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292 records · Page 17Linked to original sources
USGS2013

Hydrology and water quality of Shell Lake, Washburn County, Wisconsin, with special emphasis on the effects of diversion and changes in water level on the water quality of a shallow terminal lake

Shell Lake is a relatively shallow terminal lake (tributaries but no outlets) in northwestern Wisconsin that has experienced approximately 10 feet (ft) of water-level fluctuation over more than 70 years of record and extensive flooding of nearshore areas starting in the early 2000s. The City of Shell Lake (City) received a permit from the Wisconsin Department of Natural Resources in 2002 to divert water from the lake to a nearby river in order to lower water levels and reduce flooding. Previous studies suggested that water-level fluctuations were driven by long-term cycles in precipitation, evaporation, and runoff, although questions about the lake’s connection with the groundwater system remained. The permit required that the City evaluate assumptions about lake/groundwater interactions made in previous studies and evaluate the effects of the water diversion on water levels in Shell Lake and other nearby lakes. Therefore, a cooperative study between the City and U.S. Geological Survey (USGS) was initiated to improve the understanding of the hydrogeology of the area and evaluate potential effects of the diversion on water levels in Shell Lake, the surrounding groundwater system, and nearby lakes. Concerns over deteriorating water quality in the lake, possibly associated with changes in water level, prompted an additional cooperative project between the City and the USGS to evaluate efeffects of changes in nutrient loading associated with changes in water levels on the water quality of Shell Lake. Numerical models were used to evaluate how the hydrology and water quality responded to diversion of water from the lake and historical changes in the watershed. The groundwater-flow model MODFLOW was used to simulate groundwater movement in the area around Shell Lake, including groundwater/surface-water interactions. Simulated results from the MODFLOW model indicate that groundwater flows generally northward in the area around Shell Lake, with flow locally converging toward the lake. Total groundwater inflow to Shell Lake is small (approximately 5 percent of the water budget) compared with water entering the lake from precipitation (83 percent) and surface-water runoff (13 percent). The MODFLOW model also was used to simulate average annual hydrologic conditions from 1949 to 2009, including effects of the removal of 3 billion gallons of water during 2003–5. The maximum decline in simulated average annual water levels for Shell Lake due to the diversion alone was 3.3 ft at the end of the diversion process in 2005. Model simulations also indicate that although water level continued to decline through 2009 in response to local weather patterns (local drought), the effects of the diversion decreased after the diversion ceased; that is, after 4 years of recovery (2006–9), drawdown attributable to the diversion alone decreased by about 0.6 ft because of increased groundwater inflow and decreased lake-water outflow to groundwater caused by the artificially lower lake level. A delayed response in drawdown of less than 0.5 ft was transmitted through the groundwater-flow system to upgradient lakes. This relatively small effect on upgradient lakes is attributed in part to extensive layers of shallow clay that limit lake/groundwater interaction in the area. Data collected in the lake indicated that Shell Lake is polymictic (characterized by frequent deep mixing) and that its productivity is limited by the amount of phosphorus in the lake. The lake was typically classified as oligotrophic-mesotrophic in June, mesotrophic in July, and mesotrophic-eutrophic in August. In polymictic lakes like Shell Lake, phosphorus released from the sediments is not trapped near the bottom of the lake but is intermittently released to the shallow water, resulting in deteriorating water quality as summer progresses. Because the productivity of Shell Lake is limited by phosphorus, the sources of phosphorus to the lake were quantified, and the response in water quality to changes in phosphorus inputs were evaluated by means of eutrophication models. During 2009, the total input of phosphorus to Shell Lake was 1,730 pounds (lb), of which 1,320 lb came from external sources (76 percent) and 414 lb came from internal loading from sediments in the lake (24 percent). The largest external source was from surface-water runoff, which delivered about 52 percent of the total phosphorus load compared with about 13 percent of the water input. The second largest source was from precipitation (wetfall and dryfall), which delivered 19 percent of the load compared to about 83 percent of the water input. Contributions from septic systems and groundwater accounted for about 3 and 2 percent, respectively. Increased runoff raises water levels in the lake but does not necessarily increase phosphorus loading because phosphorus concentrations in the tributaries decline during increased flow, possibly because of shorter retention times in upstream wetlands. Phosphorus loading to the lake in 2009 represented what occurred after a series of dry years; therefore, this information was combined with data from 2011, a wet year, to estimate phosphorus loading during a range of hydrologic conditions by estimating loading from each component of the phosphorus budget for each year from 1949 to 2011. Comparisons of historical water-quality records with historical water levels and applications of a hydrodynamic model (Dynamic Lake Model, DLM) and empirical eutrophication models were used to understand how changes in water level and the coinciding changes in phosphorus loading affect the water quality of Shell Lake. DLM simulations indicate that large changes in water level (approximately 10 ft) affect the persistence of stratification in the lake. During periods with low water levels, the lake is a well-mixed, polymictic system, with water quality degrading slightly as summer progresses. During periods with high water levels, the lake is more stratified, and phosphorus from internal loading is trapped in the hypolimnion and released later in summer, which results in more extreme seasonality in water quality and better clarity in early summer. Results of eutrophication model simulations using a range in external phosphorus inputs illustrate how water quality in Shell Lake (phosphorus and chlorophyll a concentrations and Secchi depths) responds to changes in external phosphorus loading. Results indicate that a 50-percent reduction in external loading from that measured in 2009 would be required to change phosphorus concentrations from 0.018 milligram per liter (mg/L) (measured in 2009) to 0.012 mg/L (estimated for the mid-1800s from analysis of diatoms in sediment cores). Such reductions in phosphorus loading cannot be accomplished by targeting septic systems or internal loading alone because septic systems contribute only about 3 percent of the phosphorus input to the lake, and internal loading from the sediments of Shell Lake contributes only about 25 percent of phosphorus input. Complete elimination of phosphorus from septic systems and internal loading would decrease the phosphorus concentrations in the lake by 0.003–0.004 mg/L. Therefore, reducing phosphorus concentration in the lake more than by 0.004 mg/L requires decreasing phosphorus loading from surface-water contributions, primarily runoff to the lake. Reconstructed changes in water quality from 1860 to 2010, based on changes in the diatom communities archived in the sediments and eutrophication model simulations, suggest that anthropogenic changes in the watershed (sawmill construction in 1881; the establishment of the village of Shell Lake; and land-use changes in the 1920s, including increased agriculture) had a much larger effect on water quality than the natural changes associated with fluctuations in water level. Although the effects of natural changes in water level on water quality appear to be small, changes in water level do have a modest effect on water quality, primarily manifested as small improvements during higher water levels. Fluctuations in water level, however, have a larger effect on the seasonality of water-quality patterns, with better water quality, especially increased Secchi depths, in early summer during years with high water levels.

Wisconsin↗
USGS2016

Hydrological conditions and evaluation of sustainable groundwater use in the Sierra Vista Subwatershed, Upper San Pedro Basin, southeastern Arizona

This study assessed progress toward achieving sustainable groundwater use in the Sierra Vista Subwatershed of the Upper San Pedro Basin, Arizona, through evaluation of 14 indicators of sustainable use. Sustainable use of groundwater in the Sierra Vista Subwatershed requires, at a minimum, a stable rate of groundwater discharge to, and thus base flow in, the San Pedro River. Many of the 14 indicators are therefore related to long-term or short-term effects on base flow and provide us with a means to evaluate groundwater discharge to and base flow in the San Pedro River. The indicators were based primarily on 10 to 20 years of data monitoring in the subwatershed, ending in 2012, and included subwatershedwide indicators, riparian-system indicators, San Pedro River indicators, and springs indicators. Groundwater management actions including voluntary retirement of irrigation pumping in the subwatershed resulted in about a 5,100 acre-feet (acre-ft) reduction in net human use from 2002 to 2012. Subwatershed population increased more than 10,000 during the same period. Most of the reduction occurred during 2002–07 and included reductions in groundwater pumping and increases in managed recharge; net human use varied annually by a few hundred acre-ft during 2007–12. The groundwater budget for 2012 showed a deficit of about 5,000 acre-ft, although the total water-budget uncertainty was about 5,500 acre-ft. In the vicinity of the U.S. Army’s Fort Huachuca, regional-aquifer water levels were in steady decline beginning in at least the mid-1990s (in older wells since at least the early-1970s), as the cone of depression centered on the Sierra Vista and Fort Huachuca pumping centers continued to deepen. This was evident in the individual water levels on Fort Huachuca, as well as from the horizontal hydraulic gradients that extend from the pumping centers toward the San Pedro and Babocomari Rivers. Basin water levels in wells southeast of Sierra Vista, away from the river, were also experiencing declines, while some water levels closer to the river were rising. Near-stream vertical gradients along the San Pedro River showed no clear increasing or decreasing trends that would indicate a shift in the direction of subsurface flow between the riverbed and the alluvial aquifer, or a trend in the magnitude of groundwater/surface-water exchange. Annual streamflow permanence data showed no clear change in streamflow permanence trends in any of the river reaches, other than those related to precipitation trends. Similarly, the single-day, dry-season, wet-dry streamflow analysis of all subwatershed river reaches indicated no change in condition over the past 14 years, with the exception of the Hereford reach, which has seen a statistically significant increase in wetted length. Dry-season, alluvial-aquifer water levels in the Hereford reach also showed a statistically significant increase. These improvements are attributed to the end of irrigation pumping in the area. Although data indicate that the length of the Fairbank North wetted reach may be in decline, it is not yet statistically significant. Stable-isotope data indicated reduced groundwater discharge to the Babocomari River in the vicinity of the Babocomari River near Tombstone gaging station and to the San Pedro River near the San Pedro River at Palominas gaging station and near the Lewis Springs DCP stage recorder. The Babocomari River near Tombstone gaging station is downgradient of the major pumping centers. The change in isotopic signature at the Lewis Springs stage recorder could have been the result of alterations in groundwater/surface-water interactions there caused by beaver damming of the river. Base flow in the San Pedro River declined over the periods of record at the three San Pedro River gaging stations in the subwatershed (Palominas, Charleston, and Tombstone), as well as at the Babocomari River near Tombstone gaging station. Precipitation declined slightly from the 1990s to the 2000s, although there is no statistically significant trend in subwatershed precipitation from 1991 to 2012. The occurrence of large winter discharge events appeared to decline and that of large summer discharge events appeared to increase over this same period. Data for physical parameters, general chemistry, nutrient species, select trace elements, and suspended sediment were collected at San Pedro River at Charleston stream-gaging station. These data were summarized over time and analyzed in relation to discharge and season as a means to assess trends over the period of analysis. Federal and State of Arizona drinking-water and human-contact standards were all met and few exceedances occurred for the ecological thresholds investigated. Several constituents showed a significant trend over the period of analysis, but only concentration and flux data for total phosphate, orthophosphate, total nitrogen, suspended sediment, and sulfate were suitable to be used in a weighted regression analysis that statistically accounted for time, discharge, and season. Sulfate concentrations and flux showed a significant downward trend over the period of analysis, whereas total phosphorus and ortho-phosphate showed a relatively small magnitude upward trend relative to standards. Suspended sediment concentrations and flux both showed a significant downward trend in the 1980s, an effect attributed to reduction of cattle in the subwatershed at about this time, and (or) increased cottonwood ( Populus fremontii ) and willow ( Salix goodingii ) recruitment, and (or) the curtailment of sand and gravel mining adjacent to the San Pedro River with the designation of the San Pedro Riparian National Conservation Area in 1988. A spike in sediment flux in 2006 may be attributable to the more than 100 debris flows in the Huachuca Mountains during the summer monsoon of that year. Spring discharge along the San Pedro River generally increased at three sites proximate to the Sierra Vista treated effluent recharge facility and varied somewhat with climate at two other sites. Median annual discharge at the recharge facility peaked in 2006, and at Murray Springs and Horsethief Spring, downgradient of the recharge facility, in 2009. Sampling for trace organic compounds in flow from springs was carried out using both discrete sampling and passive sampling methods. Spring samples thus collected showed the presence of trace-organic compounds. Lewis Springs (background site) had the least number of detections, whereas Murray Springs, located directly downgradient of the City of Sierra Vista’s treated effluent recharge facility, had the greatest number of detections of all the springs. Discrete samples from the recharge facility had more than twice the detections found in discrete samples from Murray Spring and at much higher concentrations. Few similar trace-organic compounds were detected at both the springs and the treated effluent recharge facility, and the number of detections did not increase during the collection period. Limitations of the study prevented the determination of trace-organic concentration in passive samplers and also prevented linking trace organic compounds detected at the treated effluent recharge facility with compounds detected from the springs. In particular, trace organic compounds could also derive from other sources such as septic systems. Looking at the subwatershed as a whole, base flow was in decline along the entire river reach, but determination of the specific cause of the decline was beyond the scope of this report. Conditions in the area from the municipal pumping center of Sierra Vista and Fort Huachuca northeast to the river (from about the Charleston to Tombstone gaging stations) were more commonly in decline than in regions further south. Both long-term indicators, such as regional aquifer groundwater levels and horizontal gradients, and the isotope analysis indicated that groundwater discharge to the river and thus base flow may continue to decline in that area. South of Charleston, indicators were more mixed. Some indicators in the Hereford reach suggest groundwater discharge to the San Pedro River may be increasing there, whereas some indicators in the Palominas reach suggest groundwater discharge to the river there may be declining.

Arizona↗
USGS2013

Native Prairie Adaptive Management: a multi region adaptive approach to invasive plant management on Fish and Wildlife Service owned native prairies

Much of the native prairie managed by the U.S. Fish and Wildlife Service (FWS) in the Prairie Pothole Region (PPR) of the northern Great Plains is extensively invaded by the introduced cool-season grasses, smooth brome ( Bromus inermis ) and Kentucky bluegrass ( Poa pratensis ). Management to suppress these invasive plants has had poor to inconsistent success. The central challenge to managers is selecting appropriate management actions in the face of biological and environmental uncertainties. In partnership with the FWS, the U.S. Geological Survey (USGS) developed an adaptive decision support framework to assist managers in selecting management actions under uncertainty and maximizing learning from management outcomes. This joint partnership is known as the Native Prairie Adaptive Management (NPAM) initiative. The NPAM decision framework is built around practical constraints faced by FWS refuge managers and includes identification of the management objective and strategies, analysis of uncertainty and construction of competing decision models, monitoring, and mechanisms for model feedback and decision selection. Nineteen FWS field stations, spanning four states of the PPR, have participated in the initiative. These FWS cooperators share a common management objective, available management strategies, and biological uncertainties. Though the scope is broad, the initiative interfaces with individual land managers who provide site-specific information and receive updated decision guidance that incorporates understanding gained from the collective experience of all cooperators. We describe the technical components of this approach, how the components integrate and inform each other, how data feedback from individual cooperators serves to reduce uncertainty across the whole region, and how a successful adaptive management project is coordinated and maintained on a large scale. During an initial scoping workshop, FWS cooperators developed a consensus management objective: increase the composition of native grasses and forbs on native sod while minimizing cost. Cooperators agreed that decision guidance should be provided annually and should account for local, real-time vegetation conditions observed on the ground. Over the course of development, two prototypes of the decision framework were considered. The final framework recognized four alternative actions that managers could take in any given year: (1) Graze—targeted use of grazing ungulates to achieve defoliation, (2) Burn—application of prescribed fire as the single form of defoliation, (3) Burn/Graze—a combination treatment, and (4) Rest—no action. The study area included northern mixed-grass and tallgrass prairie. Native vegetation in mixed–grass prairie has a strong cool-season component and thus the dominant native species have a phenology similar to that of smooth brome and Kentucky bluegrass, making management of those species challenging. In contrast, tallgrass prairie has a strong warm-season native component, leading to an existence of cool-season windows, periods of time in the fall and spring when cool‐season invasive grass species are actively growing and vulnerable to damage via select management actions, but warm‐season grass species are not active and are thus less susceptible to damage via the same actions. This dichotomy between prairie types necessitated the development of separate but parallel decision support systems for mixed-grass and tallgrass biomes. Management units are parcels of native prairie that receive a single management treatment at any one time over their entire extent. At any particular time, the vegetation state of each management unit is characterized by the amount of cover of native grasses and forbs and the type of invasive grass that is dominant. In addition, each unit has a defoliation state which reflects the number of years since the last defoliation event and an index to how intensively the unit was managed during the previous 7 years. State-transition models are used to predict the state of a management unit in year t+1 from its state in year t and a prescribed management action that was applied between the two monitoring events. Alternative models are built around key uncertainties that make choice of a management action difficult. Three uncertainties revolve around whether the effect of management actions depends on (1) type of dominant invader, (2) past defoliation history, and (3) level of invasion. Two additional uncertainties are considered when choosing a management action for tallgrass units: (4) the effectiveness of grazing within the cool-season window as a surrogate for burning when smooth brome is the dominant invader, and (5) the differential effect of active management outside the window as compared to rest. Because data on the probability of transitioning from one state to another under the various models were lacking, expert opinion and elicitation were used to parameterize the models. In addition, cooperators participated in elicitation exercises to extract their beliefs regarding the value of having native prairie compared to the cost of achieving it. Quantifying the subjective expression of utility in this way allowed for mathematical representation of the management objective into an objective function. By maximizing the objective function, cumulative utility is maximized, leading to the identification of a sequence of decisions that will achieve the management objective. The NPAM system adopted a vegetation monitoring protocol that was rapid, inexpensive, and familiar to many of the cooperators. The monitoring protocol served three purposes: (1) determining current vegetation and defoliation states of each unit, (2) evaluating progress toward the management objective, and (3) assessing predictive performance of the alternative models. The management year runs from September 1 to August 31. Management can be applied anytime during that period and monitoring takes places from late June to mid-August. Cooperators enter vegetation data and management information into a centralized database by August 25 of each year. Given the current state of the system (vegetation and defoliation states) and the current understanding of the system (or the belief state), identifying the current best management decision is a matter of looking up the combination (that is, system state and belief state) in the appropriate (mixed-grass or tallgrass) optimal decision table. Given complete uncertainty at the outset of decision-making, initial assignment of equal belief weights to each model was believed reasonable. The decisions in the optimal decision table that correspond to the current belief state constitute the current optimal decision policy. By August 31 of each year, individual cooperators are provided with a recommended management action for each of their management units for the upcoming management year. Upon receiving the management recommendations for their units, managers consider the recommendation, along with other relevant information, and at some point during the year one of the management alternatives is carried out. This iterative cycle of making and implementing a management decision, predicting the response, monitoring the outcome, comparing predicted and observed outcomes, updating model weights, and recommending a management action for the next cycle is expected to result in an accumulation of weight on a representative model of system dynamics, thereby increasing understanding needed to effectively manage native prairies. The NPAM system is now entering its second full year of complete operation, and represents one of only a few fully implemented applications of adaptive management within the U.S. Fish and Wildlife Service. NPAM is truly unique in that it originated from the ground up as a result of the leadership and steadfastness of several refuge biologists and managers confronted with a common problem. These biologists recognized that working together across a large landscape presented perhaps the best opportunity for halting and reversing the invasion of native grasslands by non-native cool-season grasses. Importantly, the NPAM system encapsulates the collective thinking and experience of tens if not hundreds of individuals who have battled this vexing problem for much of their careers. The NPAM initiative is rooted in principles of adaptive management, thereby affording the opportunity for grassland managers to pursue management objectives while acquiring information to reduce uncertainty and improve future management. The project introduced a number of technical innovations that will serve as templates for conservation efforts throughout and beyond the U.S. Fish and Wildlife Service. First, NPAM is an on-the-ground implementation of active adaptive management—possibly the first of its kind in conservation management—in which recommended management actions result from a prospective analysis of future learning (Williams, 1996). Second, by the use of dynamic optimization, NPAM demonstrates how decisions can be made that take into account possible future transitions of the system. Third, NPAM demonstrates how models of partial controllability are an effective means of accommodating unpredictable circumstances that cause a manager to follow a different course than was intended. Finally, the database developed for NPAM is an unparalleled system that enables the rapid integration of data from the field for the generation of ‘just-in-time’ management recommendations. In all, NPAM provides an example of how a science-management partnership can be forged to achieve large-scale conservation objectives.

Minnesota;Montana;North Dakota;South Dakota↗
USGS1956

Surficial geology and geomorphology of Potter County, Pennsylvania

Potter County is located in the Appalachian Plateaus of north-central Pennsylvania and contains the headwaters of the Genesee River, the Allegheny River, and the Susquehanna River. Drift of Wisconsin age covers the northeastern part of the county. This study includes a detailed survev of the surficial deposits of the Genesee quadrangle in north-central Potter County and a reconnaissance of the remainder of the county; a soil survey and a botanical survey were carried on concurrently. The region is a deeply dissected plateau having extensive areas of steeply sloping land separated by narrow ridges and valleys; there is very little level land. Near the junction of the three watersheds the uplands rise to altitudes of more than 2,500 feet. The maximum relief in the Susquehanna drainage is more than 1,500 feet; in the Genesee and Allegheny drainage it. is about 800 feet. Valley walls are steep (15° to 30°), and the uplands have gentle slopes (0.5° to 10°). The drainage pattern is trellised. The climate is continental. Temperatures range from about -30° F. to more than 100° F. The average annual precipitation ranges approximately from 34 to 42 inches. Floods may occur at any season of the year. The large volumes of water from rain or melting snow carried by small streams come from springs. There is little precise data on frost in the ground, but it is probable that the ground seldom freezes in forested areas. The soils of Potter County have relatively immature profiles with poorly developed horizons that commonly have many characteristics inherited from their parent materials. At the great soil group level, the zonal soils are divided into Podzol soils and Brown Podzolic soils. Many soils have a high silt content in the upper part of the profile, apparently derived (at least partly) from a mantle of eolian silt. Mos~ of Potter County is covered by second-growth forests consisting of 40- to 60-year-old hardwood stands. The present forests growing on slopes and summits are composed approximately of 25 species of trees. The northern hardwood region includes most of the county, with an oak-forest region near the borders, principally along its southern margin. Potter County is underlain by sandstone, siltstone, shale, conglomerate, and minor amounts of coal and calcareous rock that range in age from Late Devonian to Pennsylvanian. These rocks form broad open folds that strike northeast. South of the border of the Wisconsin drift, and possibly at two localities inside the drift border, are scattered remnants of ancient soils (here called paleosol), that were formed in preWisconsin time-probably during the Sangamon interglacial stage. This paleosol ranges in texture from clay loam to silt loam, ranges in color from yellowish red to red, includes a few percent to more than 25 percent of rock fragments, and apparently contains a small percentage of gibbsite and varying amounts of kaolinite. Known thicknesses range from 1 to 33 feet. Paleosol was developed on diverse kinds of parent material, such as till, stratified drift, colluvium, and residuum, at altitudes ranging from a few hundred to 2,400 feet. The climatic conditions under which the paleosol formed are uncertain; however, these ancient soils may record an episode of subtropical climatic conditions during which lateritic soils were formed. Perhaps these soils are analogous to the Red-Yellow Podzolic soils of southeastern United States. Except for one possible remnant, no pre-Wisconsin drift has been recognized in Potter County. The Wisconsin glacial deposits of Potter County belong to either the Iowan or Tazewell substages and are dominantly till with minor amounts of glaciofluvial deposits. Erratics of igneous or metamorphic rock comprise less than 0.1 percent of the total number of rock fragments. The till is slightly weathered to depths ranging from 3 to about 12 feet. The drift border is indefinite and has been drawn at the southern limit of erratics or well-rounded or striated pebbles and is only locally marked by a terminal moraine or by a distinct change in the surficial deposits. The drift border is relatively straight and crosses the Genesee quadrangle in a northwesterly direction with little regard for the major topographic features, thus suggesting that the Wisconsin ice sheet had a relatively straight and steep front. Over most of the unglaciated part of Potter County, the bedrock is concealed beneath rubble that probably was formed during the Iowan or Tazewell substage, almost contemporaneously with the adjacent drift. In general, the rubble is thickest and most extensive within about 10 miles of the drift border, becoming thinner and less continuous farther away. The apparent parallelism between a belt of thick periglacial deposits and the drift border suggests that the deposits result from climatic factors in operation while the Wisconsin ice sheet was nearby. Ancient soil structures or patterned ground occur at, or near, the surface of both the periglacial deposits and the adjacent drift. These ancient soil structures are so similar to modern forms in arctic or alpine environments that they are considered to be the result of vigorous frost action. Many of the structures are believed to be a result of down-slope movement of debris by solifluction, facilitated by a frozen subsoil as much as 10 feet deep. Perennially frozen ground may have been present, but this is not a prerequisite. The periglacial deposits underlie long smooth slopes that extend from ridge crest to valley bottom. Flood plains are absent near the headwaters of many streams, the valley walls forming a V-shaped profile. While frost action was in progress, forests probably were restricted to flood plains, lower slopes, and scattered upland areas. Large parts of the upland were bare or partly covered by tundra vegetation; elsewhere, there were scattered trees but no dense forest. 1 2 SURFICIAL GEOLOGY AND GEOMORPHOLOGY OF POTTER COUNTY, PENNSYLVANIA Recent alluvium and alluvial fans include sand and sandy loams, 1 to 3 feet thick, that overlie gravel. The alluvium contains organic matter and lenses of finer materials. Thickness ranges from a few to more than 100 feet. Along the principal streams the alluvium probably overlies Pleistocene deposits. Most of the alluvial fans are composed of unstratified rubbly, pebbly, cobbly. or bouldery sandy loams to silty clay loams with local lenses of stratified sand and gravel. The alluvial fans mapped in the Genesee quadrangle probably include both Wisconsin stage and Recent deposits. The summits of the A.ppalachian Plateaus in north-central Pennsylvania have long been recognized as the remnants or traces of one or more peneplains. To test this hypothesis, a restored contour map was prepared to show the configuration of a supposed peneplain on the assumption that the plateau tops are remnants of such an old erosion surface. The restored contours delineate a surface that corresponds roughly to rock structure. In general, the uplands slope parallel to the dip of the bedrock. The major streams, such as the West Branch Susquehanna River, cross the ridges and valleys of the restored surface in such a way that it is difficult to suppose that the restored surface was ever graded to these streams. On the contrary, it is probable that the restored surface never existed and that the plateau tops are structurally controlled surfaces held up by sandstone and conglomerate beds in the Pottsville and Pocono formations. The plateau tops may have been lowered by erosion as much as 200 feet during the Pleistocene-in other words, after the major streams were incised. If this portion of the Appalachian Plateaus was ever reduced to a peneplain, such a hypothetical surface must have lain many hundreds of feet above the uplands of the present day. The only alternative that might involve peneplanation is the improbable hypothesis that the plateau tops are remnants of a slightly deformed peneplain and that the peneplain was folded along the axes of the Appalachian orogeny. This remote possibility is not supported by any known evidence. The geomorphic analysis yields no new data on the origin of the cross-axial drainage. Regardless of whether the plateaus are peneplain remnants or are structurally controlled surfaces, the beginning of the major southeastward-flowing streams long antedates the existing landscape. The geomorphic history of Potter County begins with an assumed long interval of erosion during the Mesozoic and early Cenozoic eras, for which no record remains in this area. The southeast master drainage was established by the latter part of the Tertiary period (perhaps at a much earlier date), probably as the result of the northwestward migration of the Atlanticinterior divide. In late Pliocene(?) time, areas adjacent to parts of the West Branch Susquehanna River-and probably elsewhere-had a moderate relief ranging from 300 to 700 feet. Some segments of the West Branch meandered across a broad valley that lay about 900 feet above the present streams. The landscape probably was covered by deep residual soils, perhaps by saprolite. The early Pleistocene history of Potter County is essentially unknown. No deposits of the Kansan stage are known except for a possible trace of pre-Illinoian drift on the uplands in central Potter County (Ayers Hill quadrangle). Some deposits in central and eastern Pennsylvania may be of Kansan age. It is probable that the assumed Aftonian regolith was removed by mass movements and other processes during the Kansan stage, thus resulting in a lowering of the plateau tops by as much as 10 feet. By the close of the Yarmouth(?) interglacial stage the major streams were incised to essentially their present depths. The climates of the Yarmouth interglacial stage probably produced deep residual soils over the landscape, parts of which may still be preserved in the paleosol remnants of the present day. No Illinoian drift is known in Potter County, but drift assigned to this stage occurs in areas to the northwest and to the southeast. Some valleys, such as Kettle Creek valley, were filled with sand and gravel alluvium to depths of as much as 150 feet above their present flood plains. It is assumed that the Yarmouth residual soils were removed by mass movements and other processes induced by a periglacial climate, thus lowering the plateau tops by as much as 10 feet. During the Sangamon interglacial stage, deep (10-to-20 foot) residual soils or paleosol were developed in Potter County and probably throughout much of Pennsylvania, perhaps as a result of lateritic weathering in a subtropical climate. It is possible that the paleosol was largely removed by mass movements and by running water during late Sangamon time. During either the Iowan or Tazewell substages of the Wisconsin (perhaps the Iowan), the ice sheet advanced into the northeastern part of Potter County. The drift is similar to the Olean drift (local usage). The paleosol was almost completely removed by mass movements and other processes induced· by a periglacial climate, prior to drift deposition. This removal probably resulted in a lowering of the plateau tops by as much as 10 feet since Sangamon time. Nearly contemporaneously with drift deposition, the periglacial deposits were formed by frost heaving, solifluction, and fluvial transport in areas outside the drift border. Soil structures or patterned ground were developed on both the drift and the periglacial deposits. It is probable that the forests in the periglacial area were greatly restricted and that large areas on the uplands were essentially treeless. Little is known about the history of Potter County in postOlean time. Presumably, forests completely covered the county by the onset of the next substage, during which the Binghamton drift of MacClintock and Apfel was deposited. This drift also is found in southern New York State. The formation of the alluvium and alluvial fans probably began in the Tazewell substage and continued during the Recent epoch. Since these deposits were formed there has been very little dissection. There is little, if any, difference between soils developed on periglacial deposits and soils developed on drift. The roots of fallen trees have disturbed the soil horizons, and it is unlikely that the existing soil profiles are more than 500 years old. The forested landscape of Potter County has a distinctive microrelief ranging from a few inches to a few feet of mounds and pits produced by the roots of fallen trees. Most mounds and pits range from 10 to 20 feet in length and from 6 to 15 feet in width. On level land, many mounds are oriented with their long axes trending northward, and in some areas the orientation is random. On slopes, the mounds are oriented with their long axes at right angles to the maximum slope as a result of trees falling downslope. The toppling of trees increases the permeability of surficial deposits and mixes and destroys the soil horizons. The microrelief is a factor in forest development. The toppling of trees on slopes is a significant agent of slope erosion. The process loosens, breaks up, or overturns the upper 2 to 3 feet of the forest soil, and it tends to make the surficial layer more stony and to produce features resembling soil structures.

Pennsylvania↗