long periods of disturbance. Usually these weeds will slowly decline as the
riparian vegetation recovers. Treatment of the weeds may increase the rate
of eradication from the site.

TABLE 8 - Wetland Indicator Status Rating
(Coles-Ritchie 2005)

Wetland

Indicator

Status

Wetland

Indicator

Value

Wetland

Indicator

Status

Wetland

Indicator

Value

OBL

100

FAC-

42

OBL-

92

FACU +

33

FACW +

83

FACU

25

FACW

75

FACU-

17

FACW-

67

UPL +

9

FAC +

58

UPL

0

FAC

50

Because vegetation composition monitoring is usually done long-term, the
same people do not do the measuring each time. This along with the
observer's ability or lack of ability to identify plant species may create a
problem interpreting the data. Those analyzing the data must know the area
and the potential plants species to make correct interpretation of the
condition and trend on the site.

35

Table 9 - Site Wetland Rating

Wetland Indicator
Value

Descriptor Class Rating

0-15

Very Poor

16-40

Poor

41-60

Fair

61-85

Good

85+

Very Good

One method of reducing misidentification is to group riparian plants,
usually by genera, into functional groups by herbaceous, shrubs, and trees.
The relative streambank stability rating (Winward 2000 and Appendices F
and G) provides a method of grouping plants with similar rooting
characteristics. Group plant genera with streambank stability rating of 7 to
10 in the deep-rooted group, ratings 5 and 6 are an intermediate group, and
rating 1 to 4 in the weak-rooted group. The genera Car ex can be
categorized into two groups, strongly rhizomatous (common examples
include beaked sedge (G utriculata) ', Nebraska sedge (C. nebraskensis),
water sedge (C. aquatica), and wooly sedge (C lanuginosa) with ratings of
8 and 9. Carex spp. with shallow rhizomes Douglas sedge(C. douglasii) has
a rating of 4 and tufted or clumped small-winged sedge (C. microptera)
with a rating of 5. In this case, the strong-rooted sedges would be combined
into a class of stabilizers with Douglas sedge as weak-rooted and small-
winged sedge as an intermediate.

Ranges of variability between observers produced an average difference of
12. However when samples are repeated by the same observer, the
difference between repeat samples averages 5 (on a scale of 0 to 100)

4. Streambank Stability (percent streambanks stable and percent
streambanks covered)

The streambank is that portion of the channel between the scour line and the
top of the first terrace on either side of the stream. The streambank stability
measurement provides an indication of the ability of streambanks, with their
associated vegetation, anchored rock, anchored wood, and/or consolidated
soils high in clay or compacted, to buffer the forces of water during high
stream flow, floating ice, or debris. The results are expressed as a
percentage of the stream in each of six classification categories,
covered/stable, covered/unstable, uncovered/unstable, uncovered/stable,
false banks, and unclassified.

Increased streambank stability on disturbed sites usually lags behind the
recovery of herbaceous and woody vegetation. Streambank stability

36

recovery rates will vary depending on the current stage of channel
evolution. Recently incised channels will have a longer recovery rate
because the channel must develop a new floodplain which requires eroding
streambanks to deposit material to create new point bars. This new
deposition must then be occupied by deep-rooted vegetation species before
the streambanks begin to stabilize. This process can take from a few years
to decades to complete.

Consider streambank alteration, greenline vegetation composition, woody
species regeneration, woody species use, and photographs to reach
conclusions concerning the trend of streambank stability.

Ranges of variability between observers produced an average difference of
12. However when samples are repeated by the same observer, the
difference between repeat samples averages 6 (on a scale of 0 to 100).

5. Residual Vegetation (Mean and Median Stubble Height)

Residual vegetation is used as an indicator of the amount of use on
dominant key vegetation species by livestock (it may be used for other large
herbivores when needed) and is not intended to be a use standard or "term
or condition" of a grazing permit or lease. It provides information
concerning whether the current grazing system is allowing adequate
vegetation growth to maintain or enhance vigor and reproduction of the
plants.

Interpretation of residual vegetation is not complicated. The result is the
median (mean or average may be used if desired) height of the residual
vegetation (key species) in inches. Do not interpret the data beyond its
precision and accuracy. For example, 5 inches of residual vegetation height
is determined to be amount necessary to meet the objectives for the site.
The median residual vegetation (key species) height at the prescribed time
(either during the grazing season or after plant growth has stopped and after
livestock grazing had concluded for the season) is 4.7 inches. The precision
and accuracy tests, at the 95 percent confidence level, indicated data was ±
0.5 inches.

Because the measured data (4.7 inches) was within the range of variability
(±, 0.5 inches) it cannot be considered below the recommended height. It
does provide information that the annual grazing is at or below the
recommended level and the long-term (trend) monitoring should be
carefully watched to determine any undesirable changes in the vegetation or
channel conditions. These conditions and concerns must be conveyed to
those involved in livestock management.

37

If the median residual vegetation is 4.2 inehes with the same variability
described above is below the desired use for the prescribed season, these
conditions should trigger a review to determine the reason for not meeting
the desired level of use. This may result in refining the grazing system or
correcting the conditions that lead to not meeting the desired use levels.

Residual vegetation must be used with greenline vegetation composition to
determine if livestock management is moving toward meeting the
objectives. Streambank alteration, streambank stability, and photographs
should also be considered prior to reaching a conclusion concerning the
condition and/or trend.

Ranges of variability between observers produced an average difference of
.9". However when samples are repeated by the same observer, the
difference between repeat samples averages .6" (from data representing a
range of stubble heights from 1 to 40 inches in length).

6. Woody Species Regeneration

Woody species regeneration will likely have the largest variability of any of
the protocols. This is particularly true on greenlines with few woody
species present. Increases in the number and age class, to older age classes,
likely indicate an improving trend. Winward (2000) indicates that most
streams with gradients of more than 0.5 percent have the potential for
woody species. The flatter the stream, the more infrequent are the
conditions for these plants to have seed fall on freshly deposited soil,
germinate, grow a root to the water table, and become established. Changes
on highly disturbed streams devoid of woody species may take 10 to 20
years to repopulate the streambank.

Data from the woody species regeneration and woody species use
procedure, along with photographs; usually provide a good indication of
changes in numbers, size or age, and abundance of the plants. Increasing
numbers of seedlings and young plants may be an indication of early
improvement along the greenline. Changing from seedling and young
plants toward more mature plants is usually an indication of continuing
improvement. When stream channels are developing meanders and point
bars are growing, it is common for an initial establishment of seedlings and
young plants, moving to mature. As the point bar continues to grow,
seedling and young plants then become dominant along the greenline. The
mature plants that were detected are more than one meter from the greenline
and new plants are establishing on the growing point bar.

Ranges of variability between observers has not been evaluated with
Woody Species Regeneration.

38

7. Greenline-to-Greenline Channel Width (GGWj

Greenline-to-greenline channel width is the average non-vegetated distance
between the greenline on either side of the stream. It provides an indicator
of the stream channel width. One expects that as disturbed, usually over-
widened, streams recover, the stream channel will narrow. Objectives
should be developed from reference sites when such information is
available. Narrowing greenline-to-greenline widths are indicators of stream
recovery. Data from GGW should be used with greenline vegetation
composition, streambank stability, streambank alteration, and residual
vegetation height.

Ranges of variability between observers produced an average difference of
.57 meter. However when samples are repeated by the same observer, the
difference between repeat samples averages .24 meter (in a data set ranging
from .5 to 20 meters in greenline to greenline width).

8. Woody Species Use

Woody species use estimates are made class, none to slight, light, moderate,
heavy to severe, and extreme (see Table 5). The degree of use should not
be interpreted to a finer scale. For example, if the average calculated use is
59 percent, the conclusion should be that the use is moderate to heavy. Or
if the use is 41 percent, the conclusion should be that the use is light to
moderate. Woody species use indicators should be set by use class and not
by specific numbers such as 35 percent.

Ranges of variability between observers produced an average difference of

8. However when samples are repeated by the same observer, the
difference between repeat samples averages 5 (on a scale of 0 to 100).

9. Thalweg Depth Variation Index

As used by Madej (1999), the Depth Variation Index is simply the standard
deviation of thalweg depth measurements. Therefore it is a statistical
measure of the spread or variability in water depths along the length of the
stream. The greater the variability, presumably the greater the habitat
complexity and quality. Because streams are variable in water depth as
streamflow rate changes temporally, the standard deviation is indexed to the
average depth of the stream. Thus in the Data Analysis Module the
"Thalweg Depth Variation Index" is calculated using the Coefficient of
Variation, or ratio of the standard deviation to the arithmetic mean of all
depth measurements. The coefficient of variation is a dimensionless
number that allows comparison of samples through time while minimizing
the effect of streamflow level on the variation of thalweg depths.

39

t

Ranges of variability between observers have not yet been evaluated for this
metric.

10. Water Width-Maximum Depth Ratio

This metric is calculated by dividing the average water width by the average

thalweg depth. The VV/D ratio indexes the shape of the wetted channel,

whether narrow and deep, or wide and shallow. Because streams are

variable in both width and depth, this dimensionless index allows

comparisons of samples through time. The assumption here is that MIM *

samples are ALWAYS collected in late summer when streams are usually

flowing within the active channel and within a relatively narrow range of

discharge. In such conditions depth changes are proportional to width ^

changes. Thus as channels tend towards stability the index value decreases.

As channels de-stabilize the index value increases. However if the channel %

is strongly entrenched (vertical banks), widths may not change with changes

in depth. In this case, variability in the W/D ratio through time would

reflect changes in discharge.

Ranges of variability between observers have not yet been evaluated for this
metric.

11. Percent Substrate Fines (<6mm)

Surface fines represent that fraction of the pebbles sampled less than 10mm
in size, Kondoff (2000) , in evaluating the biological significance of
substrate for salmonid fishes, recommended using less than 10mm (.39
inch) as the fraction that would potentially affect salmonid fry emergence.
This means that pebbles fitting the 1, 2.8, 4, 5.6, and 8mm slots in the
gravelometer would be considered fine sediment. On the Wentworth Scale,
particles less than 10mm are the fine gravel and smaller substrate types.

Ranges of variability between observers have not yet been evaluated for this
metric.

12. Median Substrate Particle Size Diameter (D50)

This metric is the median value for all pebbles in the sample. The median is
that particle diameter for which 50% of all particles are smaller in size. As
stream channels stabilize through riparian vegetation restoration and
increased bank stability, the D50 size normally increases. As channels
stabilize, they resist erosion, tend towards a narrower and deeper profile
allowing higher levels of bed scour, and increase in sediment transport
capability. These physical variables combine in determining the coarseness
of the substrate.

40

13. Discharge

Discharge is the flow of water, in cubic feet per second, passing in a stream
channel. It is calculated by multiplying the cross-sectional area of the
wetted stream channel by the water velocity, or FtA2 x Ft/second, thus
FtA3/Second. Discharge can be estimated using Mannings Equation, which
is an empirical estimation that is derived from the channel velocity, flow
area and channel slope. Channel velocity is determined from the wetted
perimeter (length of the wetted streambed perpendicular to the flow
direction) and from Mannings n, a coefficient that represents friction.
Mannings n is called the "roughness coefficient" and can be estimated from
substrate data. Table 1 in the Data Analysis Module - Substrate worksheet
shows the n values that are applied to various D50 sizes calculated from the
Pebble Count data. Thus discharge is estimated from field information on
water width, depth, and substrate particle size. It is used to approximate the
streamflow rate at the time of the survey. Streamflow differences between
sampling may be important in interpreting trends in Width-to-Depth ratio
and the Thalweg Depth Variation Index.

14. Roughness coefficient

Derivation of the Mannings roughness coefficient is described above in the
section on discharge. Mannings n is presented as a metric that has bearing
on hydraulic friction in the channel and indexes substrate quality. If the
roughness coefficient changes through time, such shifts are reflective of the
channel's ability to transport water and sediment.

15. Pool Quality Index

High frequency of good quality pools is critical to sustaining salmonids in
streams and rivers (Bauer and Ralph 1999). They are used at virtually
every life stage, and are critical to providing "space" for rearing, feeding,
resting, spawning, and incubation. A thalweg depth of .3 meter is
considered critical as cover for salmonids. Substrate is a critical
component of pool habitat for salmonids, particularly for juvenile over-
winter rearing. The larger the D50 size, the greater amount of cover is
available. Thus the Pool Quality Index is calculated from a substrate score
using both percent thalweg deeper than .3 meter, and the D50 particle size.
The following table (Table 10) describes scores applied to the Pool Quality
Index:

41

Table 10. Water Depth and Substrate Scores used to calculate the
Pool Quality Index.

% Deeper
than .3 meter

Depth Score

D50

Substrate
Score

> 50%

5

> 180 mm

5

30 - 50%

4

64-180 mm

4

20 - 30%

3

32 - 64 mm

3

10-20%

2

16-32 mm

2

5% -10%

1

8- 16 mm

1

<5%

0

< 8 mm

0

The depth score is added to the substrate score, and the total is multiplied by
10 to derive the Pool Quality Index. This index ranges from 0 to 100.

16. Photographs

Photographs described in this protocol are designed to help validate data
obtained using measured and observed protocols described in this
document. They are not intended to be adequate to provide quantitative
data.

17. PFC Calibration

We suggest that the MIM protocols can be used to validate Riparian Proper
Functioning Condition (PFC) Assessments. PFC assesses a much broader
reach of stream, however, it is a qualitative method for assessing the
condition of riparian-wetland areas, and is not designed to be a long-term
trend monitoring tool. The PFC assessment uses hydrology, vegetation, and
erosion/deposition (soils) attributes and processes to qualitatively assess the
condition of riparian-wetland areas. Many of these same attributes can be
quantitatively measured using the MIM procedure. Procedures for PFC
assessment are found in the BLM Technical Reference 1737-15, Riparian
Area Management; A User Guide to Proper Functioning Condition and the
Supporting Science for Lotic Areas.

Use the Data Analysis Module to calibrate PFC ratings. Column N in the
Data Summary Worksheet (located in the Data Analysis Module), presents
quantitative values for several of the checklist items in the "Users Guide for
Assessing Proper Functioning Condition and the Supporting Science for
Lotic Areas" (Technical Reference 173 7- 15, USDI BLM 1998). As stated
in 1737-15: "...there will be times when items from the checklist need to
be quantified. " Also: "These quantitative techniques are encouraged in
conjunction with the PFC assessment for individual calibration, where
answers are uncertain, or where experience is limited." The Calibration
Table in the Data Analysis Module provides a listing of indicators and their

42

quantitative values for the applicable checklist item(s) along with a note
describing the indicator's relevance to the item.

18. Winward Greenline Calibration (Winward 2000)

The Data Analysis Module contains a calibration for predicting the
vegetation metrics using the Winward (2000) method. This calibration is
intended for those users who desire to predict trends using MIM, where
previous samples were collected using the Winward (2000) method. Data
for developing the calibration model were collected in 2006 from 3 1
samples. These samples were derived from a variety of stream/riparian
types across southern and central Idaho.

43

REFERENCES

Archer, E.K., Roper, B.B, R.C. Henderson, N. Bouwes, S.C. Mellison, and J.L.
Kershner. 2002. Testing common stream sampling methods: How useful are
these techniques for broad-scale, long-term monitoring? U. S. Department of
Agriculture, Forest Service, Fish and Aquatic Ecology Unit, Logan, UT.
GTR-0602.

Bauer, S.B. and S.C. Ralph. 2001. Strengthening the use of aquatic habitat

indicators in Clean Water Act programs. Fisheries Vol 26, No. 6. pp 14 to 24.

Bauer, S.B. and T.A. Burton. 1993. Monitoring protocols to evaluate water quality
effects of grazing management on western rangeland streams. Idaho Water
Resources Research Institute; for US EPA. EPA 9 1 0/R-93-0 1 7.

Benngeyfield, P. and D. Svoboda. 1998. Determining allowable use levels for
livestock movement in riparian areas. Proceedings: Specialty Conference on
Rangeland Management and Water Resources. American Water Resources
Association. Middleburg, VA.

Bohn, C. 1986. Biological importance of streambank stability. Rangelands 8:55-
56.

Bunte, K. and S.R. Abt. 2002. Sampling Surface and Sub-Surface Particle Size
Distributions in Wadeable Gravel- and Cobble-Bed Streams for Analysis in
Sediment Transport, Hydraulics, and Streambed Monitoring. USDA Forest
Service, Rocky Mountain Experiment Station, General Technical Report,
RMRS-GTR-74. 450 pp.

Burton, T. 1999. Bank stability monitoring in Bear Valley Basin - an overview.
USDA, Forest Service, Boise National Forest. Unpublished.

Challis Resource Area. 1999. Photographic guide to median stubble heights.
Technical Bulletin No. 99-01. Idaho Bureau of Land Management, Boise,
Idaho.

Clary, W.P. 1999. Stream channel and vegetation responses to late spring cattle
grazing. Journal of Range Management 52 - 3.218-227. May 1999.

Clary, W.P. and B.F. Webster. 1989. Managing grazing of riparian areas in the
Intermountain Region. USDA, Forest Service, Intermountain Research
Station, General Technical Report INT-263, Ogden, UT.

Clary, W.P., C.I. Thornton, and S.R. Abt. 1996. Riparian stubble height and
recovery of

degraded streambanks. Rangelands 18:137-140.

Clary , W.P., and J.W. Kinney. 2002. Streambank and vegetation response to
simulated cattle grazing. Wetlands, Vol 22, No. 1. pp 139-148.

44

Coles-Ritchie, M.C., R.C. Henderson, E.K.Archer, C. Kennedy, and J.L. Kershner.
2004. The Repeatability of Riparian Vegetation Sampling Methods: How
Useful are These Techniques for Broad-scale, Long-term Monitoring? Gen.
Tech. Rep. RMRS-GTR-138. Fort Collins, CO. U. S. Department of
Agriculture, Forest Service, Rocky Mountain Experiment Station. 18 p.

Coles-Ritchie, Marc C. Utah State University. 2005. Evaluation of riparian

vegetation data and associated sampling techniques. Utah State University,
Logan UT. 184 p.

Cowley, E.R. 2004. Monitoring the current year streambank alteration by large
herbivores. Unpublished Report. Bureau of Land Management, Idaho State
Office. Boise, ID

Dunne, T and L.B. Leopold. 1978. Water in environmental planning. W.H.
Freeman and Co., San Francisco, CA. pp 818.

Gordon, N.D., T.A. McMahon, and B.L. Finlayson. 1993. Stream hydrology, an

introduction for ecologists. John Wiley & Sons, Ltd. West Sussex, England, pp

337-338.

Hansen, P.L., R.D. Pfister, K. Boggs, B.J. Cook, J. Joy, and D.K. Kinckley. 1995.
Classification and management of Montana's riparian and wetland sites.
Montana Forest and Conservation Experiment Station, School of Forestry, The
University of Montana, Miscellaneous Publication No. 54, Missoula, MT. p.
640.

Harelson, C.C., C.L. Rawlins, and J.P. Potyondy. Stream channel reference sites: an
illustrated guide to field techniques. Gen. Tech. Rep. RM-245. Fort Collins,
CO: U.S. Department of Agriculture.

Heitke, J. and R. Henderston. 2004. Precision of three streambank alteration

assessment methods. Salt Lake City, Utah. Society for Range Management
Annual Meeting.

Henderson, R. 2004. U.S. Forest Service. Personnel Communications.

Interagency Technical Reference. 1996. Utilization studies and residual

measurements. Interagency Technical Reference. BLM/RS/ST-96/004+1730.

pp 2-5, 51-56.

Kaufman, J.B. and W.C. Krueger. 1984. Livestock impacts on riparian plant

communities, and streamside management implications, A Review. Journal of
Range Management 37(3):430-437.

45

Kershner, J.L., O.K. Archer, M. Coles-Ritchie, E.R. Cowley, R.C. Henderson, K.
Kratz, CM. Quimby, D.L. Turner, L.C. Ulmcr, and M.R. Vinson. 2004. Guide
to effective monitoring of aquatic and riparian resources. Gen. Tech. Rep.
RMRS-GTR- 121. Fort Collins, CO: U.S. Department of Agriculture, Rocky
Mountain Research Station. 57p.

Kondoff, G.M. 2000. Assessing Salmonid Spawning Gravel Quality. Transactions
American Fisheries Society. Volume 129, Issue 1. pp 262-281.

Leopold, L.B. 1994. A view of the river. Harvard University Press, Cambridge, MA.
pp 131-133.

Madej M. 1999. What can Thalweg Profiles Tell Us. A Case Study from

Redwood Creek, California. US Geological Survey, Redwood Field Station,
Areata, CA.

Miller, J.R., K. House, D. Germanoski, R.J. Tausch, and J.C. Chambers. 2004.
Fluvial geomorphic responses to Holocene climatic change. In: Great basin
riparian ecosystem: ecology, management, and restoration, Eds: J.C.
Chambers and J.R. Miller. Society for Ecological Restoration International.
Island Press, Washington, D.C. pp 49-87.

McHugh P. and P. Budy. 2005. A comparison of visual and Measurement-Based
Techniques for Quantifying Cobble Embeddedness and Fine Sediment Levels
in Salmonid-Bearing Streams. North American Journal of Fisheries
Management. Volume 25: pp 1208-1215. American Fisheries Society.

Platts, W.S. 1991. Livestock grazing. In: Influences of forest and rangeland
management on salmonid fishes and their habitats, Ed: W.R. Meehan.
American Fisheries Society Special Publication 19. American Fisheries
Society. Bethesda, MD. pp 389-423.

Platts, W.S., C. Armour, G.D. Booth, M. Bryant, J.L. Bufford, P.Cuplin, S. Jensen,
G.W. Lienkaemper, G.W. Minshall, S.B. Monson, J.R. Sedell, and J.S. Tuhy.
1987. Methods for evaluating riparian habitats with applications to
management. U.S. Department of Agriculture, Forest Service, Intermountain
Research Station, General Technical Report INT-22 1 . Ogden, UT.

Reed, Porter B. 1988. National list of plant species that occurs in wetlands: 1988
national summary. USDI, Fish and Wildlife Service.
<http://www.fws.gov/nwi/bha/list88.html>
Accessed 2006 April 9.

Rosgen, D. 1996. Applied river morphology. Wildland Hydrology. Pagosa Springs,
CO.

Thorne, C.R. 1982. Processes and mechanisms of river bank erosion. In: Gravel bed
rivers. Eds: Hey, R.D., Bathurst, J.C. and Thorne, C.R. John Wiley and Sons
Ltd. New York, New York, pp 227-27 1 .

46

Thome, M.S., P.J. Meiman, Q.D. Skinner, M.A. Smith, and J.L. Dodd. 2005.

Clipping frequency affects canopy volume and biomass production in planeleaf
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Management 58( 1 ):4 1 -50.

University of Idaho Stubble Height Study Team. 2004. University of Idaho stubble
height study report. Submitted to Idaho State Director, BLM and Regional
Forester, Region 4, US Forest Service. University of Idaho Forest, Wildlife and
Range Experiment Station, Moscow, ID. 26p.

USDI, Bureau of Land Management. 1992. Rangeland inventory & monitoring
supplemental studies. Technical Reference 4400-5, Denver, CO. p 87.

USDI, Bureau of Land Management. 1996. Riparian area management: process for
assessing proper functioning condition. Technical Reference 1737-9, National
Applied Science Center, Denver, CO.

USDI, Bureau of Land Management. 1998. Riparian area management: a user guide
to assessing proper functioning condition and the supporting science for lotic
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CO.

USDI, Bureau of Land Management. 1999. Photographic guide to median stubble
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wetlands: northwest region 9 supplement.
http://www.fws.gov/nwi/bha/Iist88.html
Access 2006 April 9.

Winward, A.H. 2000. Monitoring the vegetation resources in riparian areas. Gen.
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Forest Service, Rocky Mountain Research Station. 49p.

)

Winward, A.H. 2000. Trend monitoring of riparian vegetation. California
Rangeland Interagency Video Series. 24 minutes 06 seconds.

Woodsmith, R.D.; Noel, J.R., Dilger, M.L. 2005. An approach to effectiveness
monitoring offloodplain channel aquatic habitat: channel condition
assessment. Landscape and Urban Planning. 72: 177-204.

Zar, J.H. 1996. Biological Analysis. Prentice Hall, Englewood Cliffs, N.J.

47

APPENDIX A - Selecting the DMA and Monitoring Indicators

Selecting the Designated Monitoring Area (DMA) and Monitoring
Indicators

1 . The DMA should be established appropriate to the monitoring
indicators as described in Appendix B.

3. While the term "DMA" originated with grazing management
applications, DMAs may be located in areas to monitor
recreation impacts, the effects of roads, and other activities. A

DMA may also be selected to serve as a reference reach to help
determine the potential and capability of a stream.

4. The DMA should not reflect an "average" amount of use in all
riparian areas of the stream reaches in the pasture but rather reflect
livestock use in only those stream reaches where livestock are
actually using riparian areas. A reach with relatively high use
may be chosen to more easily detect change and assure
compliance pasture-wide. Premise: "If proper management
occurs on the area, the remainder of the pasture or use area will
also be managed within requirements."

5. Select from those areas that are most critical in influencing
fish (or other riparian-dependant) species and where those
areas overlap with grazing use; e.g.:

a. Listed/sensitive fish species habitat

b. Spawning habitat

c. Critical over wintering or rearing habitat

6. Avoid areas compounded by other activity types or by non-
USFS or BLM (private) activities. The purpose is to monitor trends
due to the target federal management activity.

7. Avoid sites that are impervious to disturbance (e.g., rock-
armored channels) or those intentionally established for
concentrated use (e.g., water gaps).

8. Select DMAs in an interdisciplinary fashion, including specialists
knowledgeable in fish habitat requirements, channel processes,
riparian vegetation, and livestock grazing, to assure that the site
characteristics are not abnormal or unique as compared to the rest
of the riparian area in the pasture. This also assures the
appropriate "Riparian Complex" is monitored as described in item 9,
below.

A-1

APPENDIX A - Selecting the DMA and Monitoring Indicators

9. Select DMAs according to the appropriate "Riparian Complex".

Monitoring must be conducted within the same Riparian Complex (Winward
2000). Riparian complexes are defined by overall geomorphology, substrate
characteristics, stream gradient, and vegetation patterns along the stream.
They develop and function in response to interacting features of valley
bottom gradient; substrate or soil characteristics; valley bottom width;
elevation; and climate. Once the Riparian Complex is defined, the DMA
should be located by an ID Team to "best represent influences of major
activities in that complex" (Winward 2000).

SUGGESTED PROCEDURE

Step 1. Define the Riparian Complex(s) within the Pasture

Obtain information on the stream within the pasture in the office using USGS
topographic map(s), aerial photo(s), and soils or landtype inventories.

1 . Graph the stream profile; note average grades and breaks; classify
the stream gradient type using Rosgen's criteria (Table A1 ).

2. Evaluate valley width, noting any abrupt changes within the
pasture. Classify the Valley Type using Rosgen's Valley
Morphology classification (Table A2).

3. Determine the dominant soil family type from the Soils Inventory or
Landtype maps, noting key substrate characteristics - texture,
potential vegetation, flooding, etc.

4. Evaluate vegetation patterns along the stream noting key groupings
of woody types and herbaceous types where possible from the
photos.

5 Map the Riparian Complexes within the pasture based upon
changes in Stream Gradient Type, Valley Type, and/or Dominant
Soil Families.

Step 2. Define the Appropriate Monitoring Indicators for the Riparian
Complex

1 . Use the outline in Appendix B to select the monitoring indicators
appropriate to the Stream Gradient type and vegetation cover type
in the riparian complex

Step 3. Locate the Designated Monitoring Area and Transect in the
Field

1 . Walk through the Riparian Complex in the pasture to be monitored.

2. Validate the mapped Riparian Complex and adjust descriptions as
necessary

A-2

APPENDIX A - Selecting the DMA and Monitoring Indicators

3. Evaluate grazing use along and adjacent to the stream. Note
where use occurs and the types of use - herbaceous and/or woody
browse. Use a "USE PATTERN MAP" if available.

4. Select a monitoring reach typical of the grazing use and that
overlaps any critical aquatic habitat - spawning and/or early rearing
reaches, etc.

a. Make sure it does not include a cattle crossing or local
point of concentration

b. The starting point for the transect may be randomly
selected by going to the downstream end of the reach,
selecting a random number between 1 and 10, and then
pacing-off that number of steps upstream.

c. At the starting point place a stake adjacent to the stream
and well back from the edges of any cutbanks. The stake
should be located above the bankful elevation of the
stream.

d. Place a stake to demark the ending point of the transect
across the stream from the starting point (the transect will
proceed upstream from the starting point a distance of at
least 363 feet, cross the stream and proceed from that
point downstream to a stake located across the stream
from the starting point).

e. Place stakes on each bank at the upstream end of the
reach to define the transect extent.

f. If multiple channels are encountered, the current, most
active channel should be followed. Do not sample
streambanks on islands in the stream.

A-3

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APPENDIX B-Guide to the Selection of Monitoring Indicators

The following Guide can be used to prescribe streamside monitoring
indicators appropriate for various channel types (Rosgen, 1996), and existing
and potential vegetative conditions along the greenline.

I. "C" channel type, herbaceous vegetation dominant, potential
vegetation: herbaceous or mixed herbaceous and shrubs.

TRIGGER: Within-season trigger to move livestock, to maintain
or increase vigor on key hydric stabilizers:

o £tubble height on key riparian species, or species groups
On the greenline

o Use eompliance (livestock numbers and time in pasture).

o Bank disturbance or alteration
ENDPOINT: End-of-season indicator of proper use to maintain
or ensure increased composition key hydric stablizers:

o Stubble height on key riparian species, or species groups
on the greenline

o Bank disturbance or alteration
RIPARIAN OBJECTIVE: Long-term indicator of riparian
condition to assess attainment of the Riparian Management
Objectives:

o Streambank stability

o Greenline composition maintained or trend toward hydric
stablizers
STREAM CHANNEL: Long-term indicators of stream channel
condition to assess attainment of the Riparian Management
Objectives:

o Greenline-greenline width

o Thalweg water depth with water width

o Pebble count (substrate composition)

B-1

APPENDIX B-Guide to the Selection of Monitoring Indicators

II. "C" channel type, mixed shrub - herbaceous vegetation dominant,
potential vegetation: mixed herbaceous and shrubs, or shrubs.

TRIGGER: Within-season trigger to move livestock, to maintain
or increase vigor on key hydric stabilizers:

o Stubble height on key riparian species or species groups
on the greenline

o Use compliance (livestock numbers and time in pasture).

o Bank disturbance or alteration

o Change in preference to woody species sprouts and young
ENDPOINT: End-of-season indicator of proper use to maintain
or ensure increased composition key hydric stabilizers:

o Stubble height on key riparian species or species groups
on the greenline

o Bank disturbance or alteration

o Woody species use on sprouts and young (less than 5 feet
above ground)
RIPARIAN OBJECTIVE: Long-term indicator of riparian
condition to assess attainment of the Riparian Management
Objectives:

o Streambank stability

o Greenline composition maintained or trend toward hydric
stabilizers

o Woody species regeneration - 15-20% sprouts and young,
60-70% mature, and 15-20% dead
STREAM CHANNEL: Long-term indicators of stream channel
condition to assess attainment of the Riparian Management
Objectives:

o Greenline-greenline width

o Thalweg water depth with water width

o Pebble count (substrate composition)

B-2

APPENDIX B--Guide to the Selection of Monitoring Indicators

III. "C" channel type, woody dominant, potential vegetation: shrubs
and trees.

TRIGGER: Within-season trigger to move livestock, to maintain
or increase vigor on key hydric stabilizers:

o Use compliance (livestock numbers and time in pasture).

o Bank disturbance or alteration

o Change in preference to woody species sprouts and young
ENDPOINT: End-of-season indicator of proper use to maintain
or ensure increased composition key hydric stabilizers:

o Bank disturbance or alteration

o Woody species use on sprouts and young (less than 5 feet
above ground)
RIPARIAN OBJECTIVE: Long-term indicator of riparian
condition to assess attainment of the Riparian Management
Objectives:

o Streambank stability

o Woody species regeneration - 15-20% sprouts and young,
60-70% mature, and 15-20% dead
STREAM CHANNEL: Long-term indicators of stream channel
condition to assess attainment of the Riparian Management
Objectives:

o Thalweg water depth with water width

o Pebble count (substrate composition)

B-3

APPENDIX B-Guide to the Selection of Monitoring Indicators

IV. "E" channel type, herbaceous vegetation dominant, potential
vegetation: herbaceous or mixed herbaceous and shrubs.

TRIGGER: Within-season trigger to move livestock, to maintain
or increase vigor on key hydric stabilizers:

o Stubble height on key riparian species, or species groups
on the greenline

o Use compliance (livestock numbers and time in pasture).

o Bank disturbance or alteration
ENDPOINT: End-of-season indicator of proper use to maintain
or ensure increased composition key hydric stabilizers:

o Stubble height on key riparian species, or species groups
on the greenline

o Bank disturbance or alteration.
RIPARIAN OBJECTIVE: Long-term indicator of riparian
condition to assess attainment of the Riparian Management
Objectives

o Streambank stability

o Greenline composition maintained or trend toward hydric
stabilizers
STREAM CHANNEL: Long-term indicators of stream channel
condition to assess attainment of the Riparian Management
Objectives:

o Greenline-greenline width

o Thalweg water depth with water width

o Pebble count (substrate composition)

B-4

APPENDIX B-Guide to the Selection of Monitoring Indicators

V. "F" channel type (entrenched floodplain), herbaceous vegetation
dominant, potential vegetation: herbaceous or mixed herbaceous
and shrubs.

-

TRIGGER: Within-season trigger to move livestock, to maintain
or increase vigor on key hydric stabilizers:

o Stubble height on key riparian specie, or species groups s
on the greenline

o Use compliance (livestock numbers and time in pasture).

o Bank disturbance or alteration
ENDPOINT: End-of-season indicator of proper use to maintain
or ensure increased composition key hydric stabilizers:

o Stubble height on key riparian species, or species groups
on the greenline

o Bank disturbance or alteration
RIPARIAN OBJECTIVE: Long-term indicator of riparian
condition to assess attainment of the Riparian Management
Objectives:

o Streambank stability

o Greenline composition maintained or trend toward hydric
stabilizers
STREAM CHANNEL: Long-term indicators of stream channel
condition to assess attainment of the Riparian Management
Objectives:

o Greenline-greenline width

o Thalweg water depth with water width

o Pebble count (substrate composition)

B-5

APPENDIX B--Guide to the Selection of Monitoring Indicators

VI. "G" channel type (entrenched - no floodplain), herbaceous
vegetation or bare banks dominant. Potential vegetation:
herbaceous.

TRIGGER: Within-season trigger to move livestock, to maintain
or increase vigor on key hydric stabilizers:

o Use compliance (livestock numbers and time in pasture)

o Bank disturbance or alteration
ENDPOINT: End-of-season indicator of proper use to maintain
or ensure increased composition key hydric stabilizers:

o Bank disturbance or alteration
RIPARIAN OBJECTIVE: Long-term indicator of riparian
condition to assess attainment of the Riparian Management
Objectives:

o Streambank stability

o Greenline composition maintained or trend toward hydric
stabilizers
STREAM CHANNEL: Long-term indicators of stream channel
condition to assess attainment of the Riparian Management
Objectives:

o Greenline-greenline width

o Thalweg water depth with water width

o Pebble count (substrate composition)

B-6

APPENDIX B-Guide to the Selection of Monitoring Indicators

VI. "B" channel type, mixed shrub - herbaceous vegetation dominant,
potential vegetation: mixed herbaceous and shrubs, or shrubs.

TRIGGER: Within-season trigger to move livestock, to maintain
or increase vigor on key hydric stabilizers:

o Stubble height on key riparian species, or species groups
on the greenline

o Use compliance (livestock numbers and time in pasture)

o Bank disturbance or alteration

o Change in preference to woody species sprouts and young
ENDPOINT: End-of-season indicator of proper use to maintain
or ensure increased composition key hydric stabilizers:

o Stubble height on key riparian species, or species groups
on the greenline

o Bank disturbance or alteration

o Woody species use on sprouts and young (less than 5 feet
above ground)
RIPARIAN OBJECTIVE: Long-term indicator of riparian
condition to assess attainment of the Riparian Management
Objectives:

o Streambank stability

o Greenline composition maintained or trend toward hydric
stabilizers

o Woody species regeneration - 15-20% sprouts and young,
60-70% mature, and 15-20% dead
STREAM CHANNEL: Long-term indicators of stream channel
condition to assess attainment of the Riparian Management
Objectives:

o Greenline-greenline width

o Thalweg water depth with water width

o Pebble count (substrate composition)

B-7

APPENDIX B--Guide to the Selection of Monitoring Indicators

VII. "B" channel type, woody dominant, potential vegetation: Shrubs
and trees.

TRIGGER: Within-season trigger to move livestock, to maintain
or increase vigor on key hydric stabilizers:

o Use compliance (livestock numbers and time in pasture)

o Bank disturbance or alteration
ENDPOINT: End-of-season indicator of proper use to maintain
or ensure increased composition key hydric stabilizers:

o Bank disturbance or alteration

o Woody species use on sprouts and young (less than 5 feet
above ground)
RIPARIAN OBJECTIVE: Long-term indicator of riparian
condition to assess attainment of the Riparian Management
Objectives

o Streambank stability

o Woody species regeneration - 15-20% sprouts and young,
60-70% mature, and 15-20% dead
STREAM CHANNEL: Long-term indicators of stream channel
condition to assess attainment of the Riparian Management
Objectives:

o Greenline-greenline width

o Thalweg water depth with water width

o Pebble count (substrate composition)

B-8

APPENDIX B-Guide to the Selection of Monitoring Indicators

VIII. "A" channel. Mixed shrubs and herbaceous, or shrubs dominant.
Potential vegetation: mixed shrubs and herbaceous, or shrubs.
Substrate large.

TRIGGER: Within-season trigger to move livestock, to maintain or
increase vigor on key hydric stabilizers:

o Use compliance (livestock numbers and time in pasture).

o Bank disturbance or alteration

o Change in preference to woody species sprouts and young

• ENDPOINT: End-of-season indicator of proper use to maintain
or ensure increased composition key hydric stabilizers:

o Bank disturbance or alteration

o Woody vegetation use on sprouts and young (less than 5
feet above ground)

• RIPARIAN OBJECTIVE: Long-term indicator of riparian
condition to assess attainment of the Riparian Management
Objectives

o Streambank stability

o Woody species regeneration - 15-20% sprouts and young,
60-70% mature, and 15-20% dead

• STREAM CHANNEL: Long-term indicators of stream channel
condition to assess attainment of the Riparian Management
Objectives:

o Greenline-greenline width

o Thalweg water depth with water width

o Pebble count (substrate composition)

Herbaceous vegetation does not normally contribute significantly to the
stability of A channels. The rare exception would likely be associated with A5
and A6 channel types. A5's are steep channels incised in sandy materials
and that occur on highly weathered granites or sedimentary rocks. Such
channels often experience natural bank erosion through fluvial and earth flow
processes. A6's are steep, entrenched channels in weathered shales and
lacustrine soils that are very cohesive.

B-9

•
•

*

ft-

APPENDIX C - Greenline Location

Figure 1 — placement of the monitoring frame along the
greenline. Note that frame placement is not necessarily
perpendicular to the placement on the opposite bank due to
differences in greenline length.

n

v i

Stream

Greenline

Figure 2 — place the monitoring frame with the center of the frame
along the greenline.

C-l

APPENDIX C - Greenline Location

Figure 3 — the point bar (A) shows an interrupted greenline with
vegetation growing the bar not connected to the vegetation along
the stream. The greenline runs more-or-less parallel to the flow of
the stream. The areas shown by the letter "B" is an interrupted
greenline as the vegetation exceeds 75 degrees toward
perpendicular to the stream flow. The greenline continues when
the line of vegetation begins toward paralleling the stream. Roads,
trails (C), and tributary streams (D), are not considered part of the
greenline. They may be record as information, but not included in
greenline calculations. These include livestock and wildlife trail.

Greenline

Greenline

Figure 4 — the greenline is on the streambank approximately parallel
to the water flow. Streambanks perpendicular (over 75 degree angle)
to the stream flow is not considered greenline.

C-2

APPENDIX C - Greenline Location

■»

$®M^$i£liS$8^

jgm m

Figure 5 — the diagram shows the location of the greenline in a
situation with a broken bank. The field horsetail (E) is shown on
an area that is an island during above bankfull flows and
therefore the greenline is on the edge of the higher bank
(terrace). The greenline on the left-hand bank is typical of
vegetation at or slightly above the bankfull flow line.

^£^&S^

.1 ■/• ■/• :•• :•> ■/■ ■■■ ■■• •-■• •■■ •■■ ■.% •■•■ •.% ■> •■i •■■•■.• S ■■■•■■■■■•■■• ■■

Figure 6 — greenline A is an example of a shrub Booth's willow
(Sabo) overstory with beaked sedge (Caut) as an understory. The
type name would be Sabo/Caut. Greenline B is an example of the
location of the greenline when there is a shrub overstory and no
vegetation understory, the greenline is at the base of the shrub or
tree.

C-3

APPENDIX C - Greenline Location

mmmmm

Figure 7 — greenline A is an example of a single species,
beaked sedge (Caut). Greenline B is an example of the location
of the greenline when there is a conifer tree overstory with
anchored rock in the streambank. Conifer and anchored rock
are recorded as co-dominant.

C-4

APPENDIX D — Modified Daubenmire Monitoring Frame

Monitoring frames may be constructed of various materials 1/2-inch PVC
schedule 40 plastic pipe or metal. Schedule 40 PVC is rigid and does not
warp as much as the lighter pipe. This material is inexpensive, light, and
easy to use to make the frames. Carefully measure each of the products
before they are glued together as fittings, i.e., tees and elbows, are not
uniform between manufacturers. When handles or other components that
are not glued and will not stay in the fitting, the frame can be modified by
gluing male and female threaded fittings which allow the parts to be threaded
together and still can be taken apart for storage or transportation. Electrical
tape wrapped around the pipe is a good material for marking the alternating
colors. It does not come off the pipe as easily as paint.

Metal frequency plot frames (typically 40 by 40 cm) may be used by
extending the tines to 50 cm in length and marking the four incremental
segments with lines or alternating colors.

S

50 cm

n

i

s.

?

20 cm
20 cm

J

i ..

i
i
i
i
i
i
i

HMI I Co)

i

t

S N1

i

V Si

12.5 cm !

I

:

i

i
1

2

3 A

i

Figure 1 — Multi-indicator monitoring quadrat. Based on field
experience, this is the preferred quadrat configuration. It is light,
easy to carry, and manipulate in shrub type vegetation. Observers
must be careful to extend the lines to complete the quadrat.
Components consist of three 1/2 inch PVC plastic tees, four pieces
of 1/2 inch PVC pipe 19.7 cm (7 % inches) long, one 43 cm (16
15/16 inches) long, one piece of pipe 3.2 cm (1% inches) long, and
one 3 foot piece for a handle. The handle may be a convenient
length. Mark one inch increments on the handle to facilitate
stubble height measurements. Wrapping the long pipe with
electrical tape is a good way to mark the segments. It is easy to
apply and outlasts paint.

D-1

APPENDIX D — Modified Daubenmire Monitoring Frame

Figure 1 — Material list to make a monitoring quadrat from 1/2 inch
Schedule 40 PVC pipe

Item

Number

Length

Inches

Centimeters

14 inch Tee

3

-

-

PVC pipe

4

7.75

19.7

PVC pipe

1

16.9

43

PVC pipe

1

1.25

3.2

PVC pipe (handle)

1

39

100

Figure 2 — Multi-indicator monitoring quadrat. This configuration
more succinctly defines each of the two plots. It is easy to use in
non-shrubby environments. The frame consists of two 20 cm by 50
cm Daubenmire monitoring quadrats set side-by-side. The frame
may be constructed of any suitable material. One half inch
Schedule 40 PVC is an inexpensive material that is quite rugged.

D-2

APPENDIX D — Modified Daubenmire Monitoring Frame

Figure 2 — material list to make a monitoring quadrat from 1/2 inch

Item

Number

Length

Inches

Centimeters

1/2 inch tee

2

-

-

1/2 inch elbow

2

-

-

PVC pipe

3

19.6

49.7

PVC pipe

2

7.6

19.4

PVC pipe

1

1.5

3.8

PVC pipe (handle)

1

39

100

Schedule 40 PVC pipe

1 inch

$c

Figure 3 — Mark the handle in one inch
increments to facilitate measuring stubble
Height.

D-3

I
I }

<

(

APPENDIX E - Data Entry and Analysis

A data entry form has been prepared for use with PDA's using the Excel spreadsheet
format. The form can be downloaded into Excel on the users PC, and then converted
to Pocket Excel in the PDA through synchronization. This file includes user
instructions. Calculations and analyses are limited in this form to avoid time delays
caused by the much reduced processing speed of handheld computers (see Appendix
M).

Using Pocket EXCEL for PDAs & the Data Entry Module

Use Pocket EXCEL to enter data in the field and determine sample size needed.

The Data Entry Module is designed to be used with Pocket EXCEL.

Enter data for one pasture in an allotment, on one File. Save the file as the
pasture or DMA name.

Entering data

Header

The "Header" worksheet records descriptive info and is required.

You can generate a random # in the "Header" worksheet entering the
formula "=RAND()*10," followed by enter.

You should also indicate how many steps you take in a pace, and
length of your step in meters.

Gradient is stream gradient in %. You should also enter the substrate
class using the codes in the "Codes" spreadsheet.

The questions concerning woody plants must be answered to obtain a
serai status rating.

DMA

Copy plant codes from the vegetation worksheets using "copy" and
"paste" function on the PDA.

Data entry cells are non-colored

Codes

This worksheet describes the bank stability and woody regeneration
age classes

Vegetation

E-l

APPENDIX E -- Data Entry and Analysis

Worksheets contain vegetation codes for grasses (including
grass-likes), shrubs, trees, and forbs

Key species are listed in a column on the right side of the DMA
spreadsheet.

Substrate

This worksheet allows entering stream substrate data using the
Pebble Count method as explained in the bulletin and in the field
cards. Data are entered for all 20 cross sections, 1 0 per section
for a total of 200. If more pebbles are desired, for example to
meet sample size needs, add them to the rows indicated.
Measure pebble counts across the stream channel at every other
plot until the desired sample size is achieved.

Comments

Comments may be general or by plot.
Statistics

The "Stats" worksheet describes statistics used to calculate sample size

Using the Data Analysis Module

The "Data_Analysis_Module 2007 V3" is a file that will import all of the raw data
from the "Data_Entry_Module 2007 V3", and calculate metrics useful for data
interpretation. This analysis module will also format the data for export to the MIM
database, and the IIT IM Database, which are both in ACCESS format. Data may
also be copied directly into this module. Thus when users record data on hard copy
sheets, the data are transferred directly to this file rather than the Data Entry Module,
which is used for field entry only.

MACROS: The Macros in this analysis module open your Data Entry file and
extract data for analysis, and examine and correct common mistakes in coding plants
in the DMA worksheet. There is also a macro for enter new plant codes into the
system.

Macro's must be enabled to function. Enable Macros in "Tools", "Macro",
"Security"

Analyzing data prior to 2007: To run the Macro for data entered prior to Version
2007, hold down the "Control" key and select the letter "g". You will be prompted
for a data entry file. Migrate to the file in your system and select it. Data will be
copied into your Data Analysis file.

E-2

APPENDIX E -- Data Entry and Analysis

This Macro will stop after 1 DMA has been imported into the Data Analysis Module.
The "Data Summary" worksheet can then be opened to examine results.

Analyzing Data using the latest version of the Data Entry Module

To run this macro, hold down the control key and select the letter "m" to import and
analyze the data. Data are brought into the module from the Header, DMA, and
Substrate worksheets of the Data Entry Module. Follow the prompts as described
above for data prior to the 2007.

Correcting plant codes in the DMA worksheet

Use Ctrl "r" for execution. This macro searches for commonly-made mistakes in the
coding of plants and corrects them. Not all mistakes are likely to be found, so users
MUST check the data to assure that all plant codes are correct. The drop-down
menus in the plant code fields of the DMA worksheet provide a quick and efficient
means of checking the plant code list. When unsure of the code for a particular plant,
refer to the "Codes" worksheet for a complete list with their scientific and common
names.

Adding plant codes not currently in the DMA worksheet

Use Ctrl "p" for execution. If a plant is encountered in the field and is not included
in the list of plants provided in the "DMA" or the "Codes" worksheets, this macro
will insert it. You must first select a plant code from the plant list that you did not
use. You will be prompted for that code name. You will then be prompted for the
code name you intend to use for the new plant encountered. The system will then
replace the unused plant code with the new plant code, which will now be counted in
the metric calculations.

Each iteration of data import into the Data Analysis Module provides an opportunity
to save the raw data and data summary

A good convention is to save the file as follows: "allotmentDMAname"
(e.g. for the Dry Creek Allotment, Long Creek DMA:
"drycreeklongcreek")

Once the file has been saved, close it, then reopen the Data Analysis Module to
import and analyze additional DMA data.

Always keep the master copy of the Data Analysis Module in a separate folder
Make copies of the Module and place them in each data file folder.

E-3

(

APPENDIX E - Data Entry and Analysis '

♦

Use these copies to run the Macros and analyze the data - never use the master copy. f

Your field-entered vegetation codes must match those in the "Codes" worksheet. If

they don't, you will need to replace the field-entered codes with those in this

worksheet to run the analysis. ,

Additional instructions for use of the Module are contained in the "Instructions" &

worksheet. This includes instructions for using the Export worksheet. Also, there
are instructions in the MIM database for transferring data from the
DataAnalysisModule 2007 V3 directly into the database table and for up-loading
images.

>
Worksheets in the Data Analysis Module are password protected to prevent
inadvertent modification of equations used to calculate the metrics. If the user >

desires to modify a component, first make a copy to assure that the original is not lost
in case of errors, second select 'Tools", "Protection", "Unprotect Sheet" and provide
the password which is: "dma" - in lower case letters. Users are cautioned not to
make substantial changes without making sure that such changes affect the outcomes
of metric calculation. For example, if a plant code is changed in the "Codes"
worksheet, it must also be changed at all locations of occurrence in the "DMA" and
"Summary" worksheets for the metrics to be correctly calculated. If there is any
doubt, contact the developer first: Tim Burton at: tburton@blm.gov.

E-4

APPENDIX F- Riparian Monitoring Data Sheet
Instructions

Plot No. — Enter the plot no. for each plot. Leave blank if additional lines are
needed for entering data. For example, a plot contains two or more species
are encountered in the woody species regeneration, enter the species name
on the next line.

Riparian Vegetation

Dominant — enter the species code for the dominant vegetation. If
any part of the quadrat contains a woody species overstory, enter
that plant code in the first line of the plot. If there is a co-dominant
species enter it on the next line without a plot number. The first
species code of riparian community type may be entered into this
column. The second species code in the riparian plant community
designation may be entered into the Subdominant Vegetation
column.

Subdominant — enter the species code of the species into this
column. If there are two subdominant plant species, enter the code
on the next line without a plot number.

Streambank

Altered — record the number of lines (0 to 5) that intersect
streambank disturbance caused by the hooves of livestock and/or
wildlife. If more than one animal track is intersected along one of
the five lines, only one is recorded.

Stability Class — Record the streambank stability class (cs-
covered/stable, cu-covered/unstable, uu-uncovered/unstable, us-
uncovered stable, fs-false bank, or un-unclassified.

Stubble Height

Key Species — enter the code of the key species.

Average Height — record the average height of the leaves of the key
riparian species nearest the handle and within the plot. When there
are no key species in the quadrat, leave the cell blank.

Woody Species Regeneration

Species — Enter the code for the woody species encountered within

the plot.

Seedling — Record the number of individual woody plants classified
as seedlings. Leave blank if not seedlings are counted.

F-1

APPENDIX F- Riparian Monitoring Data Sheet
Instructions

Young — Record the number of individual woody plants classified as
young. Leave blank if not seedlings are counted.

Mature — Record the number of individual woody plants classified as
mature. Leave blank if not seedlings are counted.

Decadent — Record the number of individual woody plants classified
as decadent (over 50 percent of the plant is dead. Leave blank if
not seedlings are counted.

Dead — Record the number of individual woody plants classified is
dead (no part of the plant is alive). Leave blank if not seedlings are
counted.

Unclassified — Use this column for recording the number of woody
species stems within the plot that is not classified by age. It may be
used for rhizomatous species such as coyote willow (Salix exigua).

Greenline-to-Greenline Width (GGW)

Record the non-vegetated distance (meter or English) at each plot
location. The measurement is from the greenline at the back of the
quadrat across the stream, perpendicular to the water flow direction.
to the greenline. When a vegetated island is encountered, subtract
the distance of vegetated island from the total greenline-to-greenline
distance.

Woody Use

Species — record the code of the woody specie on which use will be
determined

Percent Use — enter the mid point number (none to slight = 5; slight
to moderate = 25; moderate = 50; heavy to severe = 75: and
extreme = 95) of the use class for each transect.

ln-Stream Variables

Thalweg depth - record the maximum water depth under the
greenline-greenline width transect in meters.

Water width - measure and record the width of water (excludes
islands/peninsulas) in meters

Substrate sizes - record substrate sizes in mm for each transect on
the substrate form.

F-2

APPENDIX G - Example Greenlines

Figure 1— vegetation growing within the stream channel is not part of
the greenline. Photo - PIBO, U.S. Forest Service

Figure 2— the greenline follows the (Carex sp.) on each side of the
stream. Water speedwell (Veronica anagallis-aquatica) growing in the
stream is not part of the greenline. Photo - PIBO, U.S. Forest Service

G-1

APPENDIX G - Example Greenlines

Figure 3— monkey flower {Mimulus guttatus) is an annual or short-lived
rhizomatous perennial colonizing species. It is not included as a
qreenline species. Photo - PIBO. U.S. Forest Service

l?&&2

3§*f ;.c

Figure 4— watercress (Rorippa nasturtium-aquatic urn) \s not considered
part of the qreenline. It should be noted in the remarks section.

G-2

APPENDIX G - Example Greenlines

Figure 5— brookgrass (Catabrosia aquatica) is a short-
lived perennial grass that occasionally grows on the
streambank. It grows mostly in the margin of a stream,
is not considered part of the greenline.

Figure 6 — greenline follows the continuous vegetation along the edge of the
water at summer low flow and not vegetation growing in the water or channel.
There is a distinct line between the vegetation on the streambank and the
vegetation in the channel. Photo - PIBO, U.S. Forest Service

G-3

APPENDIX G - Example Greenlines

Figure 7— when willows grow in the channel, the greenline follows the
water's edge or streambanks at summer low flow.

Figure 8— greenline follows the relatively continuous line of vegetation and not
the scatter vegetation on the sand/gravel bar. Photo - PI BO, U.S. Forest Service

G-4

APPENDIX G - Example Greenlines

Figure 9 — the greenline follows the outer streambank at bankfull. It does
not cross a channel to the island. A small channel runs along the island
on the left. Photo - PIBO, U.S. Forest Service

Figure 10— colonizing specie short-awned fox tail (A/opecurus aequalis)
forming a lineal grouping of vegetation with at least 25% foliar cover and is at
least 6 inches (15 cm) wide and 19.6 inches (50 cm) long.

G-5

APPENDIX G - Example Greenlines

Figure 11— In the case of a peninsula, or back-water channel, the
greenline jumps across the slew to the inner bank of the peninsula.

G-6

APPENDIX G - Example Greenlines

Figure 12— the island, even with vegetation is not part of the greenline.

)

Figure 13 — greenline on the left side of the photo is in two segments, the lower
segment near the water's edge and the upper segment along the edge of the
terrace with upland vegetation. The greenline on the right side of the stream is
continuous along the perennial vegetation.

G-7

APPENDIX G - Example Greenlines

Figure 14— For steep, bare banks the greenline is at the top. Vegetation
does not have to be "hydric" to be included as part of the greenline.

,^^^^^!^^^yy^i^|Hyyi

Figure 1 5 — the greenline follows the relatively continuous line of vegetation.
The vegetation near "A" is does not meet the greenline criteria of being at least
50 cm long. Photo - PI BO, U.S. Forest Service

G-8

APPENDIX G - Example Greenlines

Figure 16 — slump blocks "A" are detached and not considered part of the greenline.
The dashed line shows greenline. Photo - PIBO, U.S. Forest Service

Figure 1 7. Slump block re-attached to the bank - evidence by vegetation

G-9

APPENDIX G - Example Greenlines

Figure 18— false bank is an old slump block with vegetative cover. The
slump feature is reattached to the streambank. The greenline follows edged
of the false bank.

Figure 19— vegetation is not well established between the slump block and
the vertical terrace leaving, thus the greenline follows the bank behind it.

G-10

APPENDIX G - Example Greenlines

Figure 20 — when a log jam that crosses the stream is encountered, the greenline
continues over the log jam and is recorded as anchored wood. Photo - PIBO, U.S.
Forest Service

Figure 21 — The patch of vegetation that the quadrant is on does not
meet the 15 cm (6 in) by 50 cm (19.6 in) rule.

G-11

APPENDIX G - Example Greenlines

Figure 22 — the rock UA" is anchored and part of the greenline. Active
erosion exists on the streambank side of rock "B" and is not considered part
of the greenline.

Figure 23 — greenline follows the line of relatively continuous with lineal
arouDinas of Derennial veaetation with 25 percent foliar cover.

G-12

APPENDIX G - Example Greenlines

■ -• "f r^r: -a

Figure 23 — large anchored boulders and bedrock are recorded as rock.
Note the color change on the rocks indicating the bankfull stage. Photo

PIRC. 1 1 <? Fnmct Pontine

Figure 24— the greenline along talus a slope is considered as rock
and is at about the bankfull stream level. Record the data as rock.
Photo ■ PI BO, U.S. Forest Service

G-13

APPENDIX G - Example Greenlines

Hi

Figure 25— water, tributary streams, roads, and livestock trails are not
considered part of the greenlme. Livestock trails must be well defined
by use over years of use such as the trail shown above. Heavy use
during a single season does not create a well-defined trail that leads
away from the stream crossing. Should the quadrat fall on a trail, it is
recorded as UNG" (no greenline).

G-14

APPENDIX G - Example Greenlines

Figure 26— a narrow peninsula on a tight meander bend has no greenline
vegetation. Place the frame with the center bar along the top of the ridge
and record "NG" mo areenline veaetationV Record the non-veaetative

G-15

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<

APPENDIX J - Streambank Alteration

Figure 1— disturbance is considered trampling when a track caused
by a large herbivore exposes at least !4-inch of bare soil.
Streambank shearing is the physical displacement of part of the
streambank downward toward the stream channel.

Figure 2 — the monitoring frame is centered on the greenline and the
number of lines ((0 to 5) that intersect streambank alteration
(trampling or shearing) is counted and recorded. Lines 1, 2, 4, and
5 intersect streambank alteration. Four is recorded.

J -1

APPENDIX J - Streambank Alteration

Well defin
livestock trail

Figure 3— while livestock trails are not considered part of the greenline; they
are considered for streambank alteration. The frame is placed at the point of
the toe on a line that joins the greenline on either side of the trail. The
example above shows the frame on a livestock trail that has been used
during the current grazing season since all five lines intersect streambank
alteration, five is recorded.

Figure 4— example A is heavily trampled and all five lines intersect
streambank alteration. B shows no evidence of current years trampling that
displaces soil at least Vz inch deep. A zero is recorded.

J -2

APPENDIX J - Streambank Alteration

Figure 5— trampling on the terrace is not recorded as streambank
alteration, only alteration occurring on the steep face of the bank.
The lines are projected for the greenline down the bank, within the
quadrat, to the water line. In the example above, line one, nearest
the handle, does not intersect alteration. Line two does, lines 3 and
4, do not, and line 5 intersects a shear along the face. A total of two
is recorded.

J -3

APPENDIX J - Streambank Alteration

i ■ B5

??y' ; '

}....^..*^,c-^,

IBH!9BHBhDhHBBi

•

\ - ■ -

FN;

Figure 6 — no evident streambank alteration intersects lines
any of the lines within the quadrant. Zero is recorded.

Figure 7— lines 2 and 4 intersect streambank alteration caused by
livestock. Two is recorded.

J -4

APPENDIX J - Streambank Alteration

Figure 8 — current season streambank alteration is difficult to
distinguish from previous season use. Streambank alteration
measurements should be made while livestock are still in the pasture
or within two weeks of leaving. Streambank alteration should not be
conducted on a site such as this when the alteration is difficult to
distinguish from previous season grazing.

J -5

APPENDIX K-Streambank Stability

Bfifinitiflfla

Base Flow: The typical low flow water level in a stream late in the season is usually
in the late summer and fall after the spring snowmelt.

Covered Streambank: Perennial or sod-forming vegetation covers at least 50
percent of the height streambank (the vegetation line is usually at least 20 cm (6 in.)
wide and 50 cm (20 in.), cobbles, six inches or larger, anchored large woody debris
(LWD) with a diameter of four inches or greater, or a combination of the vegetation,
rock, and/or LWD is at least 50 percent.

Crack: A visible fracture that has not separated two portions of a streambank.
Cracks indicate a high risk of breakdown .

Depositional Bank: A streambank associated with sand, silt, clay, or gravel
deposited by the stream.

False Bank: Stream banks have slumped in the past but have been stabilized by
relatively shallow-rooted vegetation. These banks are usually lower than the terrace.
False banks vegetated with deep-rooted riparian vegetation may be considered stable
and should be counted separately and added to the stable category.

Floodplain Line: The upper limit of the streambank. The floodplain line is the level
at which water first spills onto the lowest terrace or floodplain.

Fracture: A crack is visibly obvious on the bank indicating that the block of bank is
about to slump or move into the stream.

Scour Bank: The streambank subject to the erosive energy of the stream,
depositional features are absent.

Scour Line: The lower elevational limit of a streambank. The scour line is the
elevation of the ceiling of undercut banks along streambanks. On depositional banks,
the scour line is the lower limit of sod-forming or perennial vegetation. On small
streams it is generally the base flow.

Slough (Sluff): Soil breaking or crumbling falling away from a bank (see
Illustrations 1 and 2).

Slumping Bank: A streambank that has obviously slipped down. Cracks may or
may not be obvious, but the slump feature is obvious.

Streambank: Morphological features of the stream channel created by the erosion
and deposition forces of stream flow which control the lateral movement of water
(Platts et al 1987). They are that part of a channel between the edge of the lsC terrace
and the scour line. Streambanks are the steeper-sloped sides of the stream channel
and are most susceptible to erosion during high flow events (Platts et al 1987).
Streambanks form above the streambed where vegetation, roots, rocks, and other
obstructions cause resistance to the flow energy (Rosgen 1 996). Stability along the

K- 1

APPENDIX K-Streambank Stability

edge of the I terrace/ flood plain and down to the SCOUT line are the most vulnerable
to erosion by water seouring because bankfull levels oeeur almost every year
(I^eopold 1994). Streambanks are the area between the edge of the lsl
terrace/tloodplain and the seour line.

Terrace: A relative tlat area adjacent to a stream or lake with an abrupt steeper face
adjoining the edge of the stream.

I Terrace: The first relatively flat area adjacent to and above scour line or at
the edge of the water. It may be an active floodplain or an area too high for the
water to reach under the current climate and channel conditions (see Figures 1
and 2).

2nd Terrace: The next elevated relatively flat area above the I st terrace, with a
distinctly steeper slope facing the stream (see Figure 2).

K-2

APPENDIX K-Streambank Stability

STREAMBANK STABILITY CLASSIFICATION KEY

I. Streambank Absent (side channel, tributary, slew. road, etc.) UN

II. Streambank present or should be present

A. Streambank depositional

1. Streambank not present due to excessive deposition US

2. Streambank is present (deposition not excessive)

a. Bank Covered CS

b. Bank NOT Covered (Bar) UU

B. Streambank erosional or a scour bank

1 . Streambank not fractured or the streambank is fractured with the
slump block no longer attached to the streambank. and is either
lying adjacent to the breakage or is no longer present (see Appendix
B)

a. No crack is visible from the scour line up to a point 1 5
cm behind the top of the streambank

(1) Bank covered

(a) No evidence of disturbance CS

(b) Evidence of disturbance (e.g., erosion,
slumping, bank shearing) CU

(2) Bank NOT covered

(a) Bank Angle within 10 degrees (22%) of

vertical or slough actively entering stream UU

(b) Bank angle NOT within 10 degrees (22 %) of
vertical or slough is not actively entering

stream US

b. A crack or fracture feature is visible within 15 cm (6
inches) of the top of the streambank- slump block is not
attached to the bank

(1) Bank is Covered CU

(2) Bank is NOT Covered UU

2. Streambank is fractured with the slump block feature still attached

a. The bottom of the slump block feature is below (elevationally)
the scour line (view only the fracture feature behind the slump
block)

(1) Bank NOT covered

(a) Bank angle is within 1 0 degrees (22 %) of
vertical or slough actively entering stream UU

(b) Bank angle is NOT within 1 0 degrees (22 %)
of vertical or slough is not actively entering

the stream US

(2) Bank covered CS

b. The bottom of the fracture feature behind the slump
block is above (elevationally) the scour line (view the
bank as a slump block and the fracture feature as a
vertical, exposed bank)

(1) Bank or fracture feature NOT covered UU

(2) Bank or fracture feature covered

(a) Fracture feature not covered CU

(b) Fracture feature covered and reconnected FB

K-3

APPENDIX K-Streambank Stability

Illustration I

[ luu^lain

II.A2.H. CS

Illustration 3

IIB2a(la) II

Illustration 5

IIB2b(2b) KB

Illustration 2

II.A.I IIS

Illustration 4

I IB. 21). (I) (a) Cli

Illustration 6

IIBIb(l) (I

Adapted from Kershner et al 2004

K-4

APPENDIX K-Streambank Stability

Illustration

MB. 1a(2Xa) UU

Illustration 9

2a (1Kb) CU

Illustration 1 1

IIB 2a(2)(a) UU

Illustration 10

\&cour Line

Base Flow

IIB2a(2)(b) US

Illustration 13

Base Flow

!IB2<1Xa)CS

IIB2a(1)(a)CS

Scour Line

IIB2a(1Xa)CS

Adapted from Kershner et al

K-5

APPENDIX K-Streambank Stability

Figure 1 — the 1st terrace is the first relatively flat area above
the scour line or edge of the water. An abrupt steep face
from the edge of the terrace to the scour line is a
characteristic of a terrace. Slough from the terrace wall has
direct access to the stream.

Figure 2 — a new floodplain has developed creating the 1st
terrace at a lower elevation. Slough from the 2nd terrace does
not go directly into the stream as it is filter by the 1st terrace.
K-6

APPENDIX K-Streambank Stability

Figure 3— Erosional features help determine the stability of a streambank.
Breakdown or slump blocks that are detached from the streambank are not
considered part of the streambanks. Slumps must be obvious sliding down
of a part of the streambank. Fractures are obvious breaking of a portion of
the streambank (see Illustrations 3, 4, 6 and 7 above).

Figure 4 — The photo above shows a fracture and a large slump that is still
attached to the streambank. Vegetation cover is at least 50 percent canopy
cover and is classified as covered/unstable (CU). (see Illustration 4)

K-7

APPENDIX K-Streambank Stability

Figure 6— the stream in this photo is flowing at the scour line. Slumps "A"
are still attached the bank above the scour line and would be classified as
covered/unstable (CU) (See Illustration 4). "B" has no vegetation along the
streambank and is uncovered/unstable (UU) (See Illustration 4).

Figure 6 — the dotted line represents the scour line. "A" shows a monitoring
frame placed on the greenline, just above the scour line. The streambank is
covered/stable (CS). The frame at "B" is located on the greenline. Since it
is not usually practical to pace along or near the scour line, the length of the
frame is projected to the scour line and the streambank is classified. At "B"
the streambank is uncovered/unstable (UU). Photo- PIBO, U.S. Forest
Service.

K-8

APPENDIX K-Streambank Stability

Figure 7 — slump banks "A" are still attached to the streambank above the
scour line and is classified as cover/unstable (CU). The dashed line is the
greenline. Photo- PI BO, U.S. Forest Service.

Figure ft— Slump blocks and slumping banks with the blocks and attacked
bank above the scour line are covered/unstable (CU).

K-9

APPENDIX K-Streambank Stability

f

1

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Figure 9— false banks (FB) are slump features that are reattached and with
deep-rooted vegetative cover and is stable.

Figure 10— the streambank on one side of the stream is uncovered/unstable
(UU) and the other side is covered/stable (CS).

K- 10

APPENDIX K-Streambank Stability

L.5V« , V.AV : ' ^jlWJi

Figure 11 — The scour line is near the current water level. The streambank
classification reflects the bank from scour line to first terrace. The bar is
covered, therefore stable.

mm H\

Streambank

Uncovered/

Unstable

Scour I Jne

Figure 12— The streambank has an obvious scour line. The streambank is
above the scour line to the first terrace and is uncovered/unstable (UU).

K- ll

APPENDIX K-Streambank Stability

^VB^HHIHH

<J ffahfefllS)

'

1

9 ?*'9$

Figure 13 — the streambank is not covered with vegetation, rock, or wood,
has a bank angle of more than 10 degrees from vertical with no terrace to
capture the sediment and thus the sediment enters directly into the stream
making it uncovered/unstable (UU). Banks are always classified unstable
where slough enters the stream.

K- 12

APPENDIX L - Greenl ine-to-Greenl ine Width

Greenline-to-Greenline
Width (GGW)

<

Greenline

Greenline

Broken Bank

Figure 1 — the greenline-to-greenline width is the horizontal distance
between the greenlines on each side of the stream measured perpendicular
to the flow of the stream. It is the non-vegetated stream channel. When
vegetated (at least 25% vegetation cover) slump blocks or islands
encountered along the line, the vegetated portion is subtracted from the total
width and only the non-vegetated portion of the width is recorded.

^§$fett Sabo

Greenline

Greenline

Figure 2— greenline-to-greenline width (GGW) is measured perpendicular to
the water flow and from the rooted base on the greenline to the rooted base
of plants on the greenline on the opposite side of the non-vegetated stream
channel.

L-1

APPENDIX L -Greenline-to-Greenline Width

Figure 3— greenline-to-greenline width (GGW) is measured across the non-
vegetate portion of the stream channel perpendicular to the direction of water
flow. Location V is the length of line "A" minus the length of line "B." Location
"II" GGW is the length of line "C" less the line "D." Location "III" is the length of
linft T "

Figure 4— line "A" is the total length of the greenline-to-greenline width
(GGW). The gravel bar has no vegetation. When the GGW crosses an
island with at least 25 percent cover, the n on- vegetative portion is calculated
(total length of line "B" - line "C") to determine the non-vegetated portion of
the two channels. Photo - PIBO, U.S. Forest Service

L-2

APPENDIX L - Greenline-to-Greenline Width

Figure 5-K3GW is measured at regular intervals from one side of the stream
at each plot location. Lines "A," "B," and "F" are the width of the non-
vegetated stream channel measured perpendicular to the water flow
direction. Line mC shows a non-vegetated portion above the steam. The
GGW is measured between the greenlines. The GGW for line "D" is the total
length of the line minus the distance on the island at ME."

1

'■%

*£; Tf: jB

"

H^S

wtKw^h

Figure 6— the slump block "A" is not attached to the streambank. The GGW
is the total length of "B" less the length of the slump block.

L-3

APPENDIX M - Woody Species Use - Browse

Figure 1 — None to Slight. Browse plants appear to have little or
no use. Less than 10% of the available current year's leader
growth is undisturbed. Mid-point is 5.

Figure 2 — Slight to Light. There is obvious evidence of leader use.
The available leaders appear cropped or browsed in patches and 60
- 89% of the available leader growth of browse plants remains intact.
Mid-point is 25.

M-1

APPENDIX M - Woody Species Use - Browse

Figure 3 — Moderate. Browse plants appear rather uniformly utilized
and 40 - 60% of available annual leader growth of the plants
remains intact. Mid-point is 50.

m-t i

Figure A— Moderate Browse plants appear rather uniformly
utilized and 40 - 60% of available annual leader growth of the
plants remains intact. Mid-point is 50.

M-2

APPENDIX M - Woody Species Use - Browse

~ — ~ —

Figure 5— Heavy to Severe. The use of the browse gives the
appearance of complete search by grazing animals. The preferred
browse plants are hedged and some clumps may be slightly
broken. Only between 10 and 40% of the available leader growth
remains intact. Mid-point is 75.

Figure &— Heavy to Severe. The use of the browse gives the
appearance of complete search by grazing animals. The preferred
browse plants are hedged and some clumps may be slightly broken.
Only between 10 and 40% of the available leader growth remains

M-3

APPENDIX M - Woody Species Use - Browse

Figure 7— Extreme. There are indications of repeated grazing. There is not evidence
of terminal buds. Some patches of second and third years' growth may be grazed.
Hedging is readily apparent and browse plants are frequently broken. Repeated use at
this level will produce a definitely hedged or armored growth form. Ten to 40% of the
more accessible second and third years' growth of browse plants has been utilized. All
browse plants have major portions broken. Mid-point is 95.

Figure 8— Extreme. There are indications of repeated grazing. There is not
evidence of terminal buds. Some patches of second and third years' growth may be
grazed. Hedging is readily apparent and browse plants are frequently broken.
Repeated use at this level will produce a definitely hedged or armored growth form.
Ten to 40% of the more accessible second and third years' growth of browse plants
has been utilized. All browse plants have major portions broken. Mid-point is 95.

M-4

APPENDIX N - Testing Precision and Accuracy
Appendix N- Testing Precision and Accuracy

Precision: Precision denotes the amount of agreement between repeated
measurements by the same observer and/or different observes. It reflects both the
expertise of the observers and the rigor of the procedure. We tested precision by
evaluating repeat samples at the same sites and at the same time. We tested
repeatability among the same observers and between different observers on the same
reaches of stream. Observers were instructed to complete a sample at the site, and
then to repeat sampling at the same site. Because plots are located at random by
pacing, the likelihood of the repeat sample plots being placed at exactly the same
locations on the greenline as samples taken during the initial run is low. Therefore,
spatial variation may represent some of the differences observed between initial and
final samples (spatial variation is described in the section on Accuracy, below). The
following summarizes the ranges of variability observed both among and between
observers.

Indicator

Number
of tests

Number
of

streams
tested

Mean difference &
range of
differences
among the same
observers

Mean difference &
range of
differences
between different
observers

Stubble
Height

35

6

0.6 (0-1.5) inch

0.8 (0-4.5) inch

Bank
alteration

35

6

4.8(0-15)%

8.2(0-44)%

Woody

utilization

(browse)

33

5

6.3(0-40)%

11.1 (0-40)%

Bank
Stability

35

6

6.3(0-19)%

12.4(0-40)%

% Hydric
vegetation

35

6

5.5(0-18)%

9.3 (.5 -31)%

Wetland
rating

35

6

4.9 (0 - 22)

12.1 (1-53)

Greenline-

greenline

width

35

6

.29(0-1.7) meters

.56 (.02 -1.52)
meters

Accuracy: Accuracy is the amount of agreement between the estimate from
sampling, and the true mean value, usually reflecting the number of samples collected
and spatial variability at the site. Sample size estimates are used to evaluate
accuracy. We estimated the number of samples needed using a standard power
analysis to predict the mean based on the standard normal coefficient, the measured
deviation from the mean, and a desired confidence interval width, as follows:

n=(Zac)2(s)2/(B)2

N-l

APPENDIX N - Testing Precision and Accuracy

Where:

n =
Zae =

s
B =

The sample size needed to aeeurately predict the mean.
The standard normal coefficient
The standard deviation.

The desired confidence level expressed statistically as half of the maximum
acceptable confidence interval width. This needs to be specified in
absolute terms rather than as a percentage. For example, if the desired
confidence interval width is to be within 30% of the sample mean and
expected mean = 1 0, then B = (0.30 x 1 0) - 3.0.

The standard deviation and the confidence level representing a percentage of the
mean value can be calculated from data as it is being collected in the field.
Consequently, we have added this equation to the Data Entry Module, in EXCEL, so
that users can input data and assess sample size needed as it is being collected in the
field. The module contains a cell in the Header spreadsheet that allows users to
modify the confidence level as they evaluate desired sample sizes from their data.

Observed n values from test data: Using the observed standard deviations from test
data, the following describes the average sample size needed to predict the mean.

Sample size needed to predict the mean with 95% confidence (values in parenthesis
are the numbers of plots from which the standard deviation was calculated)

SITE

Bank
Alteration

Bank
Stability

Stubble
Height

Greenline-

Greenline

Width

Woody
Species
Utilization

Marks Creek

64
(328)

78
(135)

92
(315)

102
(333)

38
(100)

Long Tom

79
(268)

45
(90)

51
(156)

73
(269)

32
(297)

Shoshone Cr

80
(326)

57
(125)

51
(129)

64

(323)

76
(146)

NF Humboldt

61

(355)

55
(86)

77
(206)

64
(361)

36
(80)

Big Elk Cr

76
(228)

54
(144)

31
(56)

24
(228)

137
(136)

Dixie Cr

9
(321)

73
(145)

25
(135)

85
(200)

53
(120)

Average
(range)

62
(9-80)

60

(45-78)

55
(25-92)

69

(24-102)

62
(32-137)

These analyses suggest that in most cases, a sample size of 80 adequately predicts
mean values for the quantitative variables, for the kinds of spatial variability
observed at the test streams.

N-2

APPENDIX O - Equipment List

The following equipment is needed to use the monitoring
protocol.

• Monitoring frame described in Appendix D.

• Waders or wading shoes are useful. It is easier to
monitoring many streams by pacing in the stream rather
than on the streambank.

• Laser rangefinder, measuring rod, or tape measure. The
laser range finder is expensive ($2,400.00 for one with a
precision of ±0.03 meters and about $800.00 for one
with a precision of ±0.3 meters), but is about 50 percent
more efficient.

• Measuring rod or tape measure (metric preferred)

• Handheld computer (PDA) with Excel spreadsheet.
Extra batteries or extended life batteries are required.

• Riparian monitoring data sheets (in lieu of PDA).

• Global Positioning Position (GPS) receiver with extra
batteries.

• Appropriate plant identification keys for riparian plants.

• Gravelometer for substrate measurement, or ruler to
measure median diameter of substrate particles.

O-l

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